540B00012
United States
Environmental Protection
Agency
Office of Emergency and
Remedial Response
Emergency Response Division
Environmental
Response
Team
Sampling for
Hazardous Materials
Environmental Response
Training Program
-------
-------
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 covered, it will have its greatest value as an adjunct to classroom presentations
involving discussions among the students and the instructional staff.
This manual has been developed with a goal of providing 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 manual are welcome.
-------
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 objectives of the course are:
Instruct participants on the basic concepts of an effective sampling strategy.
Present available equipment used to obtain representative samples from solid and liquid
wastestreams.
Compare applications and limitations of various sampling devices.
Develop safe and effective sampling plans for environmental sampling events.
After completing the course, participants will be more familiar with fundamental concepts of
sampling, sample plan development, and sampling equipment.
111
-------
CONTENTS
Section 1
Section 2
Section 3
Section 4
Section 5
Section 6
Section 7
Section 8
Section 9
Section 10
Data Quality Objectives
Sample Plan Development
Quality Assurance Sampling Plan for Emergency Response
Appendix II of Guidance for Data Useability in Risk Assessment
(Part A)
Field Screening
Environmental Photographic Interpretation Center (EPIC)
Sample Analysis
Target Compound List
Priority Pollutant and Superfund Comparison Lists
Sample Collection Requirements
Containerized Material Sampling
Hazard Categorization
Soil Sampling
Surface Water and Sediment Sampling
Groundwater Sampling
Documentation
Section 4 of A Compendium of Superfund Field Operations Methods
NEIC Policies and Procedures
Sample Packaging and Shipping
DOT Regulations
Excerpt from Section 6 of A Compendium of Superfund Field
Operations Methods
-------
Contents (continued)
Section 11 Field Exercise
Section 12
Problem Session: Sample Plan Development Exercise
Appendices
Appendix A - Removal Program: Representative Sampling
Guidance, Volume I: Soil
Appendix B - Compendium ofERT Waste Sampling Procedures
Appendix C - Compendium of ERT Soil Sampling and Surface
Geophysics Procedures
Appendix D - Compendium of ERT Surface Water and Sediment
Sampling Procedures
Appendix E - Compendium of ERT Groundwater Sampling
Procedures
VI
-------
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)
FID flame ionization detector
FIPS federal information processing standards
FIT field investigation team
FS feasibility study
FSP field sampling plan
FTS federal telephone system
vn
-------
Acronyms and Abbreviations (continued)
GC gas chromatograph or gas chromatography
GC/MS gas chromatography/mass spectroscopy
CIS geographic information system
GPR ground-penetrating radar
HAZCAT hazard categorization
MRS hazard ranking system
HSL hazardous substance list
IATA International Air Transport Association
IDL 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
NPL 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
PAH polycyclic aromatic hydrocarbon
PARCC precision, accuracy, representativeness, completeness, and comparability
PCB polychlorinated biphenyl
PE performance evaluation
PID photoionization detector
POTW publicly owned treatment works
PPM parts per million
PPB parts per billion
PRP potentially responsible party
PTFE polytetrafluoroethylene
PVC polyvinyl chloride
Vlll
-------
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
-------
DATA QUALITY
OBJECTIVES
PERFORMANCE OBJECTIVES
At the end of this lesson, participants will be able to:
Identify the three stages of the data quality objective (DQO)
process
Identify the various data uses within the DQO framework
Explain the five levels of sample analysis (analytic levels)
available
Relate the DQO process to a conceptual model
-------
NOTES
DATA QUALITY OBJECTIVES
DATA QUALITY OBJECTIVES
(DQOs)
A process that yields quality and
cost-effective:
Sampling
Analysis
Data
DQO DEVELOPMENT PROCESS
Stage 1 - Identify decision types
Stage 2 - Identify data uses and needs
Stage 3 - Design data collection program
6/93
Data Quality Objectives
-------
NOTES
STAGE 1 - IDENTIFY DECISION
TYPES
Identify and involve data users
Evaluate available data
Develop a conceptual model
Specify objectives and decisions
IDENTIFY AND INVOLVE DATA
USERS
Primary users: Those involved in ongoing
remedial investigation and feasibility study
(RI/FS) activities
Secondary users: Those who rely on RI/FS
outputs to support their activities
EVALUATE AVAILABLE DATA
Information from the EPA, the United States
Geological Survey (USGS), and state and local
regulatory agency files
Other sources: Town hall, library, and
site maps
Data Quality Objectives
6/93
-------
NOTES
DEVELOP A CONCEPTUAL
MODEL
Pathway
Receptors^
EXAMPLE OF A CONCEPTUAL
MODEL
ngestion/
nhalatlon
txposure
SPECIFY OBJECTIVES AND
DECISIONS
Identify problems to be solved
Determine:
- Presence or absence of contaminants
- Types of contaminants
- Concentrations of contaminants
- Contaminant pathways
- Public and environmental health effects
6/93
Data Quality Objectives
-------
NOTES
STAGE 2 - IDENTIFY DATA USES
AND NEEDS
Identify data uses
Identify data types
Identify data quality needs
Identify data quantity needs
Evaluate sampling and analysis options
Review PARCC parameters
IDENTIFY DATA USES
Site characterization
Health and safety
Risk assessment
Alternatives evaluation
Monitoring
Potentially responsible party (PRP)
determination
IDENTIFY DATA TYPES
Analytical requirements
- Chemical analytical parameters
- Physical parameters
Data Quality Objectives
6/93
-------
NOTES
STAGE 2 - IDENTIFY DATA
USES/NEEDS
Identify data quality needs
Analytical levels:
- LEVEL I Field screening
- LEVEL II Field analysis
- LEVEL III Laboratory analysis
- LEVEL IV Laboratory analysis CLP RAS
- LEVEL V Laboratory analysis SAS
IDENTIFY DATA QUALITY NEEDS
Contaminants of concern
Levels of concern
Detection limit requirements
Critical samples
IDENTIFY DATA QUANTITY NEEDS
Data unavailable: Develop a phased
sampling approach
Data available: Use statistical techniques
6/93
Data Qualify Objectives
-------
NOTES
EVALUATE SAMPLING AND
ANALYSIS OPTIONS
Decrease %
of samples
analyzed
Data
quality
Cost and
turnaround
time
REVIEW PARCC PARAMETERS
' P recision
A ccuracy
> R epresentativeness
C ompleteness
C omparability
PARCC
Precise - Consistent, reliable sampling
and analysis results
Accurate - Free from error
Representative - Thoroughness in selecting
sampling locations and sufficient numbers
of samples
Complete - Sufficient amount of valid data
Comparable - Consistency among data
Data Quality Objectives
6/93
-------
NOTES
STAGE 3 - DESIGN DATA
COLLECTION PROGRAM
Assemble data collection components
Develop data collection documentation
ASSEMBLE DATA COLLECTION
COMPONENTS
Develop a comprehensive data
collection program
DEVELOP DATA COLLECTION
DOCUMENTATION
Sampling and analysis plan
Work plans
Enforcement concerns
6/93
Data Quality Objectives
-------
SAMPLE PLAN DEVELOPMENT
PERFORMANCE OBJECTIVES
At the end of this lesson, participants will be able to:
Discuss the necessary elements of a sampling plan
Describe various sampling designs relative to sample location
Discuss the differences between composite and grab samples
Describe procedures for field decontamination of sampling
equipment
-------
NOTES
SAMPLE PLAN DEVELOPMENT
SAMPLE PLAN DEVELOPMENT
REQUIRES COORDINATION
SAMPLING OBJECTIVES
Establish threat to public health or welfare or
to the environment
Locate and identify potential sources of
contamination
Define the extent of contamination
Determine treatment and disposal options
Document the attainment of cleanup goals
6/93
Sample Plan Development
-------
NOTES
SAMPLE PLAN DEVELOPMENT
Review existing historical site information
Perform site reconnaissance
Evaluate potential migration pathways
and receptors
Determine sampling objectives
Establish data quality objectives
SAMPLE PLAN DEVELOPMENT
Use field screening techniques
Select analytical parameters
Select sampling approach
Determine sampling locations
ELEMENTS OF A SAMPLING PLAN
Location and description of site
Media to be sampled
Analytical parameters
Container requirements
Field measurements
Well purging procedures
Sample Plan Development
6/93
-------
NOTES
ELEMENTS OF A SAMPLING PLAN
Preservation and filtration
QA/QC samples
Sample collection techniques
Documentation and transportation
Special equipment
Decontamination
LOCATION AND DESCRIPTION OF SITE
MEDIA TO BE SAMPLED
Air
Water
Soil and sediments
Bulk and containerized materials
6/93
Sample Plan Development
-------
NOTES
ANALYTICAL PARAMETERS
Container requirements
Field measurements
Well purging procedures
Preservation and filtration
QA/QC samples
Sample collection techniques
Sample Plan Development
6/93
-------
NOTES
SAMPLING DESIGN
Simple random sampling
Stratified random sampling
Systematic sampling
Cluster sampling
SIMPLE RANDOM SAMPLING
@ ฉ@ ฉ ฉ|
e
e
STRATIFIED RANDOM SAMPLING
|Q Q
Strata
Strata
6/93
Sample Plan Development
-------
NOTES
SYSTEMATIC SAMPLING
Systematic Grid Sampling
CLUSTER SAMPLING
Clusters
Documentation
Transportation
Sample Plan Development
6/93
-------
NOTES
Special equipment
Decontamination
SPECIAL EQUIPMENT
SAMPLING EQUIPMENT
ATTRIBUTES
Disposable or easily decontaminated
Inexpensive, especially disposable items
Easy to operate
Nonreactive
6/93
Sample Plan Development
-------
NOTES
DECONTAMINATION
The goal of most sampling efforts is to
acquire representative samples
Even trace amounts of contaminants from
prior sampling may invalidate the entire
project
DECONTAMINATION GOALS
No nationwide standards; some states
and regions have their own standards
The goal of decontamination is to
remove or reduce contaminants below
detection limits in order to avoid cross-
contamination
FIELD DECONTAMINATION
PROCEDURES
Wash with nonphosphate detergent
Rinse with tap water
Second rinse with distilled/deionized water
Appropriate solvent rinse
Final rinse with distilled/deionized water
Sample Plan Development
6/93
-------
NOTES
FIELD DECONTAMINATION
PROCEDURES
Air dry equipment
Wrap in aluminum foil
Collect equipment blanks daily
REDUCE EQUIPMENT
DECONTAMINATION PROBLEMS
Use disposable equipment
Use nonpermeable equipment
Bag equipment
Follow safe work practices
6/93
Sample Plan Development
-------
Office of Emergency and Remedial Response
Emergency Response Division
Environmental Response Branch, MS-101
United States
Environmental Protection
Agency
Office of
Solid Waste and
Emergency Response
January 1992
QualityAssurance
Sampling Plan for
Emergency Response
Quality Assurance Technical
Information Bulletin
What is QASPER?
QASPER is a PC-based software package which compiles
generic text and user-provided site-specific information
into a draft Quality Assurance / Quality Control (QA/QC)
Sampling Plan for the Removal Program. QASPER ad-
dresses the nine sections of a QA/QC Sampling Plan, as
specified in OSWER Directive 9360.4-01, QA/QC
Guidance for Removal Activities, Sampling QA/QC Plan,
and Data Validation Procedures (April 1990, EPA/540/G-
90/004).
Who is the Anticipated QASPER User?
The Oh-Scene Coordinators (OSCs) or the Technical As-
sistance Team (TAT) contractors are the primary users of
QASPER. These individuals will" have access to the site-
specific information and the sampling objectives that 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/QC 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
QASPER 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 (he QASPER
program.
Generates ASCII output in both file and hardcopy
formats. Files may be uploaded to other word
processing packages (i.e., WordPerfect) for fur-
ther manipulation.
Creates a hard copy QA/QC Sampling Plan ready
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 ihe
office, region, or zone by prompting the user to
consider the same set of questions for each site to
be addressed.
Improves efficiency for creating and reviewing
QA/QC Sampling Plan documents by allowing easy
modification of the document text cither through
the editor or through the word processing package.
Picks up information that has repetitive use in the
plan and imports the information io all sections
after the first entry, thus avoiding redundant data
entry.
Provides the user with access to standardised
generic text in various sections of the plan. Based
on the user's needs, this text may be imported
directly or may be edited to fit site-specific condi-
tions.
6/93
11
Sample Plan Development
-------
Has flexible data cnlry throughout plan generating
activities and informs the user as to which sections
are complete and which sections require addition-
al information.
Contents of QASPER
QASPER addresses the nine sections of a QA/QC Sam-
pling Plan, as specified in OSWER Directive 9360.4-01,
QA/QC Guidance for Removal Activities, Sampling
QA/QC Plan and Data Validation Procedures:
0.0 Title Page Information
Section 0.0 identifies information required to
complete the title page of a 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 material
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
quality objective (DQO) logic pathway begins in
this section and is carried forward to Sections
3.0, 4.0, 6.0 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 (QA-1, QA-2, or QA-3)
related to the selection. The same sequence will
be repeated for all parameters of concern at the
site.
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 are 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 related to the
proposed design or grid to achic\c the sample
event objectives. In conjunction with the sam-
pling design, the user must specify the standard
operating procedures (SOPs) that will be
employed. QASPER contains generic text 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 section are
the sample summary tables and QC sample
tables.
5.0 Project Organization and Responsibilities
Section 5.0 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 text as
needed.
7.0 Deliverables
Section 7.0 allows the user to import generic 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 II, 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 completed, the user can compile
the plan, make any necessary modifications, and print a
hard copy of the site-specific QA/QC Sampling Plan.
For copies of the software, contact:
Mr. William Coakley
U.S. EPA, ERT
Phone: (908) 906-6921
Ms. Christine Andreas
RoyF. Weston, Inc./REAC
Phone: (908) 632-9200
Sample Plan Development
12
6/93
-------
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
6/93 13 Sample Plan Development
-------
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.
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
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
6/93 15 Sample Plan Development
-------
Field personnel health and safety
Enforcement plan
The data will be evaluated against:
Federal/state action levels
Michigan and federal ARARs
3.0 QUALITY ASSURANCE OBJECTIVES
As identified in Sections 1.0 and 2.0, the objective of this project/event applies to the following
parameters:
Parameters
BNA (semivolatiles)
Metals
Metals
PAHs
PAHs
Matrix
drum liquid
groundwater
potable water
soil
waste material
Intended Data Use
site characterization
risk assessment
risk assessment
site characterization
site characterization
QA Objective
QA1
QA3
QA3
QA2
QA2
4.0 APPROACH AND SAMPLING METHODOLOGIES
4.1 Sampling Equipment
The following equipment will be used to obtain environmental samples from the respective
media/matrix:
Sample Plan Development 16 6/93
-------
Parameter/Matrix
Sampling
Equipment
Fabrication Dedicated
Decontamination
Steps
BNA
(semivolatiles)
COLIWASA
glass
No
Metals in
groundwater
bladder pump stainless steel Yes
Metals in potable sample bottle
water
glass
Yes
PAHs in soil
trowel
stainless steel No
PAHs in waste
material
bucket auger stainless steel No
Physical removal
Nonphosphate detergent
wash
Potable water rinse
10% nitric acid rinse
Organic-free water rinse
Air dry
Physical removal
Nonphosphate detergent
wash
Pesticide-grade acetone
rinse
Distilled/deionized water
rinse
Organic-free water rinse
Air dry
Physical removal
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:
4.3 Standard Operating Procedures
6/93
17
Sample Plan Development
-------
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 initialling 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 on-site.
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.
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
Sample Plan Development 18 6/93
-------
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
thief, a COLIWASA is extremely difficult to field decontaminate and relatively expensive, thereby
making it impractical to throw away.
6/93 19 Sample Plan Development
-------
Groundwater Well Sampling
Prior to sampling well, the well will be purged. For this project, this will be accomplished with a
[(bailer), (submersible pump), (non-gas contact bladder pump) or (suction pumps)].
Brush off well cap prior to opening, unlock and open 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 foot. 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 gal/ft3)
where:
n = pi
r = radius of well casing in feet.
h = height of water column of well from water level.
7.48 = conversion from ft3 to number of gallons.
Three well volumes at a minimum should be purged if possible. Equipment must be decontaminated
prior to use and between wells.
Approximately 10 feet of plastic sheeting will be placed around the well upon which the assembly
of the decontaminated purging equipment will be placed. 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 feet 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.]
Should the well yield be insufficient to produce the requisite three volumes, purging will continue
to the point of well evacuation, then terminated and the well will be sampled upon recharge.
Once purging is completed and the correct sample jars and/or 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 Teflonฎ 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.
Measure the conductivity, temperature, and pH of the groundwater in a separate container. Record
all field measurements on the field data sheets and in the field logbook.
Sample Plan Development 20 6/93
-------
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 desired sampling depth, and is then withdrawn. The auger tip is then
replaced with a tube core sampler, lowered down the bore hole,and driven into the soil at the
completion depth. The core is then withdrawn and the sample 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-foot 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 as 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 extracted.
Subsurface soil sample collection will involve test pit/trench excavation activities. Test pits/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
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 decontamination
procedure described elsewhere in Section 4.0.
6/93 21 Sample Plan Development
-------
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
Table 1: Proposed Schedule of Work
Activity
Soil sampling
Potable water sampling
Groundwater sampling
Drum sampling
Start Date
07/28/93
07/28/93
08/10/93
08/10/93
End Date
08/10/93
08/10/93
09/10/93
11/22/93
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 QA/QC 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 lab.
The following sampling personnel will work on this project:
Personnel Responsibility
Sample Plan Development
22
6/93
-------
The following laboratories will be providing the following analyses:
Lab Name/Location Lab Type Parameters
Amazing Analytical Lab
123 Reading Rd
Pittsburgh, KN Non-CLP All
6.0 QUALITY ASSURANCE REQUIREMENTS
The following requirements 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 will be determined and recorded, along with the data, where
appropriate.
4. Document sample holding times; this includes 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.
6/93 23 Sample Plan Development
-------
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 unscreened 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.
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; this includes 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 required.
8. Definitive identification on 100% of the "critical" 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.
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 financial
Sample Plan Development 24 6/93
-------
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.
8.0 DATA VALIDATION
QA2
Data generated under this QA/QC 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 QA/QC Sampling Plan. The holding times, blank
contamination, and detection capability will be reviewed for all remaining samples.
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
lab 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 lab.
6/93 25 Sample Plan Development
-------
Example Sample Plan
Figure 1-1 Site Location Map
Sample Plan Development 26 6/93
-------
Example Sample Plan
Figure 4-1 Sample Location Map
6/93 27 Sample Plan Development
------- An error occurred while trying to OCR this image.
------- An error occurred while trying to OCR this image.
-------
TARGET COMPOUND LIST (TCL) AND
QUANTITATION LIMITS (QL) (1)
Quantitation Limits (2)
Water Low Soil/Sediment (3)
Volatiles
CAS Number
1.
2.
3.
4.
5.
6.
7.
8.
9.
10.
11.
12.
13.
14.
15.
16.
17.
18.
19.
20.
21.
22.
23.
24.
25.
26.
27.
28.
29.
30.
31.
32.
33.
Chloromethane
Bromomethane
Vinyl Chloride
Chloroethane
Methylene Chloride
Acetone
Carbon Disulfide
1,1-Dichloroethene
1,1-Dichloroethane
1 ,2-Dichloroethene (total)
Chloroform
1,2-Dichloroethane
2-Butanone
1,1,1 -Tri chloroethane
Carbon Tetrachloride
Bromodichloromethane
1 ,2-Dichloropropane
cis-1 ,3-Dichloropropene
Trichloroethene
Dibromochloromethane
1 , 1 ,2-Trichloroethane
Benzene
trans- 1,3-Dichloropropene
Bromoform
4-Methyl-2-pentanone
2-Hexanone
Tetrachloroethene
Toluene
1 , 1 ,2,2-Tetrachloroethane
Chlorobenzene
Ethyl Benzene
Styrene
Xylenes (total)
74-87-3
74-83-9
75-01-4
75-00-3
75-09-2
67-64-1
75-15-0
75-35-4
75-34-3
540-59-0
67-66-3
107-06-2
78-93-3
71-55-6
56-23-5
75-27-4
78-87-5
10061-01-5
79-01-6
124-48-1
79-00-5
71-43-2
10061-02-6
75-25-2
108-10-1
591-78-6
127-18-4
108-88-3
79-34-5
108-90-7
100-41-4
100-42-5
1330-20-7
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
(1) Specific quantitation limits are highly matrix dependent. The quantitation limits listed herein are
provided for guidance and may not always be achievable.
Sample Plan Development
30
6/93
-------
(2) 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.
(3) Medium Soil/Sediment Quantitation Limits (QL) for Volatile TCL Compounds are 125 times the
individual Low Soil/Sediment QL.
Based on the Contract Laboratory Program Statement of Work, OLMO1.6 (6/91).
6/93 31 Sample Plan Development
-------
TARGET COMPOUND LIST (TCL) AND
QUANTITATION LIMITS (QL) (1)
Semivolatiles
CAS Number
Quantitation Limits (2)
Water Low Soil/Sediment (3)
/ig/L /ig/kg
34.
35.
36.
37.
38.
39.
40.
41.
42.
43.
44.
45.
46.
47.
48.
49.
50.
51.
52.
53.
54.
55.
56.
57.
58.
59.
60.
61.
62.
63.
64.
65.
66.
67.
68.
Phenol
bis(2-Chloroethyl)ether
2-Chlorophenol
1,3-Dichlorobenzene
1 ,4-Dichlorobenzene
1 ,2-Dichlorobenzene
2-Methylphenol
2,2-oxybis(l-chloropropane)
4-Methylphenol
N-Nitroso-di-n-propylamine
Hexachloroethane
Nitrobenzene
Isophorone
2-Nitrophenol
2,4-Dimethylphenol
bis(2-Chloroethoxy)methane
2,4-Dichlorophenol
1 ,2,4-Trichlorobenzene
Naphthalene
4-Chloroaniline
Hexachlorobutadiene
4-Chloro-3-methylphenol
2-Methylnaphthalene
Hexachlorocyclopentadiene
2,4,6-Trichlorophenol
2,4,5-Trichlorophenol
2-Chloronaphthalene
2-Nitroaniline
Dimethylphthalate
Acenaphthylene
2,6-Dinitrotoluene
3-Nitroaniline
Acenaphthene
2,4-Dinitrophenol
4-Nitrophenol
108-95-2
111-44-4
95-57-8
541-73-1
106-46-7
95-50-1
95-48-7
108-60-1
106-44-5
621-64-7
67-72-1
98-95-3
78-59-1
88-75-5
105-67-9
111-91-1
120-83-2
120-82-1
91-20-3
106-47-8
87-68-3
59-50-7
91-57-6
77-47-4
88-06-2
95-95-4
91-58-7
88-74-4
131-11-3
208-96-8
606-20-2
99-09-2
83-32-9
51-28-5
100-02-7
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
10
25
10
25
10
10
10
25
10
25
25
330
330
330
330
330
330
330
330
330
330
330
330
330
330
330
330
330
330
330
330
330
330
330
330
330
800
330
800
330
330
330
800
330
800
800
69. Dibenzoruran
132-64-9
10
330
Sample Plan Development
32
6/93
-------
70.
71.
72.
73.
74.
75.
76.
77.
78.
79.
80.
81.
82.
83.
84.
85.
86.
87.
88.
89.
90.
91.
92.
93.
94.
95.
96.
97.
(1)
(2)
(3)
2,4-Dimtrotoluene 121-14-2
Diethylphthalate 84-66-2
4-Chlorophenyl-phenylether 7005-72-3
Fluorene 86-73-7
4-Nitroaniline 100-01-6
4,6-Dinitro-2-methylphenoI 534-52- 1
N-nitrosodiphenylamine 86-30-6
4-Bromophenyl-phenyl ether 101-55-3
Hexachlorobenzene 1 1 8-74- 1
Pentachlorophenol 87-86-5
Phenanthrene 85-01-8
Anthracene 120-12-7
Carbazole 86-74-8
Di-n-butylphthalate 84-74-2
Fluoranthene 206-44-0
Pyrene 129-00-0
Butylbenzylphthalate 85-68-7
3,3-Dichlorobenzidine 91-94-1
Benz(a)anthracene 56-55-3
Chrysene 218-01-9
bis(2-Ethylhexyl)phthalate 1 17-81-7
Di-n-octylphthalate 1 17-84-0
Benzo(b)fluoranthene 205-99-2
Benzo(k)fluoranthene 207-08-9
Benzo(a)pyrene 50-32-8
Indeno(l,2,3-cd)pyrene 193-39-5
Dibenz(a,h)anthracene 53-70-3
Benzo(g,h,i)perylene 191-24-2
Specific quantitation limits are highly matrix dependent. The
provided for guidance and may not always be achievable.
10
10
10
10
25
25
10
10
10
25
10
10
10
10
10
10
10
20
10
10
10
10
10
10
10
10
10
10
330
330
330
330
800
800
330
330
330
800
330
330
330
330
330
330
330
660
330
330
330
330
330
330
330
330
330
330
quantitation limits listed herein are
Quantitation limits listed for soil/sediment are based on wet weight.
calculated by the laboratory for soil/sediment on dry weight
basis will
Medium Soil/Sediment Quantitation Limits (QL) for Semivolatile TCL
The quantitation limits
be higher.
Compounds are 60 times
the individual Low Soil/Sediment QL.
Based on Contract Laboratory Program Statement of Work, OLMO1.6 (6/91).
6/93
33
Sample Plan Development
-------
TARGET COMPOUND LIST (TCL) AND
QUANTITATION LIMITS (QL) (1)
Pesticides/PCBs
Quantitation Limits (2)
Water Low Soil/Sediment (3)
CAS Number
98.
99.
100.
101.
102.
103.
104.
105.
106.
107.
108.
109.
110.
111.
113.
114.
115.
116.
117.
118.
119.
120.
121.
122.
123.
124.
125.
126.
alpha-BHC
beta-BHC
delta-BHC
gamma-BHC (Lindane)
Heptaclor
Aldrin
Heptachlor epoxide
Endosulfan I
Dieldrin
4,4'-DDE
Endrin
Endosulfan II
4,4'-DDD
Endosulfan sulfate
4,4'-DDT
Methoxychlor
Endrin ketone
Endrin aldehyde
alpha-Chlordane
gamma-Chlordane
Toxaphene
Aroclor-1016
Aroclor-1221
Aroclor-1232
Aroclor-1242
Aroclor-1248
Aroclor-1254
Aroclor-1260
319-84-6
319-85-7
319-86-8
58-89-9
76-44-8
309-00-2
1024-57-3
959-98-8
60-57-1
72-55-9
72-20-8
33213-65-9
72-54-8
1031-07-8
50-29-3
72-43-5
53494-70-5
7421-36-3
5103-71-9
5103-74-2
8001-35-2
12674-11-2
11104-28-2
11141-16-5
53469-21-9
12672-29-6
11097-69-1
11096-82-5
0.05
0.05
0.05
0.05
0.05
0.05
0.05
0.05
0.10
0.10
0.10
0.10
0.10
0.10
0.10
0.50
0.10
0.10
0.5
0.5
1.0
0.5
0.5
0.5
0.5
0.5
1.0
1.0
1.7
1.7
1.7
1.7
1.7
1.7
1.7
1.7
3.3
3.3
3.3
3.3
3.3
3.3
3.3
17.0
3.3
3.3
1.7
1.7
170.0
33.0
33.0
67.0
33.0
33.0
33.0
33.0
(1) Specific quantitation limits are highly matrix dependent. The quantitation limits listed herein are
provided for guidance and may not always be achievable.
(2) 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.
(3) Medium Soil/Sediment Quantitation Limits (QL) for Pesticides/PCB TCL compounds are 15
times the individual Low Soil/Sediment QL.
Based on the Contract Laboratory Program Statement of Work, OLMO1.6 (6/91).
Sample Plan Development
34
6/93
-------
INORGANIC TARGET ANALYTE LIST (TAL)
Detection Limit
Analyte (jug/L - water [1])
Aluminum
Antimony
Arsenic
Barium
Beryllium
Cadmium
Calcium
Chromium
Cobalt
Copper
Iron
Lead
Magnesium
Manganese
Mercury
Nickel
Potassium
Selenium
Silver
Sodium
Thallium
Vanadium
Zinc
Cyanide
200
60
10
200
5
5
5000
10
50
25
100
3
5000
15
0.2
40
5000
5
10
5000
10
50
20
10
(1) Sediment detection limit 100 x water (jug/kg - soil/sediment).
Based on the Contract Laboratory Program Statement of Work, ILMO2.1 (9/91).
6/93 35 Sample Plan Development
-------
PB92 - 963356
Publication 9285.7-09A
April 1992
Appendix II
of the
"Guidance for Data Useability in
Risk Assessment (Part A)"
Final
Office of Emergency and Remedial Response
U.S. Environmental Protection Agency
Washington, D.C. 20460
6/93 37 Sample Plan Development
-------
APPENDIX II
LISTING OF COMMON POLLUTANTS GENERATED BY SEVEN INDUSTRIES
Appendix II identifies seven industries that generate waste which contains pollutants that
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
1 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.
39 Sample Plan Development
-------
o
VI
a
o
a.
6
8,
T3
I
o a
>, .9
3 a
II
S 5
o o
II I
^ I
-------
.g
6
I
g.
I
ปiov%rปwit5
iiiSigxSS
35
-------
to;
I
o
a.
J
ง
O
to
u
s
^*i 8
:o
all I.
&9S SgP 2 ซ5งeCo5g
!g|ง||||||alง|||||ง
Sample Plan Development
42
6/93
-------
-* rป rป
I
(5/P3
43
Sample Plan Development
-------
5
I
Z
g
I
o
U
1
DC
> >
TD afl-- z > Q
" jM 2 uJ ฃ Z < Z > H Q < 2 a Z O 5 J 5. ฃ n 5.
Sample Plan Development
44
6/93
-------
.t!
I
E
o
CJ
a;
IHPiSadiiij:
Ieงige5gyl|fis35*sasi3
55 = co-MZQ2l-OH2NS
-------
o
V)
o
c
Z
O
U)
o s
s s
Sample Plan Development
6/93
-------
i
gb*
&
i
ง
47
Sample Plan Development
-------
3
O
O.
3
hi
.<00
ul
>
Sample Plan Development
48
6/93
-------
I
.it
m
1
oฃ
6/93
49
Sample Plan Development
-------
i.
J
rป rป t~t~
iง i
QQ ,g
ggoS
II
Si^l?
,ss^g|
Sample Plan Development
50
6/93
-------
is
1
g
I
I
ง 11421
3 nsnSz^u
5/PJ
51
Sample Plan Development
-------
FIELD SCREENING
PERFORMANCE OBJECTIVES
At the end of this lesson, participants will be able to:
Describe the use of aerial photography and Sanborn Fire
Insurance maps in site screening
Determine the advantages and limitations of soil gas and x--
ray fluorescence techniques
Describe the advantages and limitations of the following
geophysical techniques in locating drums and trenches:
Magnetics
Electromagnetics
Ground-penetrating radar
-------
/VOTES
FIELD
SCREENING
VISUAL RECONNAISSANCE
Aerial photographs
Sanborn Fire Insurance maps
Topographic and land use maps
Site walkover
AERIAL PHOTOGRAPHY
Historical photography
(1920 - present)
Contract photography
(current site)
6/93
Field Screening
-------
NOTES
EPIC
Environmental Photographic
Interpretation Center
Western Region - EMSL/Las Vegas, Nevada
Eastern Region - EPA-EPIC/Warrenton, Virginia
USDA ASCS
Agricultural Stabilization and Conservation Service
Aerial Photography Field Office
Salt Lake City, Utah
(801)525-5856
1945 -present
black & white
color infrared
SANBORN FIRE INSURANCE
MAPS
1869 to 1950s
Communities with populations >2000
Updated periodically
Locations of industries, pipelines, storage
vats, old dumps, and wetlands
Field Screening
6/93
-------
OTHER MAPS
USGS, ASCS, and states
Topographic
Land use
Geologic
Hydrologic
FIELD SCREENING
X-ray fluorescence
Soil gas
Geophysics
X-RAY FLUORESCENCE
Field portable instrument
Metals identification
Real-time quantitative analysis
NOTES
6/93
Field Screening
-------
NOTES
SOIL GAS
Field portable or truck-mounted
instrument
Primarily volatile organics identification
Real-time semiquantitative analysis
SOIL GAS USES
Delineate groundwater plumes
Locate source of soil contamination
Locate groundwater monitoring wells
GEOPHYSICS
Magnetics
Electromagnetics (EM)
Ground-penetrating radar (GPR)
Field Screening
6/93
-------
NOTES
MAGNETICS
Earth's magnetic field intensity measured
Total field or vertical component
Ferromagnetic material detected
Passive method
ELECTROMAGNETICS
Electric field induces secondary fields
Electrical conductivity of ground
measured
Conductive material detected
Active method
GROUND-PENETRATING RADAR
Electromagnetic energy transmitted/
received
Reflections at material horizons
Metal or changes in geology detected
Active method
6/93
Field Screening
-------
NOTES
GPR PENETRATION
Shallow for clay
Deeper for dry sands
Field Screening
6/93
-------
ENVIRONMENTAL PHOTOGRAPHIC INTERPRETATION CENTER
Advanced Monitoring Systems Division
Environmental Monitoring Systems Lab - Las Vegas
Products and Services
v>EPA
6/93
Field Screening
-------
THE ENVIRONMENTAL PHOTOGRAPHIC INTERPRETATION CENTER (EPIC)
Advanced Monitoring Systems Division
Environmental Monitoring Systems Laboratory - Las Vegas
Products and Services
EPA's Environmental Photographic Interpretation Center
(EPIC) provides a wide range of remote sensing and aerial
photographic: analyses, mainly in support of investigations under
Superfund, RCRA, the Clean Water Act and the National Contingency
Plan. The comprehensive aerial photographic analyses are
supported by a wide array of services including aerial photo
overflight planning, collateral data acquisition, aerial film
processing, historical aerial photo search and acquisition, and
CIS data base development. EPIC produces fully annotated maps
and photos accompanied by descriptive text to document historical
or current analyses of hazardous waste disposal and handling,
emergency response efforts, inventories of potential hazardous
waste sites, and specialized analyses including wetlands
classification and delineation, photogeology and fracture trace
analysis and. photogrammetric mapping. EPIC maintains a
multidisciplinary staff with backgrounds in geography, geology,
biology, remote sensing, forestry and natural resources
management.
The following sections present summary descriptions of
EPIC's products and services.
Hazardous Waste Site Analyses
Analysis of hazardous waste sites using historical and
current aerial photography comprises a major part of EPIC's
workload. Utilizing the vast archives of aerial photography of
the country maintained by government and private sources, dating
back to the 1930's, EPIC's analysts can reconstruct the waste
handling and. disposal history of a site in order to support site
cleanup and regulatory or enforcement efforts. Aerial
photography can be a powerful tool in court in the form of
evidence and expert witness testimony.
Interpretation of aerial photography can yield information
on site size, drainage patterns, type of fill materials,
leachate, burial sites, lagoons, impoundments and their contents,
and general condition of the site. Locations and descriptions of
tanks, drums, open storage areas, evidence of vegetation stress,
on-site obstacles, structures, equipment and access routes can
also be provided. Historical analysis provides the information
necessary to obtain a chronological understanding of a site's
development and activities, and can lead to the identification
of a specific problem. The information interpreted from the
6/93 9 Field Screening
-------
photography is provided to the requester on photo enlargements,
with overlays annotated with descriptive findings. Accompanying
text provides a full site description.
inventories of Potential Hazardous Waste Sites
Inventories of potential hazardous waste sites covering
large areas and decades in time are a very cost effective way to
discover sites for future investigation. The aerial photography
is systematically searched for specific features or types of
sites specified by the requester. These can include landfills,
open dumps, scrap salvage yards, chemical handling and storage
facilities, impoundments, or abandoned industrial sites.
Identified sites are located on overlays to topographic maps
accompanied by data sheets describing site conditions. The site
conditions are presented chronologically with the period of site
activity shown on the map overlay. This approach is helpful in
determining the origin of a progressive problem and in
identifying a hazardous site that is currently hidden by new
development.
Emergency Response
EPIC has the quick response capabilities to react to
emergency situations such as hazardous material releases and
natural disasters like hurricanes (Hugo) and earthquakes (San
Francisco/Oakland, Ca.). Aerial photography is flown, processed
and analyzed to provide immediate information to on-site
personnel regarding circumstances not easily or safely observed
from the ground. Typical products for an emergency response
project include an immediate telephone report to on-site
personnel followed by photographs or positive film transparencies
with interpretation results annotated on overlays, annotated
topographic maps, and a short letter report describing analysis
results.
Wetlands
Wetland analyses are performed in support of various
sections of the Clean Water Act concerning enforcement,
permitting and advance identification. Analysis of historical
aerial photography is often the only means of establishing the
prior existence of wetlands on lands that have been dredged or
filled, and calculating wetland loss acreages necessary for
mitigation settlements. Aerial photographs can also provide
information concerning vegetative type, periodicity of flooding,
tidal influences, and affected drainage patterns.
A hierarchical wetlands and deepwater habitats
classification system developed by Cowardin et al. for the U.S.
Fish and Wildlife Service is used in the analyses.
Jurisdictional delineation procedures are followed in the field
according to the Federal Manual for Identifying and Delineating
Jurisdictional Wetlands. Field checking is performed in
Field Screening 10
-------
enforcement cases to verify accuracy of interpretation and
classification by visiting representative areas. The field
reconnaissance checks representative wetlands in proximity to,
and matching the aerial photographic signatures of, those at the
site being investigated prior to its alteration.
Simplified studies are also performed on Superfund sites or
on studies where a wetland/upland boundary satisfies the needs of
the requestor. These studies entail the placement of wetland
symbols or the delineation of wetland boundaries on overlays to
photographic prints. The aerial photographic analysis is
supported by collateral information regarding the soils,
hydrology and local vegetation.
Photogeology
Photogeology involves the interpretation of the geology of
an area from an analysis of landforms, drainage, tones, and
vegetation distribution on aerial photographs. EPIC produces two
types of photogeologic products: fracture trace analyses and
lithologic mapping.
Fracture trace analysis involves the use of aerial
photography and other types of imagery to identify linear
features on the earth's surface that are naturally occurring and
are surface manifestations of subsurface fracture zones in the
bedrock. When viewed in cross-section, fracture traces are seen
to be vertical or near vertical breaks in the bedrock. Fractures
are of particular environmental concern because contaminants are
likely to move more easily through zones of fractured bedrock
than through the surrounding more consolidated bedrock material.
Thus, fracture traces can be used to identify possible migration
routes of pollutants and are often used in the placement of
monitoring/remedial wells around hazardous waste sites.
Lithologic mapping (mapping of distinct rock types or units)
from aerial photographs involves the interpretation of surface
features in order to produce a more accurate geologic map in
areas where geologic mapping is incomplete due to limited field
work, small map scale, etc.
Photoqrammetric Mapping
EPIC produces highly accurate topographic and planimetric
maps, generally at a large scale, which conform with National Map
Accuracy Standards and EPA Photogrammetric Mapping
Specifications. Map scales, contour intervals, and planimetric
details can be varied to suit specific requirements.
Photogrammetric techniques can be used to measure the area
and volume of hazardous wastes; determine the height and
placement of containment berms, dikes, and impoundments; and
determine the depth of waste pits. Changes in size, shape, and
other physical characteristics of a waste site can be documented
- Field Screening
-------
through sequential photogrammetric mapping.
Photogrammetric techniques can also be used in establishing
precise location and orientation data to support geophysical
monitoring or monitoring well placement.
Geographic Information Systems (GI8)
In cooperation with its sister branch, the Remote and Air
Monitoring Branch (AMS), which houses one of EPA's CIS Centers of
Excellence, EPIC has completed several CIS projects. One project
supported a National Priorities List (NPL) hazardous waste site
investigation using information from diverse sources (including
numerous years of historical aerial photography, geological data,
digital line graph data, soil data, property ownership,
monitoring well data, etc.). This data was combined to produce
topical maps and analyses for use in the Remedial
Investigation/Feasibility Study decision-making process under
Superfund. Another project involved the ecological
characterization of a pilot site using photo-derived information
on land use, vegetation, wetlands and landforms to produce maps
and overlays for landscape characterization and trend analysis.
Additionally, the CIS has been used to obtain wetland gain and
loss measurements for enforcement actions against violations of
the Clean Water Act.
Miscellaneous Analyses
Additional analyses include interpretation of thermal
infrared imagery for detection of illegal river discharges and
landfill and mine fires; detection of abandoned oil, gas and
water wells; mapping of submerged aquatic vegetation; and land
use and drainage mapping.
Data Acquisition
EPIC acquires historical photography, dating to the late
1930's, from a wide range of Federal, state and local government
agencies and private aerial survey companies. Current
overflights, customized to the requestor's needs as to scale,
imagery type, time of year, etc, are obtained through a network
of private aerial companies across the country. These aerial
companies are also available on short notice for emergency
response efforts. Additional sources of information acquired
include U.S. Geological Survey maps, Sanborn Fire Insurance Maps
and U.S. Department of Agriculture Soil Surveys.
Photo Lab
The technical services of EPIC's photographic laboratory
include:
o Complete photographic processing and printing of
Field Screening 12
-------
black-and-white, color, color infrared, and
black-and-white thermal infrared film;
o Custom processing and printing, to include
reproducing old maps, line work, and historical imagery
o Responding to emergencies, such as oil spills, train
derailments, and chemical fires
Graphics Support
EPIC offers graphics, cartography, drafting and ancillary
support for the preparation of finished documents. Our present
capabilities include:
o Preparing camera-ready artwork for publications,
reports, briefings, and presentations
o Preparing inked overlays keyed to aerial photography
and maps, and preparation of transparencies for use as
overlays or in briefings
o Assembling completed reports including layout, mounting
of photographs and text, covers, and binding
o Mounting and labeling of photographs for litigation or
public hearings
13 Field Screening
-------
! NVIRONMENTAL PHOTOGRAPHIC INTERPRETATION CENTER (EPIC)
AERIAL SERVICES REQUEST FORM
Request Date:
I. SITE DATA
Site Name: Region:
Program: (circle) Superfund RGRA RCRA Enf. Other
If Superfurd: Site/Spill ID*
Purpose (circle): Remedial Removal Enf. Other.
Geographic Coordinates: long. Lat.
State: County: Municipality:
USGS Quad Name (IMPORTANT: ATTACH PHOTOCOPY OF MAP SHOWING SITE BOUNDARIES
AND/OR STUDY AREA):
Regional Project Manager: Phonefl FTS COMM.
Brief discussion of site history, specific problems at site, what you hope to
accomplish through this request. Elaborate on kncwn or suspected aspects of site
operation (e.g. barrels believed dumped between 1967 and 1972 adjacent to north
lagoon). Please attach background information about the site such as site
descriptions, action memos, etc.
II. STANDARD REQUEST OPTIONS - Check and complete the appropriate section
for the type of service you are requesting.
1. CURRENT PHOTOGRAPHY ONLY (new overflight)
a. Scale: (e-g-/ 1:24,000)
***Average
turnaround b. Special conditions (e.g., do not fly if snow cover, leaves time
= 6 wks.*** on, etc.)
c. Photo size: 9"x9" 20"x20" Other
d. Are stereo pairs needed? Y N
e. Number of copies:
f. Desired delivery date:
Field Screening 14 6/93
-------
-2-
***Average
turnaround
time ป
6-10 wks.***
_ 2. HISTORICAL PHOTOGRAPHY ONLY
a. Study period (e.g., 1936-1955):
b. Specific years desired:
c. Kioto size: 9"x9" 20"x20"
d. l^fumber of copies:
e. Desired delivery date:
Other
***Average
turnaround
time =
8 wks.***
_ 3. ANALYSIS OF CURRENT (single coverage) PHOTOGRAPHY
a. Scale: (e.g., 1:24,000)
b. Special conditions (e.g., do not fly if snow cover, leaves
on, etc.)
c. Photo size: 9"x9"
d. Number of copies:
20"X20"
Other
e. Desired delivery date:
***Average
turnaround
time ซ=
12-24 wks.
4. ANALYSIS OF HISTORICAL PHOTOGRAPHY (standard site analysis
package - see attachment)
a. Study period (e.g., 1936-1955):
b. Specific years of interest:
c. Are copies of historical photos (before analysis) needed?
. Y N
20"X20" Other
If yes, photo size: 9"x9"_
d. Is an interim report (unbound format, handwritten photo
overlays with typed body of report) needed? Y N
e. Number of copies of final bound report:
f. Desired delivery date:
5. SURVEYING AND MAPPING - Complete and attach request form
6/93
15
Field Screening
-------
-3-
III. SPECIAL REQUEST OPTIONS - The following remote sensing services are also
available for sitjes with conditions that warrant their use. Check off items of
interest and contact your remote sensing coordinator for inore information.
a. Land use analysis (within specified distance from site)
b. Fracture trace analysis
c. Wetland mapping/assessment
d. Malti-spectral scanner overflights
e. Thermal infrared scanner overflights
f. Mensuration (measurements) of features (e.g., barrel/drum count,
terrain transects, building dimensions< lagoon dimensions, etc.)
Field Screening 16
-------
EPA/EPIC
Remote Sensing Training Course
Sanoorn Maps
The Sanborn maps are fire insurance maps created by the Sanborn Map
Company of Pel ham, New York. The maps, produced as early as 1867, were made
to provide insurance companies with pertinent information to make risk.
assessments on commercial buildings, factories, and dwellings. Information
provided on each of these structures typically includes a structure's size and
shape, locations of windows and doors, presence of firewalls, sprinkler
systems, types of roofs, distance to fire hydrants and the location of water
mains.
The maps give an accurate delineation of the boundaries of industrial or
commercial activities, the current state of activity (i.e., under construction
in'1903'}, the number and location of storage tanks (and frequently their
contents), the type of processing taking place in specific areas, "and such
features as the presence of earthen fire walls around storage tanks or
processing areas which may serve as secondary structures to restrict the
spread of-any accidental spills or leaks.
6/93 17 Field Screening
-------
COMPREHENSIVE LISTING OF AERIAL PHOTOGRAPHY
libraried at the
U.S. DEPT OF AGRICULTURE, ASCS
AERIAL PHOTOGRAPHY FIELD OFFICE
2222 WEST 2300 SOUTH
P.O. BOX 30010
SALT LAKE CITY, UTAH 84130-0010
The comprehensive listing shows the various photographic coverages used by the
U.S. Department of Agriculture archived at the Aerial Photography Field
Office. This library includes photography used by the Agriculture
Stabilization and Conservation Service (ASCS) and it predecessor agencies, the
U.S. Forest Service (FS) and the Soil Conservation Service (SCS).
Coverage of the Agricultural Stabilization and. Conservation Service and the
Soil Conservation Service is listed alphabetically by states and counties.
A Federal Information Processing Standards (FIPS) numerical code is
assigned to each county flown by ASCS and SCS after July 1, 1971.
Coverage of Forest Service photography is listed alphabetically for each
forest within a region. Numerical cades used to identify FS projects are
assigned by the Forest Service.
NAPP - National Aerial Photography Program and
NHAP - National High Altitude Photography - are flown in color infrared
positive film. Coverage is listed alphabetically by state and county.
Due to the constant state of change in the acquisition of new coverage
available from NAPP/NHAP, this part of the listing is designed to allow
for timely and periodic updates. New listings by state are available upon
written request.
Photo indexes or spot indexes and microfilm duplicates are available for
most projects. The number of index sheets required to cover a project is
shown.
Rectified enlargements are available from photography used for ASCS
programs. This means that scale, tip, and tilt data, computed through an
analytical aerotriangulation system, is available to produce true-to-scale
enlargements for indicated projects. An increasing amount of
rectification data is also available from some of the Soil Conservation
Service and Forest Service projects.
See reverse side for a glossary of terms, however, if you have any questions
please contact the Aerial Photography Field Office at (801) 524-5856.
Field Screening 18 6/93
-------
GLOSSARY OF TERMS
YEAR - Year the original contract was let.
CONTRACT YEAR(S) - Year the original contract was let. Not the year the photography
was flown. (1. - Cycle 1 NHAP i.e. 1HAP80
2_ - Cycle 2 NHAP i.e. 2HAP85
1 - Cycle 3 NAPJP i.e. 3HAP87)
MAJ YR
FLOWN - (NAPP/NHAP Listing only) Year the majority of the county was flown.
(P) - Partial coverage. For ASCS projects, partial coverage
generally occured in counties containing large areas of non-agricultural
land.
SCALE - Fractional scale [i.e. (40) = 1:40,000]
INTERNEG - Black ฃป white internegative from NAPP/NHAP photography is on file.
FILM - Film Type
B/W - Black and White Negative
CIRP - Color Infrared Positive
CIRN - Color Infrared Negative
CN - Color Negative
PI - Photo index. A rough mosaic assembly of the prints covering each project or
county area. The assembly of prints is copied to a scale of 1" = 1 mile. The
number listed indicates the number of index sheets needed to cover a county
or project area.
SI - Spot or Line Index. A detailed map with the center of each photograph
plotted by flight line and exposure number.
RECT - Rectification data available. Enlargements can be photographically rectified
to produce scale accurate reproductions of cropland or cultural areas.
REMARKS -
* - Scheduled for rectification.
BLK - One or more county or project areas grouped to form a larger block.
ASCS/
SCS - First agency to require rectification accuracy.
6/93 19 Field Screening
-------
United States
Department of
Agriculture
Agricultural
Stabilization and
Conservation Service
Aerial
Photography
Field Office
P.O. Box 30010
Salt Lake City.
Utah 84130
NAPP PHOTOGRAPHY
(1937 -Present)
. NAPP - NATIONAL AERIAL PHOTOGRAPHY
PROGRAM.
. COLOR INFRARED POSITIVE PHOTOGRAPHY/
ORIGINAL FILM HELD BY APFO.
(B&cW products are available.)
. 1:40,000 SCALE.
. CONTRACTED BY STATE/PARTIAL STATE.
. LEAF-ON AND LEAF-OFF PHOTOGRA15HY
DEPENDING ON CONTRACTING SEASON.
. FLOWN IN N/S DIRECTION.
. 6" FOCAL LENGTH.
. AVERAGE ENDLAP 62%.
. AVERAGE SIDELAP 40%. (Ranges from
30% to 50% depending on latitude.)
. ONE FJLL FRAME COVERS APPROXIMATELY
32 SQUARE MILES OF TERRAIN.
. 10 STEREOSCOPIC PHOTOGRAPHS PER USGS
STANDARD 7 1/21 TOPOGRAPHIC MAP.
(*Quarter-quad centered photography.)
NHAP PHOTOGRAPHY
(1900 - 1987)
. NHAP - NATIONAL HIGH ALTITUDE PROGRAM.
. COLOR INFRARED POSITIVE PHOTOGRAPHY/
ORIGINAL FILM HELD BY APFO.
(BkU products are available.)
. 1:60,000 SCALE.
. CONTRACTED GEOGRAPHICALLY lฐxlฐ.
.. CYCLE 1 (1980-1985) - LEAF-OFF PHOTOGRAPHY.
CYCLE 2 (1985-1987) - LEAF-ON PHOTOGRAPHY.
. FLOWN LN N/S DIRECTION.
. 8 1/4" FOCAL LENGTH.
. AVERAGE ENDLAP 65%.
. AVERAGE SIDELAP 12%.
ONE FULL FRAME COVERS APPROXIMATELY
72 SQUARE MILES OF TERRAIN.
4 STEREOSCOPIC PHOTOGRAPHS PER USGS
STANDARD 71/2' TOPOGRAPHIC MAP.
(*Quad centered photography.)
*2 FLIGHT LINES PER 7 1/2' QUAD
AREA COVERED
BY ONE FRAME
*1 FLIGHT LINE PER 7 1/2' QUAD
AREA COVERED
BY ONE FRAtffi
Field Screening
20
6/93
-------
SAMPLE ANALYSIS
PERFORMANCE OBJECTIVES
At the end of this lesson, participants will be able to:
Define the target compound list
Determine the type of analysis necessary to identify specific
analytes
Define quality control and how it affects the sampling
process
Determine appropriate sampling containers and preservatives
based on the sample media
Define holding time and its importance to sample analysis
-------
NOTES
SAMPLE ANALYSIS
SAMPLE ANALYSIS
Target compound list
Quality control
Quality control samples
Sample containers
Comprehensive Environmental Response,
Compensation and Liability Act (CERCLA)
Superfund
(CLP)
Target compound list
6/93
Sample Analysis
-------
NOTES
TARGET COMPOUND LIST
Organics
- Volatile compounds
- Semivolatile compounds
- Pesticides and PCBs
Inorganics
- Metals
- Cyanide
QUALITY ASSURANCE/QUALITY
CONTROL (QA/QC) GOAL
Identify and implement correct
sampling and analysis methods
Limit the error introduced into
the sampling and analysis procedures
QA/QC SAMPLES
Analyze in addition to field
samples
Provide information on variability
and usability of data
Sample Analysis
6/93
-------
NOTES
BACKGROUND SAMPLES
Collect sample upgradient of
contaminated area (onsite or
offsite)
Select area with little or no
contaminant migration
BACKGROUND SAMPLES
Determine the natural composition
of the soil
Determine the constituents of water
Provide a basis for comparison for
samples collected at the site
COLLOCATED SAMPLES
Collect adjacent to the routine
field sample
Collect 0.5 - 3 feet away from the
selected field sample
6/93
Sample Analysis
-------
NOTES
COLLOCATED SAMPLES
Determine local variability of
contamination at the site
Can be used to assess site variation
in immediate sampling area
Cannot be used to assess variability
across the site
FIELD REPLICATE SAMPLES
Obtain samples from one location
Homogenize the samples
Divide homogenized sample into
separate containers
Treat as separate samples in subsequent
sample handling and analysis processes
FIELD REPLICATE SAMPLES
Assess error associated with:
Sample heterogeneity
Sample methods
Analytical procedures
Sample Analysis
6/93
-------
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
Use with volatile organic samples
TRIP BLANKS
Assess error associated with:
Sampling
Sample handling and shipping
Laboratory handling and analysis
NOTES
6/93
Sample Analysis
-------
NOTES
FIELD BLANKS
Prepare in the field
Use certified clean sand or soil
or analyte-free deionized water
FIELD BLANKS
Evaluate contamination errors
associated with:
Sampling methods
Laboratory procedures
MATRIX SPIKE SAMPLES
Field sampling
- Collect triple the volume for organic
water samples
- Collect double the volume for inorganic
water samples
Laboratory analysis
- Use selected or requested field samples
- Spike samples in the laboratory with known
concentrations of target analytes
Sample Analysis
6
6/93
-------
NOTES
MATRIX SPIKE SAMPLES
Verify percent recoveries
Check sample matrix interferences
Monitor laboratory and method
performance
PERFORMANCE EVALUATION
(PE) SAMPLES
Third party prepares sample
Analytes in PE samples are the same
as analytes of concern
Analyte concentration(s) known to preparer
Analyte concentration(s) unknown to laboratory
PERFORMANCE EVALUATION
(PE) SAMPLES
Evaluate the overall bias of the
analytical laboratory
Detect error in the analytical
method used
6/93
Sample Analysis
-------
NOTES
QA/QC SAMPLES
Sample type
Background
Collocated
Quantity
At least 1"
Minimum of 8 samples"'"
Individual agency's
regulations may vary
Varies by site
Source: US EPA, 1991. Removal Program: Representative Sampling Guidance
Source: US EPA, 1990. QA/QC Control Guidance for Removal Activities
For statistical analysis to be valid
QA/QC SAMPLES
Sample type
Field replicates
Rinsate blanks
(Equipment blanks)
Quantity
Minimum of 8 samples1'"'0
or 1 sample per 10
samples, whichever is
greater
One per day per type
of sampling device*
Source: US EPA, 1991. Removal Program: Representative Sampling Guidance
Source: US EPA, 1990. QA/QC Control Guidance for Removal Activities
For statistical analysis to be valid
QA/QC SAMPLES
Sample type
Trip blanks
Field blanks
Quantity
1 per day for VOA
samples"'"
1 per day for each
group of samples of
a similar matrix-
Source: US EPA, 1990. Samplers Guide to the Contract Laboratory Program
'One per cooler
Sample Analysis
6/93
-------
NOTES
QA/QC SAMPLES
Sample type
Matrix spike-
liquids
Matrix spike-
solids
Quantity
Organics: Triple volume for 1
sample per 20 samples'
Inorganics:
Double volume for 1
sample per 20 samples'
Organics and 1 sample per 20
Inorganics: samples
Source: US EPA, 1990. Samplers Quids to the Contract Laboratory Program
SAMPLE CONTAINERS
Volatiles
Semivolatiles
Pesticides and PCBs
Metals
Cyanide
HOLDING TIME
The maximum amount of time that samples may
be held before analysis and still be considered
valid
Starts when the sample is collected in the field
6/93
Sample Analysis
-------
SAMPLE ANALYSIS
To understand the Superfund program and its role in cleaning up abandoned waste sites, some of the
major environmental laws and regulations affecting these cleanups must be understood. These pieces
of legislation introduce several compound lists that dictate a variety of sampling and analytical
requirements, such as levels of analysis, media to be sampled, and type of sample container. It is
important to recognize what compound list is associated with each of the laws or regulations to
properly collect samples at a cleanup site.
Priority Pollutant List
The federal Water Pollution Control Act of 1972 was designed to keep intact the integrity of the
nation's surface waters, either by maintaining their physical, chemical, and biological parameters or
by restoring them and providing proper maintenance. In 1977, the act was amended by and became
known as the Clean Water Act (CWA). The CWA is regulated by 40 CFR (Code of Federal
Regulations) Part 122. This part of the CFR is the National Pollutant Discharge Elimination System
(NPDES). NPDES states that a permit must be obtained prior to discharge of any "pollutants" from
any "point source" into "waters of the United States" (40 CFR Part 122. Ib). Before an NPDES
permit will be issued, several analyses of the wastestream are required. These analyses are listed
in the Priority Pollutant List. This list, which was derived from an initial list of 65 compounds,
includes those constituents that were believed to be the most toxic and the most frequently discharged
to wastestreams by industries.
Appendix IX of 40 CFR Part 264
Another important piece of legislation that affects sampling requirements is the Resource
Conservation and Recovery Act of 1976 (RCRA). The intent of RCRA is to minimize hazardous
waste (as defined in 40 CFR Part 261.3) to protect the public and the environment. There are many
amendments associated with RCRA, but the regulations found in 40 CFR Parts 264 and 270 are most
relevant to sampling. Appendix IX of 40 CFR Part 264 (also known as the Groundwater
Monitoring List) contains 230 constituents that must be monitored as part of a groundwater
compliance program before a RCRA permit will be issued (40 CFR Part 270Hazardous Waste
Permit Programs).
Target Compound List
A third relevant piece of legislation is the Comprehensive Environmental Response, Compensation
and Liability Act of 1980 (CERCLA), which has been most recently amended by the Superfund
Amendments and Reauthorization Act of 1986 (SARA). These acts cover the cleanup of abandoned
hazardous waste sites for which the U.S. Environmental Protection Agency's Contract Laboratory
Program (CLP) offers analytical services of known quality to provide legally defensible results for
use in enforcement actions. CLP laboratories follow the Target Compound List (TCL), which
contains 147 constituents, when performing analyses for cleanups at hazardous waste sites. The TCL
is provided on the following pages. Following the TCL is Table 1, which presents a comparison
of the constituents found on the TCL with those found on the Priority Pollutant List.
6/93 11 Sample Analysis
-------
TARGET COMPOUND LIST
Volatile Compounds
Acetone
Benzene
Bromodichloromethane
Bromoform
Bromomethane
2-Butanone
Carbon disulfide
Carbon Tetrachloride
Chlorobenzene
Chloroethane
Chloroform
Chloromethane
Dibromochloromethane
1,1-Dichloroethane
1,2-Dichloroethene(Total)
1,1-Dichloroethene
1,2-Dichloroethane
1,2-Dichloropropane
cis-1,3-Dichloropropene
trans-1,3-Dichloropropene
Ethylbenzene
2-Hexanone
Methylene Chloride
4-Methy 1-2-pentanone
Styrene
1,1,2,2-Tetrachloroethane
Tetrachloroethene
Toluene
1,1,1 -Trichloroethane
1,1,2-Trichloroethane
Trichloroethene
Vinyl acetate
Vinyl chloride
Xylene (Total)
BTEX
Benzene
Toluene
Ethylbenzene
Xylene (Total)
Sample Analysis
12
6/93
-------
TARGET COMPOUND LIST CONTINUED
Semi-Volatile Compounds
Base/Neutral Extractables
Bis(2-chloroethyl)ether
1,3-Dichlorobenzene
1,4-Dichlorobenzene
1,2-Dichlorobenzene
Bis(2-chloroisopropyl)ether
N-Nitroso-di-n-propylamine
Hexachloroethane
Nitrobenzene
Isophorone
Bis(2-chloroethoxy)methane
1,2,4-Trichlorobenzene
Naphthalene
Hexachlorobutadiene
2-Chloronaphthalene
Dimethylphthalate
Acenaphthylene
2,6-Dinitrotoluene
Acenaphthene
2,4-Dinitrotoluene
Diethylphthalate
4-Chlorophenyl-phenylether
Fluorene
4-Bromophenyl-phenylether
Hexachlorobenzene
Phenanthrene
Anthracene
Di-n-butylphthalate
Fluoranthene
Pyrene
3-3'-Dichlorobenzidine
Benzo(a)anthracene
Chrysene
Bis(2-Ethylhexyl)phthalate
Di-n-octylphthalate
Benzo(b)fluoranthene
Benzo(k)fluoranthene
Benzo(a)pyrene
Indeno( 1,2,3-cd)pyrene
Dibenz(a,h)anthracene
Benzo(g ,h, i)pery lene
Hexachlorocyclopentadiene
N-Nitrosodiphenylamine
Butylbenzylphthalate
4-Chloroaniline
2-Methylnaphthalene
2-Nitroaniline
3-Nitroaniline
Dibenzofuran
4-Nitroaniline
Acid Extractables
Phenol
2-Chlorophenol
2-Nitrophenol
2,4-Dimethylphenol
2,4-Dichlorophenol
4-Chloro-3-methylphenol
2,4,6-Trichlorophenol
2,4-Dinitrophenol
4-Nitrophenol
4,6-Dinitro-2-methylphenol
Pentachlorophenol
Benzyl alcohol
2-Methylphenol
4-Methylphenol
Benzoic Acid
2,4,5-Trichlorophenol
6/93
13
Sample Analysis
-------
TARGET COMPOUND LIST CONTINUED
Pesticides and PCBs
Aldrin
alpha-BHC
beta-BHC
gamma-BHC (Lindane)
delta-BHC
alpha-Chlordane
gamma-Chlordane
4,4-DDT
4,4-DDE
4,4-DDD
Dieldrin
Endosulfan
Endosulfan II
Endosulfan sulfate
Endrin
Endrin ketone
Heptachlor
Heptachlor epoxide
Methoxychlor
PCB-1016
PCB-1221
PCB-1232
PCB-1242
PCB-1248
PCB-1254
PCB-1260
Toxaphene
Inorganic Target Analyte List (TAL)
Metals
Aluminum
Antimony
Arsenic
Barium
Beryllium
Cadmium
Calcium
Chromium
Cobolt
Copper
Iron
Lead
Magnesium
Manganese
Mercury
Nickel
Potassium
Selenium
Silver
Sodium
Thallium
Vanadium
Zinc
Cyanide
Reference: "USEPA Contract Laboratory Program Statement of Work for Organic and
Inorganic Analysis" (refer to the most current publication).
Sample Analysis
14
6/93
-------
TABLE 1: Priority Pollutant and Superfund
Comparison Lists
Chemical Name
Priority Pollutant
Target Compound
List
ORGANICS:
Acenaphthene
Acenaphthylene
Acetone
Acrolein
Acrylonitrile
Aldrin
Anthracene
Aroclor 1016
Aroclor 1221
Aroclor 1232
Aroclor 1242
Aroclor 1248
Aroclor 1254
Aroclor 1260
Benzene
Benzidine
Benz(a)anthracene
Benzo(b)fluoranthene
Benzo(k)fluoranthene
Benzole acid
Benzo(ghi)perylene
Benzo(a)pyrene
Benzyl alcohol
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
6/93
15
Sample Analysis
-------
TABLE 1: Comparison Lists (Cont'd)
Chemical Name
alpha-BHC
beta-BHC
delta-BHC
gamma-BHC
Bis(2-chloroethoxy)methane
Bis(2-chloroethyl)ether
Bis(2-chloroisopropyl)ether
Bis(2-ethylhexyl)phthalate
Bromodichloromethane
Bromomethane
4-Bromopheny 1-pheny lether
Butylbenzylphthalate
Carbon disulfide
Carbon tetrachloride
*Chlordane
4-Chloroaniline
Chlorobenzene
p-Chloro-m-cresol
Chlorodibromomethane
Chloroethane
2-Chloroethyl-vinylether
Chloroform
Chloromethane
2-Chloronaphthalene
Priority Pollutant
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
Target Compound
List
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
Sample Analysis
16
6/93
-------
TABLE 1: Comparison Lists (Cont'd)
Chemical Name
2-Chlorophenol
4-Chlorophenyl-phenylether
Chrysene
2-Methylphenol
4-Methylphenol
4,4'-DDD
4,4'-DDE
4,4'-DDT
Dibenzo(a,h)anthracene
Dibenzofuran
Di-n-butylphthalate
1 ,3-Dichlorobenzene
1 ,2-Dichlorobenzene
1 ,4-Dichlorobenzene
3,3'-Dichlorobenzidine
1,1-Dichloroethane
1 ,2-Dichloroethane
1,1-Dichloroethene
1 ,2-Dichloroethene(Total)
Dichloromethane
2 ,4-Dichlorophenol
1 ,2-DichIoropropane
cis-1 ,3-Dichloropropene
trans-1 ,3-Dichloropropene
Priority Pollutant
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
Target Compound
List
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
6/93
17
Sample Analysis
-------
TABLE 1: Comparison Lists (Cont'd)
Chemical Name
Dieldrin
Diethylphthalate
2,4-Dimethylphenol
Dimethlyphthalate
4,6-Dinitro-o-cresol
2,4-Dinitrophenol
2 ,4-Dinitrotoluene
2,6-Dinitrotoluene
Di-n-octylphthalate
1 ,2-Diphenylhydrazine
Di-n-propylnitrosamine
Endosulfan sulfate
Endosulfan I (alpha)
Endosulfan II (beta)
Endrin
Endrin aldehyde
Endrin ketone
Ethyl benzene
Fluoranthene
Fluorene
Heptachlor
Heptachlor epoxide
Hexachlorobenzene
Hexachlorobutadiene
Priority Pollutant
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
Target Compound
List
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
Sample Analysis
18
6/93
-------
TABLE 1: Comparison Lists (Cont'd)
Chemical Name
Hexachlorocyclopentadiene
Hexachloroethane
2-Hexanone
Indeno(l ,2 ,3-cd)pyrene
Isophorone
Methoxychlor
2-Butanone (MEK)
2-Methylnaphthalene
4-Methyl-2-pentanone
Naphthalene
3-Nitroaniline
2-Nitroaniline
4-Nitroaniline
Nitrobenzene
2-Nitrophenol
4-Nitrophenol
N-nitrosodimethylamine
N-nitrosodiphenylamine
Pentachlorophenol
Phenanthrene
Phenol
Pyrene
Styrene
2,3,7,8-Tetrachlorodibenzo-p-dioxin
Priority Pollutant
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
Target Compound
List
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
6/93
19
Sample Analysis
-------
TABLE 1: Comparison Lists (Cont'd)
Chemical Name
1 , 1 ,2,2,-Tetrachloroethane
Tetrachloroethene
Toluene
Toxaphene
Bromoform
1 ,2,4-Trichlorobenzene
1,1,1 -Trichloroethane
1,1,2-Trichloroethane
Trichloroethene
2,4,5-Trichlorophenol
2,4,6-Trichlorophenol
Vinyl acetate
Vinyl chloride
Xylenes (Total)
Priority Pollutant
X
X
X
X
X
X
X
X
X
X
X
Target Compound
List
X
X
X
X
X
X
X
X
X
X
X
X
X
X
METALS:
Aluminum
Antimony
Arsenic
Barium
Beryllium
Cadmium
Calcium
Chromium
Cobalt
X
X
X
X
X
X
X
X
X
X
X
X
X
X
Sample Analysis
20
6/93
-------
TABLE 1: Comparison Lists (Cont'd)
Chemical Name
Copper
Iron
Lead
Magnesium
Manganese
Mercury
Nickel
Potassium
Selenium
Silver
Sodium
Thallium
Vanadium
Zinc
Cyanide
Priority Pollutant
X
X
X
X
X
X
X
X
X
Target Compound
List
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
*Priority Pollutant List = Technical chlordane
Target Compound List = alpha and gamma chlordane
Source: Priority Pollutant List =
Target Compound List =
40 CFR Part 122, App. D
"US EPA Contract Laboratory Program Statement of
Work for Organic and Inorganic Analysis" (refer to
the most current publication).
6/93
21
Sample Analysis
-------
SAMPLE COLLECTION REQUIREMENTS
Sample collection methods are dictated by the analysis required for each sample. Therefore, it is
important to consider the analytical test or tests that a sample will undergo before actual sample
collection begins. To maintain the integrity of the sample, the sample type, type of container,
preservation method, and holding time must be considered before sampling begins.
Table 2 can be used as a guide for sample collection for compounds and/or analytes found on the
TCL. For example, to collect a liquid sample for a metals analysis, a 1-L polyethylene container
with a polyethylene-lined cap is the recommended container. Nitric acid should be added to the
sample until it has reached a pH < 2. The preservative helps to keep the analytes that may be in the
sample in solution. As shown in Table 2, the holding time for the metals sample is 6 months. The
holding time is a specific time frame that is set from the time of sample collection to the time of
completion of the laboratory analysis. If the holding time is exceeded, the sample analysis is not
valid. If a particular sample will be analyzed for more than one test, it must be collected in the
appropriate container, preserved properly, and analyzed within its holding time to be considered
complete.
Table 3 lists the sample types, types of containers, preservatives, and holding times for a variety of
tests other than those recommended on the TCL.
Sample Analysis 22 6/93
-------
TABLE 2: REQUIRED CONTAINERS, PRESERVATION TECHNIQUES
AND HOLDING TIMES
NAME
ORGANIC TESTS:
Purgeable halocarbons
Purgeable aromatic hydrocarbons
Acrolein and acrylonitrile
Phenols
Benzidines
Phthalate esters
Nitrosamines
PCB's, acrylonitrile
Nitroaromatics and isophorone
Polynuclear aromatic hydrocarbons
Haloethers
Chlorinated hydrocarbons
TCDD
Total organic halogens
PESTICIDES TESTS:
Pesticides
RADIOLOGICAL TESTS:
Alpha, beta and radium
CONTAINER*
G, Teflon-lined septum
G, Teflon-lined septum
G, Teflon-lined septum
G, Teflon-lined cap
G, Teflon-lined cap
G, Teflon-lined cap
G, Teflon-lined cap
G, Teflon-lined cap
G, Teflon-lined cap
G, Teflon-lined cap
G, Teflon-lined cap
G, Teflon-lined cap
G, Teflon-lined cap
G, Teflon-lined cap
G, Teflon-lined cap
-P, G
PRESERVATION
Cool, 4ฐC, 0.008% sodium
thiosulfate
Cool, 4ฐC, 0.008% sodium
thiosulfate, HC1 to pH2
Cool, 4ฐ C, 0.008%
sodium thiosulfate, adjust
pH to 4-5
Cool, 4ฐC, 0.008% sodium
thiosulfate
Cool, 4ฐC, 0.008% sodium
thiosulfate
Cool, 4ฐC
Cool, 4ฐC, store in dark,
0.008% sodium thiosulfate
Cool, 4ฐC
Cool, 4ฐC, 0.008% sodium
thiosulfate, store in dark
Cool, 4ฐC, 0.008% sodium
thiosulfate, store in dark
Cool, 4ฐC, 0.008% sodium
thiosulfate
Cool, 4ฐC
Cool, 4ฐC, 0.008% sodium
thiosulfate
Cool, 4ฐC, sulfuric acid to
pH <2
Cool, 4ฐC, pH 5-9
Nitric acid to pH <2
HOLDING TIME
14 days
14 days
14 days
7 days until extraction
40 days after extraction
7 days until extraction
40 days after extraction
7 days until extraction
40 days after extraction
7 days until extraction
40 days after extraction
7days until extraction
40 days after extraction
7 days until extraction
40 days after extraction
7 days until extraction
40 days after extraction
7 days until extraction
40 days after extraction
7 days until extraction
40 days after extraction
7 days until extraction
40 days after extraction
7 days
7 days until extraction
40 days after extraction
6 months
6/93
23
Sample Analysis
-------
TABLE 2: REQUIRED CONTAINERS, PRESERVATION TECHNIQUES
AND HOLDING TIMES (Cont'd)
NAME
BACTERIAL TESTS:
Coliform, fecal and total
Fecal streptococci
INORGANIC TESTS:
Chloride
Cyanide, total and amenable to
chlorination
Hydrogen ion (pH)
Acidity and alkalinity
Ammonia
Biochemical oxygen demand
Bromide
Biochemical oxygen demand,
carbonaceous
Chemical oxygen demand
Chlorine, total residual
Color
Fluoride
Hardness
Kjeldahl and organic nitrogen
METALS:
Oxygen, dissolved probe
Chromium VI
Mercury
Metals, except chromium VI and
mercury
Nitrate
Sulfate
Sulfide
Nitrate-nitrite
CONTAINER*
P.G
P, G
P, G
P, G
P, G
P, G
P, G
P, G
P, G
P, G
P, G
P, G
P
P, G
P, G
G bottle and top
P, G
P, G
P, G
P, G
P, G
P, G
P, G
PRESERVATION
Cool, 4ฐC, 0.008% sodium
thiosulfate
None required
Cool, 4ฐC, sodium hydroxide to
pH > 12, 0.6g ascorbic acid
None required
Cool, 4ฐC
Cool, 4ฐC, sulfuric acid to
pH <2
Cool, 4ฐC
None required
Cool, 4ฐC
Cool, 4ฐC. sulfuric acid to
pH <2
None required
Cool, 4ฐC
None required
Nitric acid to pH <2, sulfuric
acid to pH <2
Cool, 4ฐC, sulfuric acid to
pH < 2
None required
Cool, 4ฐC
Nitric acid to pH < 2
Nitric acid to pH <2
Cool, 4ฐC
Cool, 4ฐC
Cool, 4ฐC, add zinc acetate plus
sodium hydroxide to pH >9
Cool, 4ฐC, sulfuric acid to
pH <2
HOLDING TIME
6 hours
28 days
14 days
Analyze immediately
14 days
28 days
48 hours
28 days
48 hours
28 days
Analyze immediately
48 hours
28 days
6 months
28 days
Analyze immediately
24 hours
28 days
6 months
48 hours
28 days
7 days
28 days
Sample Analysis
24
6/93
-------
TABLE 2: REQUIRED CONTAINERS, PRESERVATION TECHNIQUES TIMES
AND HOLDING TIMES (Cont'd)
NAME
METALS(cont'd):
Nitrate
Oil and grease
Organic carbon
Orthophosphate
Winkler
Phenols
Phosphorus (elemental)
Phosphorus, total
Residue, total
Residue, Filterable
Residue, Nonfilterable (TSS)
Residue, Settleable
Residue, Volatile
Silica
Specific conductance
Sulfite
Surfactants
Temperature
Turbidity
*G-Glass or P-Polyethylene
CONTAINER*
P, G
G
P, G
P, G
do
G only
G
P, G
P, G
P, G
P, G
P, G
P, G
P
P, G
P, G
P, G
P, G
P, G
PRESERVATION
Cool, 4ฐC
Cool, 4ฐC, sulfuric acid to
pH <2
Cool, 4ฐC, HC1 or sulfuric acid
to pH <2
Filter immediately, cool, 4ฐC
Fix on site and store in dark
Cool, 4ฐC, sulfuric acid to
pH <2
Cool, 4ฐC
Cool, 4ฐC, sulfuric acid to
pH <2
Cool, 4ฐC
Cool, 4ฐC
Cool, 4ฐC
Cool, 4ฐC
Cool, 4ฐC
Cool, 4ฐC
Cool, 4ฐC
None required
Cool, 4ฐC
None required
Cool, 4ฐC
HOLDING TIME
48 hours
28 days
28 days
48 hours
8 hours
28 days
48 hours
28 days
7 days
7 days
7 days
48 hours
7 days
28 days
28 days
Analyze immediately
48 hours
Analyze immediately
48 hours
Reference: US EPA, November 1986, SW-846, Third Edition, Volume 1A
6/93
25
Sample Analysis
-------
ADDITIONAL SOURCES OF INFORMATION
NUS. 1987. Analytical Laboratory Guidebook for Environmental Professionals. NUS Corporation,
Pittsburgh, Pennsylvania.
CFR. 1991. Code of Federal Regulations, Title 40, Parts 190 to 299, Protection of the
Environment. July 1991.
CFR. 1991. Code of Federal Regulations, Title 40, Parts 300 to 399, Protection of the
Environment. July 1991.
U.S. EPA. 1987. Data Quality Objectives for Remedial Response Activities: Development
Process. EPA/540/G-87/003. U.S. Environmental Protection Agency, Washington, DC. March
1987.
U.S. EPA. 1990. Samplers Guide to the Contract Laboratory Program. EPA/540/P-90/006. U.S.
Environmental Protection Agency, Washington, DC. December 1990.
/
U.S. EPA. 1986. Test Methods for Evaluating Solid Waste (SW-846). Third Edition, Volumes
1A and IB. U.S. Environmental Protection Agency, Washington, DC. November 1986.
U.S. EPA. Statement of Work for Organic and Inorganic Analysis. U.S. Environmental Protection
Agency, Washington, DC. (Refer to the most current edition.)
U.S. EPA. 1988. User's Guide to the Contract Laboratory Program. EPA/540/8-89/012. U.S.
Environmental Protection Agency, Washington, DC.
Sample Analysis 26 6/93
-------
CONTAINERIZED MATERIAL
SAMPLING
PERFORMANCE OBJECTIVES
At the end of this lesson, participants will be able to:
Describe the characteristics of samples from containers
List the different types of containers likely to be encountered
Describe the various techniques for accessing containers
Describe appropriate techniques and devices for sampling
containerized materials
-------
CONTAINERIZED
MATERIAL SAMPLING
OSHA REGULATIONS
29 CFR Part 1910.120 (j) and Part 1926
General requirements and standards
for storing, containing, and handling
chemicals and containers
CHARACTERISTICS
High concentrations and hazards
Large quantities
Multiphase layers/sludge
Containers under pressure
NOTES
6/93
Containerized Material Sampling
-------
NOTES
CONTAINER TYPES
TRUCKS
Pressurized or nonpressurized
Multicompartmented
Placards/symbols for identification
TANKS
Horizontal or vertical
Underground vs. aboveground
Safety
- Structural integrity
- Slip, trip, and fall
Containerized Material Sampling
6/93
-------
NOTES
DRUMS
Labels
Drum construction
Exotic materials
- Aluminum
- Nickel
- Stainless steel
POLY DRUMS AND CARBOYS
Contents - strong acids or bases
Hazards
Configuration of drumhead
* Signs of deterioration (e.g., leaks)
ACCESSING
CONTAINERS
6/93
Containerized Material Sampling
-------
NOTES
GAINING ACCESS PRIOR TO
SAMPLING CONTAINERS
Special equipment may be needed
- Cherry picker
- Safety lines
- Bolt cutters
- Air monitoring devices
ACCESS MAY NOT BE THROUGH
NORMAL OPENINGS
Existing holes in containers
Plasma arc
PREPARATION NEEDED BEFORE
SAMPLING
Number containers
Obtain information from labels
Secure containers on flat surface before
attempting to gain access
Containerized Material Sampling
6/93
-------
NOTES
OPENING CONTAINERS
MANUAL DRUM OPENING
Bung wrench
Drum deheader
Manual spiking
Bolt cutters
DRUM SAMPLING
Under OSHA 1910.120, manual drum
opening cannot be used if contents are:
Unknown
Flammable
Reactive or explosive
Shock sensitive
6/93
Containerized Material Sampling
-------
NOTES
BUNG WRENCH
Nonsparking alloy
- Bronze
- Beryllium
- Aluminum
Safety techniques
DRUM DEHEADER
Not intrinsically safe
Forged steel with an alloy steel blade
Scissor-like cutting action
Closed head drums only
Industrial settings
MANUAL SPIKING
Hand pick, pickax, and hand spike
Nonsparking material
Sharpened point that can penetrate
drum lid
Containerized Material Sampling
6/93
-------
NOTES
SAFETY
A remote opening device should be used
on drums that are bulging or swelling
DO NOT use a manual method!
REMOTE DRUM OPENING
Pneumatic bung remover
Pneumatic drill
Hydraulic drum piercer
Backhoe spike
Robot units
PNEUMATIC BUNG
REMOVER/DRILL
Adequate distance
Nonsparking equipment
Do not use on sample containers
or lab packs
Decontaminate after each use
Different types of fittings
6/93
Containerized Material Sampling
-------
NOTES
HYDRAULIC DRUM PIERCER
Nonsparking tip
Side or top mount
Consider secondary containment with
side mount
BACKHOE
(with spike attachment)
Advantages
- Distance
- Minimal personnel contact
Disadvantages
- Cross contamination
- Access
- Toxic vapor cloud
GAINING ACCESS PRIOR TO
SAMPLING DRUMS
Use caution when working below grade
or high above ground
Use drum grapplers to stage drums in
rows for easy access
Containerized Material Sampling
6/93
-------
NOTES
GUIDELINES FOR STAGING
AREAS
Allow 2 feet between rows
Place two drums per row
Establish separate areas for
drum opening and sampling
Stage by compatibility groups
BULKING
Containers with small quantities
of compatible materials are mixed
together before sampling
HAZARD CATEGORIZATION
(HAZCAT)
Screening tool
Cost-effective
User friendly
Can be used to identify hazard class
for shipping
6/93
Containerized Material Sampling
-------
NOTES
PRIOR TO SAMPLING
Inventory
Stage
Check container integrity (use secondary
containment if necessary)
Open using proper techniques
SAMPLE COLLECTION
DRUM SAMPLING
Look for signs that drum is under
pressure or is shock sensitive
Monitor headspace gases
- Combustible gas indicators (CGIs)
- Radiation detection instruments
- Organic vapor analyzers (OVAs)
Containerized Material Sampling
10
6/93
-------
NOTES
DRUM SAMPLING
EQUIPMENT
GLASS THIEF SAMPLER
6 mm to 16 mm in diameter
48 inches long
Do not break and leave in drum
COLIWASA
(Composite Liquid WAste SAmpler)
4 cm in diameter
152 cm long
Insert tube with neoprene stopper,
Teflonฎ flange, or glass ball at
end-sealing mechanism
6/93
11
Containerized Material Sampling
-------
NOTES
PUSH TUBES
Use for sludge-like materials
Remove plug easily with stainless steel
spoon
SUMMARY
Use proper drum opening techniques
and equipment
Use proper levels of protection
Use caution
TANK SAMPLING
Conduct air monitoring of headspace
with CGI
- If LEL >25%, discontinue sampling
Can use a bailer, glass thief, sludge
judge, bacon bomb, COLIWASA, or
subsurface grab sampler
Containerized Material Sampling
12
6/93
-------
NOTES
TANK SAMPLING
EQUIPMENT
SLUDGEJUDGE
3/4-inch plastic pipe in 5-foot sections
marked in 1-foot increments
Check valve on bottom
BACON BOMB
Cylindrical body made of brass,
bronze, and stainless steel with
an internal tapered plunger that
acts as a valve to admit the sample
6/93
13
Containerized Material Sampling
-------
NOTES
PROBLEMS
SAFETY
Slip, trip, and fall
Buddy system
Safety lines
Shoring of excavation areas
SAFETY
Stacked containers
Overhead hazards
Product-escaping containers
Chip, wipe, and sweep sampling
procedures may be used in these
situations
Containerized Material Sampling
14
6/93
-------
NOTES
LAB PACKS
Do not sample individual containers
Use remote crushing technique
REMINDERS
After sampling is complete, seal or close
container to preserve integrity of the
contents
Follow proper sampling procedures and
techniques to ensure quality results
6/93
15
Containerized Material Sampling
-------
HAZARD CATEGORIZATION (HAZCAT)
Stockpiled drums at a hazardous waste site pose problems in cleanup and disposal. Laboratory
analysis of each individual drum can be costly and time consuming. Combining wastes from drums,
tanks, ponds, and lab packs is more economical and efficient. However, wastes must first be
sampled and tested for compatibility. Compatibility testing is a set of simple chemical tests such as
pH, solubility, and flammability. Test results from field categorization can also be used to help
satisfy RCRA hazardous waste characteristic definitions and will provide some data for use in
defining DOT hazard classes for shipping. Hazard field categorization is not as extensive as
laboratory analysis and not as costly; it is used only as a screening mechanism. There are limitations
to each one of the different screening tests. Field HAZCAT procedures should not be substituted
for standard laboratory analysis (see the Compatibility Testing flow diagrams of the HAZCAT
procedures on the following pages). When using the diagrams, follow the steps sequentially.
EPA-ERT has standard operating procedures for using the HAZCAT procedures during field
investigations.
6/93 17 Containerized Material Sampling
-------
Flow Diagram 1: CMA COMPATIBILITY TESTING PROTOCOL
Test for Radioactivity
Isolate Gas Cylinders
Isolate Suspected Explosives
Liquids
Open Drum
Test (or Radioactivity
Confirm Liquid
Test for Peroxides
and Oxidizers
Test for Water
Reactivity
No
Test for Water
Solubility
Yes
Test for Water
Content
See
Water Soluble
Liquids
Yes
ป Isolate
Determine Contents
of Containers
Isolate Oddball Drums
Isolate Lab Packs
Solids
Open Drum
Yes
Isolate
Yes
Test for Radioactivity
To Solids To Liquids
No
Regroup
Yes
Isolate
Isolate
No
Yes
Confirm Solid
Yes
Remove Free Liquid
Test for EP Toxicity
and PCBs
NoPCB
No
See
Water Insoluble
Liquids
Source: Drum Handling Practices at Hazardous Waste Sites. (EPA/600/2-86/013).
Containerized Material Sampling
18
6/93
-------
Flow Diagram 2: CMA COMPATIBILITY TESTING PROTOCOL
Water Insoluble Liquids Testing
Test for
Organic Halogen
Test for PCB
on Composite
Test for PCB
on Composite
High
Halogen
No PCB
Composite
Low
Halogen
No PCB
Composite
High
Halogen
Low PCB
Composite
Mixed
Halogen
Middle PCB
Composite
Mixed
Halogen
High PCB
Composite
Low
Halogen
No PCB
Composite
Source: Drum Handling Practices at Hazardous Waste Sites. (EPA/600/2-86/013).
6/93
19
Containerized Material Sampling
-------
Flow Diagram 3: CMA COMPATIBILITY TESTING PROTOCOL
Water Soluble Scan
No
Isolate
Strong
Acids
pH<2
Weak
Acids
pH2-7
Isolate
Yes
Neutralize (optional)
Weak
Bases
Strong
Bases
pH7-12 pH>12
Cyanide. Sulfide
No
Neytralizejopjional)
No
No
Isolate
Source: Drum Handling Practices at Hazardous Waste Sites. (EPA/600/2-86/013).
Containerized Material Sampling
20
6/93
-------
SOIL SAMPLING
PERFORMANCE OBJECTIVES
At the end of this lesson, participants will be able to:
Describe the objectives of a soil sampling event
Describe the basic methods of soil sampling
List examples of various soil sampling equipment
Describe the use of the lysimeter
List several methods of data presentation
-------
NOTES
SOIL SAMPLING
WHY SAMPLE THE SOIL?
Chemical characterization
Migration pathways
Soil/geologic characteristics
CHEMICAL CHARACTERIZATION
Contaminant identification
Spatial distribution
Levels of contamination
6/93
Soil Sampling
-------
NOTES
MIGRATION PATHWAYS AND
TRANSPORT MECHANISMS
Man-made pathways
Surface drainage
Vadose zone transport
Wind dispersion
Human and animal activity
SOIL/GEOLOGIC
CHARACTERISTICS
Soil classification
Organic content
Adsorptive characteristics
Transport characteristics
RELATIONSHIP OF VADOSE AND
SATURATED ZONES
Vadose zone
(unsaturated)
Saturated zone
Soil moisture
Partial saturation
Capillary fringe
Groundwater
. Water table
Soil Sampling
6/93
-------
NOTES
SURFACE SAMPLING
Depth
Tools
SUBSURFACE SAMPLING
Power auger
Hollow-stem auger
Rotosonic drill
SAMPLING DEVICES
Split spoon
Shelby tube
Core barrel
6/93
Soil Sampling
-------
NOTES
ALTERNATIVE SAMPLING
TECHNIQUES
Backhoe/trenching
Geoprobeฎ
Cone penetrometer
LYSIMETER
A device for sampling interstitial
moisture in the unsaturated zone
DATA PRESENTATION
Geologic graphics
Data posting
Contour plotting
Soil Sampling
6/93
-------
6/93
Soil Sampling
-------
SURFACE WATER AND
SEDIMENT SAMPLING
PERFORMANCE OBJECTIVES
At the end of this lesson, participants will be able to:
Describe basic stream morphology as it affects the location
of sampling points
Describe lake morphology as it affects the location of
sampling points
Describe and select equipment for obtaining representative
samples from surface water and sediment
Define the basic factors governing the fate of hazardous
materials in the water column and sediment
-------
SURFACE WATER AND
SEDIMENT SAMPLING
NOTES
6/93 1 Surface Water and Sediment Sampling
-------
SURFACE WATER MORPHOLOGY
Lakes and Streams
Flow
NOTES
Surface Water and Sediment Sampling
6/93
-------
FLOW DETERMINATION
Stream Channel
TTTTP; i ' 1 I 1 I
i i i ,, i i i
-1-4
I I
I , I
fH-+
1 2
5J6|7|8|9J10|
L I I , I
current
meter
Q = E Velocity x Area (Section)
0.6 Depth
V mean
10
NOTES
6/93
Surface Water and Sediment Sampling
-------
STREAM CHANNEL FLOW
(0.86 max)
Outline of 0.99V max
ggg&m Stream boundary
K.SXNI Turbulence
NOTES
Surface Water and Sediment Sampling
6/93
-------
IN-STREAM FLOW
Channel Flow Characteristics
Flow
Right Bend
Turbulent flow
Stream water
Sediment
Underlying strata
Water sample site
NOTES
6/93
Surface Water and Sediment Sampling
-------
GRAB VS. COMPOSITE SAMPLING
Flow
Individual Grabs
Composited Grabs
NOTES
Surface Water and Sediment Sampling
6/93
-------
LAKE STRATIFICATION
Depth
Depth
Te'mper'aturefCJ/b.t).
Winter
D.O:
Temperature (C)/D.O.
NOTES
6/93
Surface Water and Sediment Sampling
-------
RANDOM SAMPLING
Standing Water
4
5
6
7
Square
4-4
NOTES
Surface Water and Sediment Sampling
6/93
-------
SURFACE WATER
SAMPLING EQUIPMENT
NOTES
Surface Water and Sediment Sampling 9 6/93
-------
WATER QUALITY PARAMETERS
Surface Water
Temperature
pH
Dissolved oxygen
Oxidation/reduction potential
Conductivity
NOTES
Surface Water and Sediment Sampling 10 6/93
-------
STREAM CHANNEL MIGRATION
Alluvium
Bedrock
NOTES
6/93
Surface Water and Sediment Sampling
-------
STREAM MORPHOLOGY
Riffle-Pool Relationship
Riffle
Flow
Pool
Riffle
\\| Deposited Material
Obstruction
Riffle
Dam
NOTES
Surface Water and Sediment Sampling
12
6/93
-------
LAKE SEDIMENT DISTRIBUTION
Inlet
Inlet
NOTES
6/93
13
Surface Water and Sediment Sampling
-------
SEDIMENT SAMPLING
EQUIPMENT
NOTES
Surface Water and Sediment Sampling 14 6/93
-------
CONTAMINANT TRANSPORT
Contaminant, - Flow
Cone.
Time
NOTES
6/93
15 Surface Water and Sediment Sampling
-------
WHAT AFFECTS DISPERSION?
Characteristics of the Setting
Physical stratification
Currents
Ambient temperature
NOTES
Surface Water and Sediment Sampling 15 6/93
-------
WHAT AFFECTS DISPERSION?
Contaminant Attributes
Solubility
Specific gravity
Viscosity
NOTES
6/93 17 Surface Water and Sediment Sampling
-------
SAMPLING SAFETY
NOTES
Surface Water and Sediment Sampling 18 6/93
-------
SURFACE WATER/SEDIMENT
SAMPLING
Stainless
Steel Bucket
Ponar
Dredge
_, . . ... Sewage Beta
Peristaltic sampler Sampler
Pump K
Shallow/Fast wm
NOTES
6/93
19
Surface Water and Sediment Sampling
-------
SURFACE WATER AND SEDIMENT SAMPLING
INTRODUCTION
The usefulness of sampling in surface waters for evidence of a hazardous material release has been
well documented. Surface waters exist in low-lying areas and function as biological "sinks," which
often may show the first signs of a chemical release. Initial studies included investigations of the
influence of point-source pollution from industrial and municipal facilities on waterways. Many of
these early studies aided in developing the methodology used in hazardous waste site situations.
A surface water sampling study may require establishing several sampling locations to characterize
a particular contaminant or background concentrations. Such site-specific considerations often
include determining physical characteristics of the particular body of water in order to dictate
sampling strategies and proper sampling devices.
SITE SELECTION
Aqueous environments can be divided into two broad categories: freshwater and saltwater. Within
the freshwater category, situations exist where the waster is free flowing (i.e., rivers, streams, and
creeks) or is relatively stationary (i.e., lakes, ponds, and lagoons). There are, however, situations
where a transition exists between the various freshwater environments (e.g., impoundments, flowage)
or between freshwater and saltwater (estuaries). The various characteristics of each of these
situations will influence the approach that will be necessary to obtain samples representative of the
water body or portion of the water body so that contaminant migration can be determined.
The size of the body of water will determine the site selection process, both in determining modes
of personnel transport and types of sampling devices. Large streams and lakes accessible by boat
have the obvious advantage of maneuverability and aid in performing activities at multiple sampling
points. Smaller bodies of water may require wading, which requires personnel to carry all sampling
equipment to and from access locations. Specific considerations exist when sampling from artificial
structures (e.g., bridges, dams, and weirs). The problem of access combined with the number of
sample locations outlined in the study objectives will undoubtedly affect the time and personnel
assigned to this task.
Samples obtained from all aqueous environments can be roughly divided into three categories:
water, sediment, and biological. The latter category requires somewhat separate approaches and
methods particular to each organism. Biological samples are pertinent and necessary in numerous
hazardous waste site settings. They can yield significant information on contaminant transport and
fate. However, this discussion will emphasize water and sediment sampling. Sediment can be
defined as solid material (mineral and organic) situated beneath an aqueous layer. Water contains
organic matter, minerals, nutrients, and ions in varying amounts that are in constant physical contact
with the underlying sediment. This water/sediment interface is an important location of many
complex chemical interactions.
6/93 21 Surface Water and Sediment Sampling
-------
Rivers, Streams, and Creeks
The terms "creek" or "stream" generally refer to the relative size of the body of water. A river is
larger than a stream, which is larger than a creek, and so on. Free-flowing bodies of water,
regardless of size, have several common characteristics. In addition to the obvious function as water
transport in the water cycle, streams serve to transport eroded mineral (e.g., sand, gravel, and rock)
and have a complex biological function whereby organic matter (e.g., leaves, woody material, and
soil) entering the system is used by various organisms, transported, and changed. Diurnal
fluctuations in values such as dissolved oxygen, pH, conductivity, and various concentrations of
many nutrients can vary widely depending on the time of day. The combined effect of physical and
biological activity in moving water can result in longitudinal fluctuations of numerous water quality
values. Dissolved oxygen levels can vary widely depending on whether the samples were taken
upstream or downstream of a dam. These variations dictate that the water quality parameters be
determined and recorded while samples are being collected.
All streams consist of alternating series of riffles (i.e., fast water velocity, shallow depth) and pools
(i.e., slow water velocity, more depth) and will tend to form bends or meander, which is more
pronounced in low gradient areas. The water moving in a given stream, or "in-stream flow"
measurements like velocity, can vary widely in either cross section (lateral flow), along a water
column (vertical flow), or even horizontally. In ordinary streams, water flow is best described as
turbulent or nonuniform in nature. Friction from the underlying substrate and the surface air causes
the maximum velocity within a stream cross section to usually be found in mid-channel just below
the surface. The average or mean velocity usually occurs at six-tenths to eight-tenths of the total
depth below the surface. Average stream flow and total discharge can only be determined by
measuring several intervals along the stream cross section at measured depths at each particular
interval.
Most hazardous waste investigations in running waters involve measuring contaminant concentrations
originating from a source with a small volume release relative to the receiving waters. The sample
station chosen to detect the contaminant may or may not be located downstream to a point of
complete mixing. A tributary or point source will tend to remain near the bank for a considerable
amount of time before adequate horizontal and vertical mixing has taken place. One solution could
be to select multiple sampling sites across the cross section of the stream. Another possible solution
could be to use fluorescent tracer dye data to demonstrate complete mixing. Selecting sample points
just downstream of major features, such as riffles or dams, may prevent sampling of inadequately
mixed surface water. Other suggestions include using multiple sampling points along the stream
length (2-3 stations downstream) and "bracketing" additional tributaries or feature changes with
additional sampling points.
The general rule for the correct number of samples necessary to characterize a stream varies with
stream size. For small streams (<30 feet), a single grab sample taken at mid-channel below the
surface will be adequate to represent the cross section. With larger streams, multiple samples at
various measured depths may be necessary to adequately characterize the cross section. Sediment
samples may be comprised of several grab samples in that cross section, but the various grab samples
will be homogenized prior to placing the aliquot in its respective container. Samples, however,
should be of similar composition or particle size within that composite. Sediment samples obtained
at multiple sites along the stream length should also consist of a comparable substrate. In streams,
it is difficult, if not impossible, to obtain sediment samples of identical consistency because of the
Surface Water and Sediment Sampling 22 6/93
-------
in-stream flow variability and the heterogeneous nature of the parent material. It is possible to find
similar features that decrease water velocity (< 1 ft./sec), which may promote deposition of fine
material. These microhabitats include areas immediately downstream of large obstructions, the
upstream end of riffles, the middle of a slow pool, the insides of bends, and just upstream of dams
or log jams.
Lakes, Impoundments, Ponds, and Lagoons
Standing water has a tendency to stratify during certain times of the year. The density difference
imposed by the energy provided by sunlight creates two distinct layers of water. This stratification
is more pronounced during the summer months where little mixing occurs between the upper and
lower layers. Fall "turnover" occurs when the upper layer is cooled to the point where the
temperature is vertically uniform. Complete mixing occurs rather abruptly where water and the
upper layers of sediment intermix. Temperature stratification can also occur in large rivers. The
exact location of the strata may be found by using a temperature probe to record the temperature at
various depths to obtain a temperature profile. Samples may have to be obtained from various depths
using a discrete "at depth" sampling device.
Lake morphology may have to be characterized to assess sampling needs. Sediment in ponds and
lagoons is usually uniformly distributed with similar consistency so that a single bottom sample in
the deepest area may be considered representative. Impoundments are usually dammed streams that
are deepest near the dam. The finest sediments are usually found in this deep area, and coarser
deposits are found near the headwaters of the reservoir. For large lakes, a transect or grid system
may be developed to organize sample location and various sampling activities. Lakes with irregular
shapes may require that certain bays or coves be considered separately.
Estuarine Waters
Estuaries are areas where freshwater systems meet the saline waters of the ocean. Tidal action and
differences in density of the fresh and salt water are characterized by variable mixing. A
freshwater/saltwater wedge can form which migrates according to the tidal action, or an increase in
salinity can occur with no halocline present. These phenomena can be investigated using boat-
mounted depth soundings in combination with data from a salinometer and a dissolved
oxygen/temperature meter that generates vertical profiles. Samples may need to be obtained from
discrete depths and sediment sampling points may need to be determined in reference to the particular
mixing zone.
Investigations in estuary environments will likely involve a two-stage process during wet and dry
times of the year. As during investigations in large bodies of water with complex physical
characteristics, objectives of studies in estuaries must remain flexible to accommodate changes in
sample location and time.
6/93 23 Surface Water and Sediment Sampling
-------
WATER AND SEDIMENT COLLECTION EQUIPMENT
Specific analytical categories have specific sample container requirements which can limit the type
of sampling device used in collection. Volatile organic analysis (VOA) samples should be collected
in a pair of 40 mL vials which must be immersed in the water sample by slowly tilting and gently
allowing them to fill with as little agitation as possible. Absolutely no air bubbles should remain in
either of the filled VOA containers. Prepreserved sample containers may require the use of a
sampling device other than the container. In locations that are inaccessible, a properly
decontaminated stainless steel or Teflonฎ dip-bucket with dedicated rope should be used. Any
sample device that uses positive or negative pressure is not recommended.
Sampling for oil and grease involves partially filling the sample bottle without having to transfer
water from a sampling device or container that could adsorb the contaminant and thus reduce the
accuracy of analysis.
Certain in-situ water quality parameters can be measured directly, but most analyses will involve
collecting the sample from the selected area and delivering it to an analytical laboratory. Collecting
water for hazardous waste investigations involves obtaining a sample representative of the sample
location. The accuracy of the sample collection is ensured by minimizing any physical and chemical
influence prior to analysis. The scale or size of the body of water will deternine the extent of
sample site selection and appropriate sampling devices.
Small streams and shallow ponds or lagoons may require a single grab sample obtained by immersing
the sample bottle directly into the middle of the water. By facing upstream in running water, the
samples can be obtained without disturbing the bottom sediment. Caution should be exercised when
entering unknown bottom substrate in severely impacted areas because solids may not support the
weight of an individual. Another method is to use a hand-held or pole-mounted scoop which can
allow a sampler to sample from the bank if waters are not wadable or footing is unreliable. A metal
rod can also help when searching the bottom for fine-grained material. Sediment collection on small
streams and ponds usually employs a sample device. Hand scoops of a nonreactive material are
sometimes adequate, although more standardized methods exist using commercially available gravity
corers, augers, and dredges. The top layer of sediment should be included in a bottom sample and
many sampling devices or techniques can disturb this portion, thus reducing the accuracy of the
analysis. The Peterson dredge is a heavy-duty design suited for sand/gravel substrate. The Ponar
dredge is similar in design, but is tailored to travel through the water column with less disturbance
to the underlying material. The Ekman dredge is a spring-loaded device best suited for soft substrate
and is designed to travel through the water and reduce the shock wave which occurs prior to
instrument impact. Depending on the size of the dredge being used, some may require a boat-
mounted mechanical winch. Gravity corers also reduce the shock wave and yield a sample which
may be sampled for a vertical profile. Very soft substrate can be collected using hand-held push
tubes. In some cases, scuba diving may be used to ensure that site selection and sample collection
are properly completed.
Larger bodies of water will require special water sampling equipment capable of sampling at discrete
depths. Submersible pumps and peristaltic pumps can be effective in certain cases. Also, these
pumps are advantageous because they may be manufactured from a variety of nonreactive materials.
Other discrete depth sampling devices will collect a sample volume at various depths. They range
from relatively simple pond sampler devices to more complicated devices such as the Kemmerer,
Surface Water and Sediment Sampling 24 6/93
-------
Bacon Bomb, and LaMotte samplers. These devices use a mechanical messenger that trips the
sampler to close, allowing the sample to be retrieved and transferred to its proper container.
ADDITIONAL INFORMATION SOURCES
Crickmay, C.H. 1974. The Work of the River. American Elsevier Publishing Co., New York.
Gilbert, R.O. 1987. Statistical Methods for Environmental Pollution Monitoring. Van Nostrand
Reinhold Co., New York.
Lind, O.T. 1979. Handbook of Common Methods in Limnology. Second Edition. The C.V.
Mosby Co., St. Louis, Missouri.
U.S. EPA. 1969. A Practical Guide to Water Quality Studies of Streams. PB-196367. National
Technical Information Service, Springfield, Virginia.
U.S. EPA. 1973. Handbook for Monitoring Industrial Wastewater. PB-259146. U.S.
Environmental Protection Agency Technology Transfer, National Technical Information Service,
Springfield, Virginia.
U.S. EPA. 1991. Compendium of ERT Surface Water and Sediment Sampling Procedures.
EPA/540/P91/005. U.S. Environmental Protection Agency, Washington, DC. January 1991.
U.S. EPA. 1991. Standard Operating Procedures and Quality Assurance Manual. U.S.
Environmental Protection Agency, Environmental Services Division, Athens, Georgia.
6/93 25 Surface Water and Sediment Sampling
-------
GROUNDWATER SAMPLING
PERFORMANCE OBJECTIVES
At the end of this lesson, participants will be able to:
Explain the difference between a confined and an unconfmed
aquifer
Describe a properly installed monitoring well
List the proper order of groundwater sample collection
Describe the various groundwater sampling equipment and
sample collection procedures
-------
NOTES
GROUNDWATER MONITORING
BASIC PROPERTIES OF
AQUIFERS
Porosity
Permeability
AQUIFER
A permeable geologic unit with the
ability to" store, transmit, and yield
water in usable quantities
6/93
Groundwater Sampling
-------
NOTES
UNCONFINED AQUIFER
The water is in direct contact with the
atmosphere
There is no upper confining layer
CONFINED AQUIFER
A permeable zone between two
geologic formations of relatively
low permeability
CASING AND SCREEN
MATERIALS
PTFE (Teflonฎ)
Stainless steel
Rigid, threaded PVC
Groundwater Sampling
6/93
-------
MONITORING WELL
CONSTRUCTION
Grout
Bentonite
Sand pack
Well cap
Riser pipe
Screen
A WELL MUST BE PROPERLY:
Designed
Located
Constructed
Secured from tampering
GROUNDWATER SAMPLING
NOTES
6/93
Groundwater Sampling
-------
NOTES
FIELD MEASUREMENTS
Water level
Electrical conductivity
pH
Temperature
WATER LEVEL MEASUREMENT
EQUIPMENT
WELL PURGING
A Compendium of Superfund Field
Operations Methods, 1987
Common procedure: three to five
bore volumes
Reliable method: stability of water
measurements over three well volumes
Groundwater Sampling
6/93
-------
NOTES
WELL VOLUME
Well column x Well radius
(in feet) (in inches)
Well volume
(in gallons)
2
x 0.163
(conversion)
VERIFY PURGING BY
Temperature
pH
Conductivity
COLLECTION ORDER
1 . Volatile organics
2. Extractable organics
- BNAs
- Pesticides/PCBs
3. Total metals
4. Dissolved metals (if applicable)
5. Cyanide
6/93
Groundwater Sampling
-------
NOTES
GROUNDWATER SAMPLING
EQUIPMENT
EQUIPMENT
Fultz pump
Bladder pump
Waterra inertial pump
Bailers
FIELD FILTERING
Used for dissolved inorganics
Not used for
- TOX (total organic halogens)
- TOC (total organic carbon)
- Organic analysis
Groundwater Sampling
6/93
-------
NOTES
ALTERNATIVE SAMPLING
TECHNIQUES
Hydropunchฎ
Geoprobeฎ
Cone penetrometer
6/93
Groundwater Sampling
-------
DOCUMENTATION
PERFORMANCE OBJECTIVES
At the end of this lesson, participants will be able to:
Describe the best practices for field logbook use
Describe the correct methods for field sample identification
Describe the proper methods for photo documentation
Define the proper circumstances of sample custody
-------
NOTES
DOCUMENTATION
SAMPLE DOCUMENTATION
Field Logbooks - provide daily records
of significant events, observations, and
measurements during 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
6/93
Documentation
-------
NOTES
FIELD DOCUMENTATION
Best Practices:
Field records should be direct and
succinct
Documentor should sign and date each
page
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
Description of sample
Description of sampling point
Date and time of sample collection
Documentation
6/93
-------
NOTES
FIELD LOGBOOK ENTRIES
Sample identification number
Field observations
Field measurements
(e.g., pH, flammability)
SAMPLE IDENTIFICATION
All sample containers should be labeled
with eight categories of identifying
information
1. Project code
2. CLP case and sample number
SAMPLE IDENTIFICATION
3. Station location and number
4. Date and time of sample collection
5. Preservative
6/93
Documentation
-------
NOTES
SAMPLE IDENTIFICATION
6. Requested analysis
7. Signature(s)
8. Remarks
SAMPLE DOCUMENTATION
Sample tags and labels
Site maps
Photographs
Chain of custody
Field documentation
SAMPLE CHAIN OF CUSTODY
A reconstruction of who had access
to the sample from the time it was
collected until produced in court
Documentation
6/93
-------
NOTES
SAM RLE CUSTODY
A sample is under 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
VIDEO
6/93
Documentation
-------
DOCUMENTATION
taken from:
EPA/540/P-87/001
(OSWER Directive 9355.0-14)
December 1987
A COMPENDIUM OF SUPERFUND
FIELD OPERATIONS METHODS
(Section 4)
OFFICE OF EMERGENCY AND REMEDIAL RESPONSE
OFFICE OF WASTE PROGRAMS ENFORCEMENT
U.S. ENVIRONMENTAL PROTECTION AGENCY
WASHINGTON, DC 20460
Documentation
-------
SECTION 4
SAMPLE CONTROL, INCLUDING CHAIN OF CUSTODY
4.1 SCOPE AND PURPOSE
This section describes procedures for sample identification and chain of 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 the 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 contractor's employee (see Subsection 1.1).
4.3 APPLICABILITY
When environmental measuring 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 sample control procedures (i.e., field
operations leader). However, each sampler is responsible for the activities described in Subsections 4.5
and 4.6.
4.5 RECORDS
The following records 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 Services (SAS); see Exhibits 5-2, 5-3, and 5-9)
Chain-of-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)
6/93 9 Documentation
-------
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
Oioxin 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 identification 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.
Documentation 10 6/93
-------
The organization's 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 specific 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
project 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 Regional 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 to the CLP 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 lost, 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.
6/93
11 Documentation
------- An error occurred while trying to OCR this image.
-------
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 sampling point by the sampling team leader
and listed in the sampling plan
Date: A six-digit number indicating the year, month, and day of collection
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 placed 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 with 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-
Documentation 14 6/93
------- An error occurred while trying to OCR this image.
-------
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 file. 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's 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 (TR), a four-part carbonless form printed with a unique sample identification number.
One TR 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 TRs.)
To provide a permanent record for each sample collected, the sampler completes the appropriate TR,
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
Documentation 16 6/93
-------
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 individuals relinquishing and receiving 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 facility or agency requests the signature of the receiving party on a
recelpt-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 COC record and receipt-for-samples form should contain a statement that the samples
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 nonhazardous 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 prepaid. Freight bills, postal service receipts, and bills 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) rf 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.
6/93 17 Documentation
-------
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 (QA) 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 COC 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 allow 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 18
-------
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 to-refresh 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, chain-of-custody records, and receipt-for-samples forms are written in waterproof ink.
These accountable serialized documents are not 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 individual 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 initialed and dated.
For all photographs taken, a photographic log is kept; the log records date, time, subject, frame and
roll number, and 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.
6/93
19 Documentation
-------
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 III uses a serialized 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 Region IV
Region IV has a detailed procedural discussion in the Engineering Support Branch Standards Operating
Procedures and Quality Assurance Manual, U.S. EPA, Region IV, Environmental Services Division, 1 April
1986.
4.7.5 Region V
Region V uses a serialized chain-of-custody seal. Region V seals are color coded; orange is used for
REM and FIT work. Seals are placed on the outside of the shipping cooler 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 num-
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 of custody is followed as
described above.
4.7.8 Region VIM
Region VIII 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.
Documentation 20 6/93
-------
4.7.10 Region X
Region X does not use a serially numbered custody seal. Seals are signed, and the sample ID number
is written on the seal.
4.8 INFORMATION SOURCES
SuperfundAmendments andReauthorization Act (SARA). Section 104(m), "Information Gathering Access
Authorities."
U.S. Environmental Protection Agency. NEIC Policies and Procedures. EPA-330/9-78-001-R. May 1978.
(Revised February 1983.)
U.S. Environmental Protection Agency. REM IV Zone Management Plan. Contract No. 68-01-7251,
CH2M HILL and U.S. EPA.
U.S. Environmental Protection Agency. User's Guide to the Contract Laboratory Program. Office of Emer-
gency and Remedial Response. December 1986.
U.S. Environmental Protection Agency. Zone IIREM/FITQuality Assurance Manual. Contract No. 68-
01-6692, CH2M HILL and Hazardous Site Control Division.
21 Documentation
-------
UNITED STATES ENVIRONTMENTAL PROTECTION AGENCY
OFFICE OFENFORCEMENT
EPA-330/9- 78-001-R
NEIC POLICIES AND PROCEDURES
May 1978
[Revised August 1991]
NATIONAL ENFORCEMENT INVESTIGATIONS CENTER
Denver, Colorado
-------
CONTENTS
FOREWORD i
ORGANIZATION CHART m
I. GENERAL POLICIES AND PROCEDURES
CONFLICTS OF INTEREST, GIFTS AND GRATUITIES l
PUBLIC RELATIONS 1
ENTERING FACILITIES 2
Authority 2
Entry Procedures 4
Denial of Entry Procedures 4
INVESTIGATIONS OF ALLEGED CRIMINAL ACTIVITY 5
COMMUNICATIONS EXTERNAL TO OFFICE OF ENFORCEMENT.5
Requesting Information from Persons Subject to Regulation 6
Disclosure of Official Information to the Public 6
FOIA Response Procedures 8
II. PROJECT MANAGEMENT
PROJECT REQUEST 9
PROJECT TEAM FORMATION 11
Civil Investigations 11
Criminal Investigations 12
BACKGROUND INFORMATION REVIEW 12
PROJECT PLAN PREPARATION 13
PROJECT PLAN IMPLEMENTATION 15
REPORT PREPARATION 15
ENFORCEMENT CASE SUPPORT 16
HI. EVIDENCE MANAGEMENT
SAMPLE CONTROL 18
Sample Identification 18
Split Samples 19
Chain-of-Custody for Samples 19
Sample Custody 22
Transfer of Custody and Shipment 22
Laboratory Custody 25
-------
CONTENTS (cont.)
III. KVTDENCf. MANAGEMENT (cont.)
DOCUMENT CONTROL 25
Project Logbooks 26
Sample Tags 26
Chain-of-Custody Records 27
Lidar Magnetic Tapes 27
Laboratory Records 27
Photographs 28
Corrections to Documentation 28
Consistency of Documentation 28
Branch/Division Files 29
Evidentiary Files 29
Litigation Documents 30
Confidential Business Information 30
EVIDENCE AUDIT 30
QUALITY ASSURANCE 31
APPENDIX
Witness Guidelines 32
FIGURES
1 Project Management Procedures ID
2 Receipt for Samples 20
3 Completed Receipt for Samples 21
4 Chain-of-Custody Record 23
5 Completed Chain-of-Custody Record 24
TABLES
1 Authorities Granted Under Federal Environmental Laws and
Regulations for Administrative/Civil Investigations 3
2 Transmittal of NEIC Documents & Correspondence 7
-------
FOREWORD
The National Enforcement Investigations Center (NEIC) is the
organizational element of the Office of Enforcement which provides a full
range of technical, investigative, and litigation support expertise for the
Agency's administrative, civil, and criminal enforcement cases. NEIC
focuses on those nationally and regionally significant enforcement
initiatives which require:
Development and/or application of new methods and
procedures/approaches for enforcement investigations, case
development/management and resolution;
Methods/procedures developed and used for a specific project
or case in one region which can be applied nationally or on a
multi-regional basis for improving the EPA enforcement
program and addressing and achieving risk reduction
objectives;
Evaluation, review and/or support of proposed pollution
controls, abatement and remedial measures applying
innovative engineering and scientific technology with
subsequent widespread application;
Investigation of special environmental compliance problems
where an initial application and/or innovative interpretation of
statutory and regulatory requirements is necessary,
Defense of the methods and techniques used and/or positions
taken by the government during legal proceedings/settlement
negotiations;
State-of-the-art litigation support, information/records
management and evidence audits for the Agency's priority
cases.
NEIC maintains expert staff and sophisticated equipment capabili-
ties for conducting investigations throughout the United States. NEIC has
the ability to:
Plan and manage a wide range of environmental
investigations
Conduct comprehensive multi-media investigations
Gather and analyze information on facilities and
businesses from a variety of EPA and other databases
Perform industrial process evaluations
-------
Evaluate the adequacy and validity of data collection and
analyses
Review and develop analytical techniques, methodolo-
gies, and computer information systems
Implement enforcement strategies in coordination with the
Office of Enforcement, other EPA Headquarters and Regional
Offices
Assist in the preparation of cases for litigation
Provide specialized and expert testimony on a wide
variety of subjects
Provide assistance to EPA's delegated state enforcement
programs including state criminal enforcement efforts
Provide training to federal and state employees regarding
environmental investigations and enforcement }
The primary objective of NEIC is to provide expertise and resources
for development and support of Federal and State civil and criminal
enforcement cases. To meet this objective, NEIC has established the
following policies and procedures. These emphasize the need to
(a) thoroughly understand the applicable environmental laws and
regulations; (b) clearly identify project objectives; and (c) adequately plan
and implement all field, laboratory', and other support activities.
The goal of this manual is to present procedures for collection and
development of admissible and defensible evidence in support of the Agency
enforcement programs. In instances where these prescribed procedures
are inappropriate or inadequate, NEIC personnel may use alternate
procedures after securing the approval of their supervisor or consulting
with the Enforcement Specialist Office, as appropriate.
This manual contains policies and procedures developed solely to
provide internal guidance to NEIC employees and its contractors. The
policies and procedures which are set forth do not create any rights,
substantive or procedural, enforceable at law by a party to litigation with
EPA or the United States.
NEIC makes available, through various forums, the expertise ii has
developed by conducting enforcement investigations, supporting
litigation/ settlement negotiations, etc.
11
-------
Office at
*.O ftoi 2S227
Dwtvcr. COM22S
SPEGAL ASSISTANT
CharปS W Murray Jr
DIRECTOR
Frank M Covington
DEPUTY DIRECTOR
Carroll G. Wills
ASSISTANT DIRECTOR.
PLANNING ซ MANAGEMENT
t Craig
INFORMATION
MANAGEMENT BRANCH
RotMflH
EVIDENCE AUDIT/QUALITY
ASSURANCE UNIT
NFORMATXX SERVICES
SECTION
Chปrt.rปM Swfeks
ADMINISTRATIVE SERVICES
BRANCH
B O90ปn
HUMAN RESOURCES
SECTION
. Parr
SUPPORT SERVICES
SECTION
Jan* E Chadbourn*
DATA SYSTEMS SECTION
Gซorgซ C Allison
ASS.STANT DIRECTOR
LABORATORY SERVICES
Oary D Vounj
CHEMISTRY BRANCH
Joซ H
PESTICIDES 4 TCXIC
SUBSTANCES BRANCH
Dซan f Hill
ANALYTICAL
INVESTIGATIONS SECTION
K Ene Nottingham
APPLIED
INSTRUMENTATION
SECTON
Douqtซt S
COMPLIANCE SECTION
Dซnซ E
ANALYTICAL SECTION
Vacant
DATA ANALYSIS SECTION
Ricnaro C Ross
PROGRAM t
TECHNOLOGY
ADVISORY STAFF
Thomas O Dart
ASSISTANT:
OPERAT
)|RECTOR
IONS
QUAIL STREET
FACILITY
CfVIL ENFORCEMENT
SUPPORT BRANCH
CRIMINAL ENFORCEMENT
SUPPORT BRANCH
TECHNICAL t TRAINING
SUPPORT BRANCH
C Gxo*
111
-------
I. GENERAL POLICIES AND PROCEDURES
CONFLICTS OF INTEREST. GIFTS AND GRATUTTTES
Each NEIC employee is expected to promote public confidence in the
integrity, reliability and dependability of the Environmental Protection
Agency. Employees are required to perform their duties in a dignified,
tactful, courteous and diplomatic manner, as the situation dictates. At all
times they must comply with the regulations governing EPA employee
conduct (40 CFR Part 3). Employees should consult their supervisors
and/or the Enforcement Specialist Office for guidance on ethics issues. For
general information regarding ethics refer to:
Ethics in a Nutshell ... Ethical Conduct for EPA Employees ... in Brief.
U.S. EPA, Office of the Inspector General (March 1988)
Employee Resonsibilities and Conduct.
U.S. EPA, Office of General Counsel (Feb. 1984).
EPA's Guidance on Ethics and Conflicts of Interest
(Feb. 1984)
Employees shall avoid actual and apparent conflicts of interest
through outside employment and other private interests or activities. A
conflict of interest may exist whenever an EPA employee has a direct or
indirect personal interest in a matter which is related to his official duties
and responsibilities. Each NEIC employee must avoid even the appearance
of a conflict of interest because the appearance of a conflict damages the
integrity of the Agency and its employees in the eyes of the public. All
employees must, therefore, avoid situations which are, or give the
appearance of, conflicts of interest when dealing with others in or outside
the Government. Any information acquired during an employee's duties is
for official use only.
An employee is forbidden to solicit or accept any gift, gratuity,
entertainment, favor, loan or any other item of monetary value from any
person, corporation or group which has interests that may be substantially
affected by such employee's official actions, or which conducts operations
regulated by EPA. Further guidance on EPA's policy for accepting gifts,
gratuities or entertainment may be found at 40 CFR S.400.
PUBLIC RELATIONS
Good working relations should be established when dealing with the
public, including personnel at facilities being investigated. This can best be
accomplished by using diplomacy, tact and persuasion. Employees should
not speak of any person, other regulatory agency, or facility in a derogatory
-------
manner and should avoid providing a professional opinion on specific
products or projects.
Good public relations and common sense dictate that employees
dress appropriately for the activity in which they are engaged, this
includes wearing the proper protective clothing and using safety
equipment, as appropriate.
ENTERING FACILITIES
Authority
Federal environmental statutes grant EPA enforcement personnel
authority to enter and inspect facilities [Table 1]. Each authority is similar
to that stated below from Section 308 of the Clean Water Act:
"(a)(B) the Administrator or his authorized representative ... upon
presentation of his credentials
(i) shall have a right of entry to, upon, or through any premises in
which an effluent source is located or in which any records
required to be maintained ... are located, and
(ii) may at reasonable times have access to and copy any records,
inspect any monitoring equipment or method... and sample
any effluents which the owner or operator of such source is
required to sample."
For investigations conducted pursuant to the Safe Drinking Water
Act (SDWA), Toxic Substances Control Act (TSCA), or Federal Insecticide,
Fungicide and Rodenticide Act (FIFRA), the investigator must provide a
responsible official of the facility with a written notice of inspection. In
addition, during TSCA inspections, TSCA Confidentiality Notice forms
should be offered. At the completion of the TSCA inspection, a Declaration
of Confidential Business Information and Receipt for Samples and
Documents forms are completed, as appropriate.
Many NEIC inspections are conducted after obtaining consent from
the person(s) in charge of a site. Consent means the intentional foregoing
of right to privacy which is not the result of either fear, ignorance or
trickery. When obtaining consent, do not suggest that civil or criminal
consequences will result from denial of entry. Consent to photograph onsite
activities during any consensual administrative/civil investigation should
be obtained before any photographs are taken. In administrative/civil
matters, if the element of surprise is critical to the inspection, the site is
unoccupied, or prior behavior indicates that entry may be denied, an
administrative search warrant may be needed. If so, employees should
consult the Enforcement Specialist Office before the inspection is attempted.
------- An error occurred while trying to OCR this image.
-------
While consent may not be necessary for entering a public area or for
acting under emergency conditions, no forcible nonemergency entry is
permitted into a private area without a search warrant. When consent is
withdrawn after the inspection has begun, the team shall leave the area
and follow the procedures for denial of entry as detailed below.
Entry Procedures
To comply with statutory requirements during civil/administrative
investigations, a facility should be entered in the following manner:
The plant premises should be entered through the main gate
or through the entrance designated by the facility personnel.
The inspectors should introduce themselves in a dignified,
courteous manner to a responsible plant official, clearly
identify the organization they represent, and briefly describe
the purpose of the inspection. Identification credentials will
always be presented before an inspection is commenced. A
responsible plant official may be the owner, operator, officer or
agent-in-charge of the facility, including a person responsible
for the plant's environmental affairs.
If there is only a guard present at the entrance, the employee
should present credentials and ask the guard to call his
supervisor or the responsible official.
If the company provides a blank sign-in sheet, log or visitors'
register, it is acceptable to sign it. However, NEIC employees
must not sign a release of liability (waiver) or any statement
which would place limits on EPA's use of the information for
enforcement purposes.
When problems or questions arise, the NEIC employee should
call his supervisor or the Enforcement Specialist Office.
Denial Of Entry Procedures
If entry is denied, the employee should not contest the issue with the
facility representative, but immediately do the following:
Cite the appropriate EPA administered legislation and
inspection authority, ask if he/she heard and understood the
reason for your presence, and record the answer and any
reasons given for denial of entry.
-------
Record the name, title and telephone number of the individual
denying entry as well as the date and time.
Leave the premises.
If consent is withdrawn after the inspection is already
underway, retain .all notes, records and samples and remove
all equipment taken into the facility.
After leaving the facility, the inspector should, at the earliest
opportunity, document the events related to the denial of entry and inform
the appropriate NEIC supervisory personnel and the Enforcement
Specialist Office.
INVESTIGATIONS OF ALLEGED CRIMINAL ACTIVITY
Participants in criminal investigations may be subject to additional
requirements governing such investigations. Because of the severe
penalties that may be imposed on the individuals convicted of violating the
criminal provisions of the environmental laws or other statutes, there is
closer scrutiny of constitutional safeguards to protect the individual's
rights. Special Agents of the EPA, Criminal Investigations Division, will
provide instructions regarding these safeguards to the project team on all
investigations in which they are involved. From the beginning of such an
investigation until it is completed, the rights of all individuals must be fully
protected.
If, during the course of a civil/administrative inspection, aspects of
criminal activity become apparent, the inspector should obtain all the
evidence documenting the possible violation. The Criminal Investigations
Division, or the appropriate Special Agent-in-Charge must then be apprised
immediately. If a criminal investigation is opened, any files will be
maintained separately from the current (or planned) civil investigation.
Where applicable, the Agency's policy on parallel criminal and civil
enforcement proceedings shall be followed.
COMMUNICATIONS EXTERNAL TO THE OFFICE OF ENFORCEMENT
In the course of business, NEIC employees communicate with
persons outside the Agency's Office of Enforcement. Untimely releases of
information and expressions of opinions can greatly hinder NEIC's
investigative activities. Judgment is required, and supervisors should be
consulted and kept informed of all such communications. For
communications regarding matters in litigation and criminal
investigations the Enforcement Specialist Office must be consulted.
NEIC has established internal distribution and filing procedures for
all correspondence. Employees producing correspondence should do so
-------
through their secretaries or check with their secretaries regarding the
internal distribution of correspondence.
Table 2 contains requirements for transmittal of specific documents
and correspondence, external to the Office of Enforcement.
Requesting Information from Persons Subject to Regulation
NEIC employees may request information from a facility before,
during or after an on-site investigation. The environmental statutes
require those regulated to keep various records and to make them available
to EPA upon request. Several statutes also protect the trade secrets and
confidential information of the regulated community.
Any confidential information received in the mail or hand-delivered
shall be marked Confidential and handled as Confidential Business
Information. "In compliance with EPA regulations, any written request for
company information, pursuant to statutory authority, must contain a
statement notifying the facility that it may designate all or part of the
information requested by the Agency as confidential in accordance with 40
CFR Part 2.
NEIC personnel should not accept confidential information unless it
is needed. When confidential information is entered into an inspector's
logbook the entire logbook must be treated as confidential. The Evidence
Audit Unit (EAU) will provide the inspectors with adhesive labels and/or
stamps to mark information submittals or logbook notes of observations
which are claimed to be confidential. Where documents are provided by the
company, the company officials should be requested to mark the document
to identify the material which they claim is confidential. Confidentiality
claims, which cover portions of otherwise nonconfidential documents,
should be clearly identified by company officials. Logbooks must be marked
as confidential by the inspector; in no case shall company officials be
permitted to copy or review logbooks. See Chapter III of this manual for
additional information on the treatment of confidential business
information.
By statute, certain information, including effluent, emission, health
and safety data is not entitled to confidential treatment.
Disclosure of Official Information to the Public
EPA policy is to make information about EPA and its work available,
freely and equally, to all individuals, groups and organizations. This
policy, however, does not extend to confidential business information or
investigatory information relating to the suspected violation of federal laws.
------- An error occurred while trying to OCR this image.
-------
Any NEIC employee who receives a request, written or verbal, for the
inspection or disclosure of NEIC investigatory records or confidential
information, including those made under judicial discovery procedures,
the Privacy Act or the Freedom of Information Act, shall immediately
advise the Chief, Enforcement Specialist Office.
FOIA Response Procedures
The NEIC Director is delegated the authority to respond to Freedom
of Information Act (FOIA) requests directed to NEIC. This delegation
authorizes the Director to make the initial determination concerning the
release of NEIC records. The FOIA procedures and requirements
contained in 40 CFR Part 2 Subpart A, EPA Order 1550.1C and the FOIA
manual apply to such determinations.
Any NEIC employee, including NEIC contractors, who receive a
written request to disclose records, must immediately forward the request,
together with its envelope, to the Enforcement Specialist Office (ESO) which
will initiate efforts to identify and locate responsive records. Responsive
records will not necessarily be released. There are numerous exemptions
which permit or even require NEIC to deny the request in whole or in part.
No acknowledgement of the request is necessary.
The ESO will date-stamp and log in the request; coordinate collection
of relevant documents; coordinate with appropriate Regional, Headquarters
and Department of Justice (DO J) attorneys; and prepare the response to the
FOIA request.
Denials shall include the basis for withholding the documents
requested and a statement that the requestor has the right to appeal the
denial. Only the NEIC Director has the authority to deny disclosure of
requested records, in whole or part.
8
-------
II. PROJECT MANAGEMENT
This section discusses how NEIC activities should be planned and
implemented so that work is conducted in a timely manner and meets case
objectives.
Projects undertaken by NEIC span a wide variety of activities
ranging from one employee performing technical or administrative tasks to
numerous employees from diverse disciplines working as a team to
accomplish a series of complex tasks. NEIC projects can include any or all
of these phases:
Project Request
Project Team Formation
Background Information Review
Project Plan Preparation
Project Plan Implementation
Report Preparation
Enforcement Case Support
This section of the manual discusses each phase and outlines
pertinent NEIC policies [See Figure 1].
Not all of these phases are required for each NEIC project. Moreover,
these phases are not necessarily discrete steps to be performed in order,
before going on to the next phase. A project team may repeat or return to
any phase during the life of the project and may work on several phases
simultaneously.
PROJECT REQUEST
Requests may be received from other offices of EPA, other Federal
agencies, State agencies and local governments. Unless otherwise
directed, all requests should be sent to the Director of NEIC. Prior to
preparing a request, requesting parties are encouraged to make a
preliminary inquiry to determine if NEIC can provide the assistance
required. Depending on the type of assistance needed, NEIC may respond
to verbal requests. Acceptance of a verbal request is normally given on a
tentative basis pending receipt of a written request. Any request should
detail the objectives, relate those objectives to the enforcement actions
anticipated, specify general time frames for the work and identify the
technical and/or legal contacts) of the requesting office. A written request
facilitates understanding of the request by all involved parties. However,
routine or recurring requests may not require any written request and
NEIC, at its option, may accept any project without a written request.
Requests received by NEIC have included those which require
extensive field investigative work on environmental problems (e.g., multi-
------- An error occurred while trying to OCR this image.
-------
media investigations), as well as others which require only a limited
technical or legal review of a remedial or abatement proposal, or analytical
support for Regional enforcement cases. Other requests have involved
development of enforcement cases, performance audits, compliance
evaluation inspections, pesticide investigations, ground water
investigations and pollution control technology assessments.
NEIC usually will notify the requesting party in writing when it
accepts the project. When possible, the notification also will include a
tentative schedule. Specific NEIC employees should be named as the
contacts for coordination with the requesting party. In addition, the
acceptance notice should identify any further information needed by NEIC.
PROJECT TEAM FORMATION
Civil Investigations
Once a project is accepted, a project team is organized. It will
include representatives from those NEIC organizational units participating
in the project. As appropriate, representatives from outside NEIC (e. g.,
the U.S. Department of Justice) may also participate in team activities and
discussions.
The initial functions of the project team are to determine:
The applicable statutory/regulatory provisions
The evidence which must be obtained to address project
objectives
The resources and scheduling necessary to achieve objectives
The technical expertise necessary to evaluate the target or
source.
The team has the responsibility to identify and minimize potential
problems. Team members must be knowledgeable about their respective
units' activities in the particular project, and are responsible for describing
or defending that activity in subsequent negotiations and/or legal
proceedings.
NEIC names a specific individual from the project team as the
coordinator. This person generally serves as a central point of contact with
the requesting party and is responsible for communicating and
coordinating project requirements and information with all involved
parties. In addition, this person must assure that a requestor's needs are
met, including preparation of the necessary documents and reports.
11
-------
The makeup and coordination of the project team is dictated by the
type of investigation conducted. Sometimes a "team" may consist of only
one person.
Criminal Investigations
In criminal investigations, the NEIC project coordinator is
responsible for sampling, analysis and other technical activities and works
with the EPA Special Agent, FBI agent and/or the appropriate U.S.
Attorneys' Office.
BACKGROUND INFORMATION REVTEW
The purpose of a background information review is to gather
information pertinent to the project. This review usually begins before a
project plan is written and continues throughout the course of a project.
The information obtained is used to prepare the project plan, conduct the
field investigation, and write the report.
The scope and duration of the background review are related to the
project objectives and vary with project complexity. Background
information is available through the in-house and affiliated libraries and
the NEIC computerized data retrieval systems. Meetings may be held with
EPA Headquarters, Regional offices and/or State and local agencies and
other Federal agencies to discuss the project, and to review and obtain
copies of relevant files. Where necessary, a site reconnaissance and/or
preliminary site visit provides verification and/or updating of background
information. Examples of information obtained and/or reviewed may
include:
Applicable (current and previous) State and Federal laws and
regulations
Current and previous facility permits and permit applications
Previous inspection reports
Case files from previous and pending enforcement
actions/litigation
Correspondence between regulatory agencies and the facility
Administrative Orders, settlement agreements, compliance
schedules
Headquarters/Regional legal strategy and/or policy related to
the NEIC investigation
12
-------
Specific descriptions of facility processes and pollution control
systems
* Self-monitoring data
Alternative control and treatment technology applicable to the
facilities) being investigated
Available and state-of-the-art sampling and analytical
methods
Information received through interviews of informants
In all investigations requiring field activities, knowledge of the
potential and existing safety hazards associated with the facilities or
targets, and local emergency services, is essential.
PROJECT PLAN PREPARATION
The format of a project plan will depend on the scope of the project.
Some projects require a detailed plan, describing the objectives,
enforcement history, facility operation, investigative methods, safety
protocols, etc. In others, a memorandum defining the objectives, tasks and
schedules may suffice. A general outline of NEIC project activities may be
included in the written response to a requesting party. After sufficient
background information has been obtained and evaluated, a detailed project
plan can be prepared. In many cases the plan is not completed until
planning meetings have been held, files have been reviewed, and a
preliminary site visit has been made. Projects requiring only analytical
services may not require a project plan. In some cases, the NEIC project
acceptance letter is a sufficient project plan, as long as safety issues are
addressed, as necessary, in the letter or in a separate safety plan.
The project coordinator, in conjunction with other team members,
prepares the project plan detailing the scope, logistics, and objectives. In
addition, other items usually addressed in a project plan include:
Background information. For example, background
information for a hazardous waste treatment, storage and
disposal facility investigation or an industrial facility
evaluation, may include a summary of processes, sources of
pollution - their control or treatment, applicable regulations
and permit requirements. In those investigations where there
is, or a potential exists for groundwater pollution, information
on the geologic and hydrogeologic conditions, and on-site
hazardous waste disposal operations, are necessary for plan
development.
13
-------
Investigative methods. For example, this should include a
description of sampling locations and procedures, analytical
requirements, the on-site records review and collection of
operating process data and information.
Quality assurance/quality control procedures
Document control and chain-of-custody procedures
Safety requirements and safety plan for on-site activities
Schedules for investigative activities. This should include
schedules for field work, analyses, reports, etc.
Prior to commencing a field investigation, a briefing session with all
project team members should be held. At that time, those aspects of the
investigation such as communication with facility personnel, sampling
and monitoring requirements, test procedures and analyses, special
technical needs, legal aspects and safety requirements can be discussed.
The project coordinator, as the identified contact person representing
the project team, should communicate closely with the requestor during the
planning phase to ensure the identified objectives are addressed. The
completed project plan represents an agreement between the requestor and
NEJC.
Project plans (draft or final) for activities related to
administrative/civil enforcement cases will usually be transmitted by an
Assistant Director or the Deputy Director [Table 2]. The project coordinator
numbers draft copies in red ink and maintains a record showing who
received draft copies and when such copies were returned. The project
coordinator should have all draft copies returned. Changes and
modifications desired by the requestor should be communicated to the
project coordinator who will assure that all affected parties are apprised of
the requested changes and provided an opportunity to respond. Once all
concerned parties agree to the project plan, it serves as a reference
document for the project. The plan is subject to change as circumstances
warrant and should contain a statement to that effect. Any change(s)
should be documented and appropriate parties notified.
Because of the greater sensitivity associated with criminal
investigations, the distribution and review of planning documents will be
limited. Transznittal external to the Office of Enforcement of any technical
document prepared by NEIC for a criminal investigation must be by the
Chief, Enforcement Specialist Office.
14
-------
PROJECT PIJIN IMPLEMENTATION
Project activities include legal and technical information searches,
facility inspections, process and pollution control technology evaluations,
sampling, monitoring, laboratory analyses, laboratory evaluations and
analytical data reviews. To the extent possible, these activities are
conducted following established NEIC techniques and standard operating
procedures, EPA policy and program guidance and promulgated
regulations. When new methods or modifications to existing procedures
are appropriate, these changes will be documented.
Each team member must assure that all work is conducted safely
and that required safety equipment is used. All participants must adhere
to the applicable safety requirements.
Because the information generated during an investigation can be
subjected to close scrutiny during subsequent negotiations and/or litigation,
procedures ensuring the integrity and security of all evidence must be
followed throughout any project. See Part III, Evidence Management.
REPORT PREPARATION
NEIC prepares various reports in carrying out its enforcement
program responsibilities. These reports include field trip reports, status or
progress reports, technical memoranda and enforcement investigation
reports all of which detail the who, what, where, when, and how of the
enforcement activity. NEIC reports can be used by Regional and
Headquarters offices, other law enforcement organizations, the U.S.
Department of Justice and U.S. Attorneys to support enforcement actions.
Other reports prepared by NEIC include internal procedures and operating
manuals, technical reports and papers (e.g., a report on an NEIC-
developed laboratory procedure or field investigation technique). Report
format, including the color of the cover, should be in accordance with the
NEIC Report Services Operating Procedures Manual.
Enforcement reports are prepared by the appropriate individual or
project team members. All participants in the report preparation process
must assure that their individual contributions to the report and other
document* are accurate, fully supportable and commensurate with Agency
and NEIC policies. Although the overall responsibility for preparation and
content of the reports (including all supporting documents) rests with the
project coordinator, all team members must accept responsibility for the
quality, accuracy and admissibility of the information in the final report.
Reports are reviewed internally prior to distribution in either draft or
final form outside of NEIC. The NEIC reviewers can include the team
members and others directly involved in the project and report preparation
process, as well as appropriate Assistant Directors and their Branch
Chiefs, the Deputy Director and the Chief, Enforcement Specialist Office.
15
-------
External review drafts should be transmitted according to Table 2. All
external review drafts will be numbered in red ink and stamped on the
cover page with the following statement: DRAFT REPORT - FOR AGENCY
REVIEW ONLY, DO NOT DUPLICATE. All other pages of the draft will
also be marked DRAFT.
Reports prepared for criminal investigations will receive limited
distribution. Any draft or final report prepared by NEIC for a criminal
investigation which must be sent external to the Office of Enforcement will
be transmitted by the Chief, Enforcement Specialist Office.
Copies of NEIC civil enforcement reports are maintained by the
library. NEIC reports may receive public distribution through the National
Technical Information Service (NTIS). Their availability to the public is
announced through the NTIS publication "Government Reports
Announcement" and a fee is set by the NTIS for their reproduction and
distribution in either paper or microfiche form.
External distribution of enforcement reports not available through
NTIS must be authorized through the Chief, Enforcement Specialist Office
who will consult with the project coordinator and the appropriate EPA
Office of Regional Counsel.
Distribution is also restricted for reports that contain confidential
business information. Under several environmental laws, including
TSCA, businesses may claim certain information given to EPA to be
confidential business information. When a report contains confidential
business information, the title page and every page containing that
information is marked CONFIDENTIAL.
All reports containing confidential information will be kept in secure
areas until restrictions are removed. Questions concerning the availability
of reports should be directed to the Enforcement Specialist Office.
ENFORCEMENT CASE SUPPORT
Completion and transmitted of a report does not signify the end of
NEIC involvement in an investigation. When the initial assistance activity
leads to an enforcement action, NEIC staff are available to:
Participate in the preparation of the enforcement case and in
subsequent legal proceedings
Assist in negotiations
Provide further technical consultation and assistance (e.g.,
additional field work as necessary)
16
-------
As necessary, NEIC personnel are available to serve as witnesses
(fact and expert) and to provide technical and legal assistance to
government attorneys before and during depositions, pretrial hearings and
trials.
The project coordinator is responsible for tracking any enforcement
action planned or being taken by the requesting party. In conjunction with
the Enforcement Specialist Office, this individual is also responsible for
identifying and offering any other support NEIC can provide.
17
-------
III. EVIDENCE MANAGEMENT
SAMPLE CONTROL
A sample is one type of physical evidence collected during an
investigation. An essential part of all NEIC enforcement investigations is
accounting for the evidence gathered. To ensure the integrity of the
evidence, the following sample identification and chain-of-custody
procedures have been established. The use of alternative procedures must
be documented.
Sample Identification
When in-situ measurements are made, the data are recorded directly
into logbooks or are electronically recorded, with identifying information
(project code, station number, station location, date, time and samplers),
field observations and remarks. Examples of in-situ measurements
include pH, temperature, conductivity, flow measurement, continuous air
monitoring and stack gas analysis.
Samples, other than in-situ measurements, are identified by a
sample tag or other appropriate identification. These samples are removed
and transported from the sampling location to a laboratory or other location
for analysis. Whenever a sample is separated into portions to be provided to
another party each portion is identified by a sample tag marked "split." In
a similar fashion, tags will be marked for "Blank" or "Replicate" samples.
The information recorded on the sample tag includes:
Project Code (A three-alpha-numeric digit assigned by NEIC)
Project Name
Station Location (Description)
Station No. (Usually a two digit code)
Date
Time
Samplers' signatures
Remarks (The samplers record pertinent information
including preservatives used)
After collection, the samples are maintained in accordance with the
chain-of-custody procedures discussed below.
IB
-------
Blank, uniquely numbered sample tags, logbooks and other
accountable documents are provided by the Evidence Audit Unit.
Sp]it fomples
NEIC policy is that sample splits will be offered to facility officials
whenever samples are collected during a civil investigation. Section
3007(a)(2) of the Resource Conservation and Recovery Act (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 CERCLA contains similar requirements. Samples may also
be split with other Government agencies. Whether split samples should be
collected or given to facility personnel in a criminal investigation is a
decision to be made by the EPA Special Agent assigned to the case and the
prosecuting attorney (e.g. Assistant U.S. Attorney).
When samples are split, a separate Receipt for Samples form
[Figures 2 and 3] is prepared for those samples and marked to indicate with
whom the samples are being split. The person relinquishing the split
samples to the facility or agency should request the signature of the party or
his representative acknowledging receipt of the samples. If a
representative is unavailable or refuses to sign, this is noted in the
"Received by" space. When splits are offered but refused, such refusal
should be documented on the Receipt for Samples form or in the logbook or
elsewhere.
Chain-of-Custodv for Samples
Due to the evidentiary nature of samples collected during
enforcement investigations, possession must be traceable from the time the
samples are collected until they or the data derived from the samples are
introduced as evidence in legal proceedings. To maintain and document
sample possession, chain-of-custody procedures are followed.
Custod
All samples collected as evidence are to be maintained under secure
conditions and documented chain-of-custody procedures. In general, as
few people as possible should be a part of the chain-of-custody. A sample is
under custody if:
It is in your possession.
It is in your view, after being in your possession.
You secured the sample in an appropriate container and made
arrangements to transport it to the laboratory.
3S
------- An error occurred while trying to OCR this image.
-------
i ซJ !
^ ฃ:Z
< s
* Z =
:!l
"
"
-C f
T;
i
uj
! 2*3
! T -2 -
C7 -,
a
2 2
- - !
55
i K.
it;
:Jl i
r * *
O O O.
c
c-
I, ง
*i ฃ
nGURE 3 - COMPLETED RECEIPT FOR SAMPLES
Best available copy.
-------
You transferred the sample to authorized personnel.
It is held in a secure area.
Transfer of Custody and Shipment
Samples are accompanied by a Chain-of-Custody Record
[Figure 4]. When transferring the possession of samples, the
individuals relinquishing and receiving will sign, date and
note the time on the Record. This Record documents sample
custody transfer. Figure 5 illustrates a completed Chain-of-
Custody Record.
Samples will be packaged properly* for shipment and
dispatched to the appropriate laboratory for analysis, with a
separate Chain-of-Custody Record accompanying each
shipment. Shipping containers will be padlocked or otherwise
sealed for shipment to the laboratory.
All shipments should be accompanied by the completed Chain-
of-Custody Record. The original record will accompany the
shipment, and a copy will be retained by the Project
Coordinator.
Freight bills, post office receipts and Bills of Lading must be
retained as part of the permanent documentation.** If
samples can be sent by mail (not those samples suspected of
containing hazardous materials), the package should be
registered with return receipt requested.
Laboratory Custody
Laboratories at NEIC are locked at all times. Access is limited
to authorized personnel and accompanied visitors.
Laboratory personnel accept custody of the shipped samples
and verify that the information on the sample tags matches
that on the Chain-of-Custody Record. Pertinent information as
to shipment, pickup, courier, etc. is entered in the "Remarks"
section. The laboratory recipient of the samples assures that
all samples are transferred to the proper analyst or stored in
the appropriate secure area.
See NEIC Standard Operating Procedures for Packaging, Marketing, Labeling and
Shipping of Samples (DOT requirements).
Copies of the bills and receipts may be provided to the NEIC Office of Planning and
Management to assure proper payment. Originals of these documents are retained tor the
project file.
22
-------
5, 5
2 ฃ
5 8!
o:
! X
C
FIGURE 4 - CHAIN-OF-CUSTODY RECORD
Best available copy.
------- An error occurred while trying to OCR this image.
-------
The laboratory will use the sample tag number, sample station
number or assign a unique laboratory number to identify each
sample.
Laboratory personnel are responsible for the care and custody
of samples from the time they are received until the sample is
exhausted or while it is in storage.
Each Laboratory Services Branch will follow a system for
tracking samples through the laboratory and identifying the
documents generated during the analysis of those samples.
Each employee must understand the Standard Operating
Procedures applicable to his/her respective Branch.
After sample analyses and necessary quality assurance checks
have been completed, the remaining portion of the sample, will
be kept secured as evidence until disposal is authorized as
described below. All identifying tags, data sheets and
laboratory records must be retained as part of the permanent
documentation unless they are contaminated. If records are
contaminated they can be enclosed in plastic and copied before
being disposed of as hazardous waste.
The Assistant Director, Laboratory Services, in coordination
with the Chief, Enforcement Specialist Office, and the project
coordinator will authorize disposal of samples and remaining
sample portions for all administrative/civil investigations. For
criminal investigations, the Assistant Director, Laboratory
Services, will contact the EPA Criminal Investigations
Division or other appropriate offices (e.g. FBI, DOJ) to
coordinate the disposal of samples collected in support of
criminal investigations.
DOCUMENT CONTROL
The goals of document control are: (1) to assure that all documents
generated or obtained by NEIC personnel will be accounted for when the
project is completed and (2) to prevent premature or inadvertent disclosure
of information. This program includes a serialized document system, a
document inventory procedure and an evidentiary filing system, operated
and controlled by the Evidence Audit Unit (EAU). The Document Control
Officer (DCO) maintains separate locked files for confidential business
information. The protocol for the transmittal of documents generated
during an enforcement investigation is, in large part, implemented and
monitored by the Enforcement Specialist Office [See Table 2].
25
-------
To provide document accountability for technical investigations, each
of the document categories discussed below features a unique serialized
number assigned by EAU for each item within the category. Accountable
documents used or generated by NEIC employees include logbooks, sample
tags, graphs, Chain-of-Custody forms, Receipt for Samples forms, and
bench sheets. The project coordinator disposes of any unused serialized
documents or may return them to EAU. Unless prohibited by weather,
waterproof ink should be used to record all data. When weather conditions
prohibit use of waterproof ink, entries should be made using a non smear
lead pencil (e.g. 2H or 3H).
Project Logbooks
The project coordinator is responsible for the transfer of logbooks to
field team members. Each person signs their logbook upon receipt and
records all information pertinent to the project in that logbook. A separate
logbook is used for each project.
Logbook entries should be dated, legible and contain an accurate,
factual and complete account of the investigation. Because the logbook is
the basis for the later written reports, it must contain only facts and
observations. Language should be objective, factual and free of the
inspector's personal feelings, characterizations, speculation, or other
terminology which is inappropriate. Entries made by individuals other
than the person to whom the logbook was assigned must be dated and
signed by the individual making the entry.
All project logbooks are the property of NEIC and are to be returned
by the project coordinator to the Evidence Audit Unit when a project has
been concluded. Representatives of facilities being inspected shall not fre
permitted to copy or review logbook notes.*
Sample Tags
Serialized sample tags are used to identify samples. After the tag
has been completed, it is attached to a sample. Transfer to another
individual is by use of a Receipt for Samples form [Figures 2 & 3]. Sample
tags contaminated with a hazardous substance will not be saved. The
serial number of the contaminated tag must be noted in the appropriate
logbook and the project coordinator notified. All information from
contaminated tags is recorded and the tags are photocopied, if possible, and
disposed of. At the completion of the field activities, all unused tags
(including those damaged or voided) must be returned to the project
coordinator for disposal or returned to EAU.
As appropriate, the inspector may copy document and I or photograph, logs for facility
representatives.
26
-------
Chain-of-Cuatodv Records
Serialized Chain-of-Custody Records are distributed in a manner
similar to that used for sample tags. When samples are transferred to
laboratory personnel, the recipient, after signing, files it in a secure place.
When dispatching samples via common carrier the original accompanies
the shipment and is signed by the receiving laboratory personnel.
Employees of common carriers do not sign the Chain-of-Custody form.
When samples are split with the source or another Government
agency, this is documented on a Receipt for Samples form. The tag serial
numbers from all splits are recorded on the form and a copy of the form is
provided for the source or agency. The white originals are returned to the
project coordinator.
Lidar Magnetic Tapes
Lidar data are recorded on the on-board computer. This computer is
used to analyze data and print results in report format. After analysis the
data are archived to a magnetic tape and maintained as an evidence record.
Laboratory Records
The instrument logbooks, bench sheets and the analyst's personal
notebook(s) must contain information sufficient to recall and describe each
step of the analysis performed. Sufficient detail also is necessary to enable
others to reconstruct the procedures followed should the original analyst be
unavailable for testimony. Any irregularities observed during the testing
process need to be noted. If, in the technical judgment of the analyst, it is
necessary to modify a particular method to perform an analysis, the
modification must be justified and properly documented.
The numbered laboratory notebook assigned to an individual can be
used for more than one project; however, only one project should be
discussed on each page. That page must be labeled with the project code,
dated and signed by the individual.
Where applicable, a numbered instrument logbook is used to record
information relating to calibration and maintenance of a particular
laboratory instrument.
In addition to information documenting the analyses performed,
field analysts should document in their project logbooks, in their laboratory
notebooks, or on bench sheets the date and calibration results for mobile
laboratory equipment. A record is also kept of any incidents; for example,
the disruption of electrical service to the laboratory, tampering with
Government vehicles or equipment, etc. Appropriate notations regarding
27
-------
visitors to the mobile laboratory, such as facility personnel, are entered in
the logbook.
Photographs
When photographs or videotapes are taken which show aspects of an
investigation, descriptions of those photographs or videotapes are entered in
a logbook. Identifying information (e.g. photographer, date, time, site
location, etc.) is normally entered into the logbook as photos (or groups of
photos) are taken. The photographer is not required to record the aperture
settings and shutter speeds for photographs taken within the normal
automatic exposure range. Special lenses, films, filters or other image
enhancement techniques must be noted in the logbook, if they could distort
or misrepresent what is depicted in the photographs. Logbook notations
and other documentation used to account for film processing must be
maintained. Once developed, the slides or photographic prints are
identified to correspond with the logbook descriptions.
Corrections to Documentation
If an error is made on an accountable document assigned to one
individual, that individual may make contemporaneous corrections simply
by drawing a line through the error, initialing it and entering the correct
information. Any subsequent error discovered should be corrected by the
person who made the entry, the person who discovered the error, or
another person familiar with the work. All subsequent corrections must be
initialed and dated.
If a sample tag is separated from a sample and lost in shipment, or a
tag was never prepared for a sample, or a properly tagged sample was not
transferred with a formal NEIC Chain-of-Custody Record, a written
statement should be prepared detailing how, when, and to whom the
sample was collected, air-dispatched, or hand-transferred. The statement
should include all pertinent information, such as entries in field logbooks
regarding the sample, whether the sample was in the sample collector's
physical possession or in a locked compartment until hand-transferred to
the laboratory, etc. Copies of the statement are distributed to the project
coordinator and the appropriate Branch project files.
Consistency
Each Branch or Division assembles its documents and cross-checks
information on corresponding sample tags, custody records, bench sheets,
analyst notebooks and other logbooks to ensure that data pertaining to each
particular sample is complete and consistent throughout the record. The
file should be arranged according to the procedures described in this
manual under "Evidentiary File." The project coordinator concurrently
performs a cross-check of field documents Oogbooks, custody records, etc.)
28
-------
to ensure that the field information is complete. The laboratory similarly
reviews their documentation for completeness. The EAU will review files
after these have been transferred to EAU. Criminal case files are
inventoried and numbered at the time of file assembly by the EAU or the
respective NEIC Branches/Divisions involved in the case.
Branch/Division Files
After a Branch has completed its work for a particular investigation,
all documents generated from that project should be assembled in the
Branch or Division file. Individuals may retain clean (no handwritten
comments) copies of documents for their personal files but only after
personally verifying that the original or similar copy is in the file. Each
project coordinator is responsible for assuring the collection and assembly
of all documents relative to a project at the time the project objectives are
completed. The technical investigation portion of criminal case files is
numbered, inventoried and transferred to EAU for storage. Any record
leaving the file after it has been transferred to EAU must be signed out.
Evidentiary Files
When NEIC has completed the project objectives, all inventoried
Branch and Division file documents are reviewed and submitted to EAU, as
specified above. The evidentiary file should be organized into the following
document classes in this sequence:
Privileged or Confidential Information
Project Plan
Project logbooks
Sampling documentation
- Sample tags
- Chain-of-Custody Records
- Receipt for Samples forms
Laboratory records (logbooks, bench sheets, etc.)
Project Correspondence
Documents obtained from facilities being investigated
Background information
Report notes, calculations, etc.
Photos, maps and drawings
Final reports)
Litigation/settlement documents
Other documents, as appropriate.
Once deposited in the evidentiary file, documents may only be
checked out through the EAU document control personnel.
2S
-------
Litigation Pogtimentg
Any litigation reports, letters, memoranda, draft court documents,
etc. from the Enforcement Specialist Office or other Government attorney
which discuss legal matters or strategies should be separately identified in
individual Branch and Division files. These documents should be marked
to identify the privileged nature of their contents. Internal distribution is
limited to the appropriate project participants and their supervisors.
Confidential Business Information
Some information requested and obtained by NEIC may contain trade
secrets which companies may request be guarded as confidential business
information (CBI). In general, NEIC employees who have a need to know
may have access to CBI. When CBI is obtained, NEIC employees must
follow specific requirements to protect the information. The regulations to
be complied with by every employee are at 40 CFR Part 2, Subpart B. Those
requirements vary with the particular law involved. If in doubt regarding
the requirements governing the handling of documents identified
as"confidential" or "trade secret," employees should consult the
Enforcement Specialist Office.
Of particular importance are the provisions of Section 14 of the Toxic
Substances Control Act (TSCA). A company may make confidentiality
claims for any and all information provided to the Agency with the
condition that specific criteria under TSCA are met. Once confidentiality
under TSCA is claimed, stringent procedures are followed to maintain tH'e
confidentiality of that information. Refer to the TSCA Confidential
Business Information Security Manual, U.S. EPA, Office of Toxic
Substances (Approved Nov. 1, 1985), for guidance. Before obtaining access
to anv CBI protected under TSCA. everv person must obtain TSCA CBI
clearance through the EAU.
All analytical work conducted on confidential samples will be
performed in a manner to preserve the confidentiality of the information
generated. The resulting documentation will be isolated from the Branch
or Division files when the records are called in by EAU.
EVIDENCE AUDIT
The Evidence Audit Unit (EAU) provides a continuing evaluation of
enforcement investigation activities. This evaluation addresses sample
control, document control, chain-of-custody, file assembly and evidence
security.
Some projects may be selected for an audit. The audit may include
an evaluation of sampling, sample custody, data recording and any
supporting documentation.
-------
For administrative/civil investigations and the technical portions of
criminal investigations, EAU requires submission of all records for
inclusion in the evidentiary file at the completion of a project. These files
are reviewed to assure that all documents generated or obtained during the
course of the investigation are present. Any discrepancies are brought to
the attention of the project coordinator and the Chief, Enforcement
Specialist Office.
QUALITY ASSURANCE
A Quality Assurance (QA) program is established at NEIC to assure
that data produced are of known and documented quality. QA program
requirements cover all measurement activities performed, supported or
required by NEIC. The authority and responsibility for directing QA
activities within NEIC are delegated to the QA Officer (QAO). QA direction
and guidance are.specified in the NEIC QA Program Plan.
The Quality Assurance Officer's responsibilities include
development, evaluation and documentation of QA policies and procedures
at NEIC. The QAO is assisted by QA division representatives in
implementing and coordinating the QA program. All employees involved
in sampling or measurement activities are responsible for carrying out
quality assurance requirements in accordance with the QA Program Plan
and any NEIC standard operating procedure and for informing the QAO or
QA coordinators of the need for corrective actions.
The QAO develops and conducts system audits to monitor the QA
program and the quality of data produced.
31
-------
APPENDIX
WITNESS GUIDELINES
-------
WITNESS GUIDELINES
The following suggestions are made for prospective witnesses in
order to lessen the fears and apprehensions which almost everyone has
when first testifying before a board, commission, hearing officer or in
court. Even those who have testified previously encounter a certain anxiety
when called for a repeat performance. When a witness is properly
prepared, both with regard to the subject matter of testimony and conduct
on the witness stand, there should be little fear about testifying.
It is of utmost importance that the witness be thoroughly prepared on
the subject matter of the testimony. Only the witness can recall what
occurred in the field and/or laboratory and why. Since many cases are tried
substantially after the field and laboratory activities have been conducted, it
is imperative that adequate documentation be originally prepared in order
that a witness' memory may be refreshed. A thorough and detailed review
of all relevant documents is the only way prospective witnesses can be
adequately prepared.
In order to assist witnesses on how they should conduct themselves
the following suggestions are given.
The witness will be required to take an oath to tell the truth. The
important point is to remember that there are two ways to tell the truth -
one is a halting, stumbling, hesitant manner, which makes the trier of fact
(the hearing officer, judge or jury) doubt that the witness is telling all the
facts in a truthful way; and the other way is in a confident, straightforward
manner, which inspires faith in what is being said. It is most important
that-the witness testify credibly. To assist a witness in testifying in such a
manner, a list of time-proven hints and aids are provided below.
GENERAL INSTRUCTIONS FOR A WITNESS
If you are to be a witness in a case involving testimony concerning
the appearance of an object, place, condition, etc., try to refresh your
recollection by again inspecting the object, place, condition, field notes and
records, etc., before the hearing or trial. While making such inspection,
close your eyes and try to picture the item and recall, if you can, the
important points of your testimony. Repeat this until you have thoroughly
familiarized yourself with the features of your testimony that will be given.
Before you testify, visit a court room trial or administrative hearing
and listen to other witnesses testifying. This will make you familiar with
such surroundings and help you understand some of the things you will
come up against when you testify. You should consider being present at the
hearing of the matter in which you are to testify in sufficient time to hear
other witnesses testify before you take the witness chair. This, however,
may not always be possible since, on occasion, witnesses are excluded from
the court room until they testify.
32
-------
A good witness listens to the question and then answers calmly and
directly in a sincere manner. The facts should be well known so they can be
communicated. Testimony in this manner applies to cross-examination as
well as direct examination.
Wear neat, clean clothes when you are to testify. Dress
conservatively. Do not chew gum while testifying or taking an oath. Speak
clearly and do not mumble.
DIRECT EXAMINATION
In a discussion on administrative procedures, E. Barrett Prettyman,
Retired Chief Judge, U.S. Court of Appeals for the District of Columbia,
gave the following advice:
The best form of oral testimony is a series of short, accurate
and complete statements of fact. Again, it is to be emphasized
that the testimony will be read by the finder of the facts, and
that he will draw his findings from what he reads. Confused,
discursive, incomplete statements of fact do not yield
satisfactory findings.
Stand upright when taking the oath. Pay attention and say "I do"
clearly. Do not slouch in the witness chair.
Do not memorize what you are going to say as a witness. If you have
prepared answers to possible questions, by all means do not memorize such
answers. It is, however, very important that you familiarize yourself as
much as possible with the facts about which you will be called upon to
testify.
During your direct examination, you may elaborate and respond
more fully than is advisable on cross-examination. However, when you
elaborate, do not ramble and do not stray from the main point raised by the
lawyer's question. The taking of testimony is a dialogue, not a monologue.
If your testimony concerns a specialized technical area, the Court or
hearing officer will find it easier to understand if it is presented in the form
of short answers to a logical progression of questions. In addition, by
letting the lawyer control the direction of your testimony, you will avoid
remarks which are legally objectionable or tactically unwise.
Be serious at all times. Avoid laughing and tallrmg about the case in
the halls, restrooms or any place in the building where the hearing or trial
is being held.
While testifying, look at the judge, hearing officer or jury most of the
time, and speak frankly and openly as you would to any friend or neighbor.
Do not cover your mouth with your hand. Speak dearly and loudly enough
33
-------
so that anyone in the hearing room or courtroom can hear you easily. At
all times make certain that the reporter taking the verbatim record of your
testimony is able to hear you and record what you actually say. The case
will be decided entirely on the words that are finally reported as having
been the testimony given at the hearing or trial. Always make sure that
you give a complete statement in a complete sentence. Half statements or
incomplete sentences may convey your thought in the context of the
hearing, but may be unintelligible when read from the cold record many
months later.
CROSS-EXAMINATION
Concerning cross-examination, Judge Prettyman gives the following
advice to prospective witnesses:
Don't argue. Don't fence. Don't guess. Don't make
wisecracks. Don't take sides. Don't get irritated. Think first,
then speak. If you do not know the answer but have an opinion
or belief on the subject based on information, say exactly that
and let the hearing officer decide whether you shall or shall
not give such information as you have. If a 'yes or no' answer
to a question is demanded but you think that a qualification
should be made to any such answer, give the 'yes or no' and at
once request permission to explain your answer. Don't worry
about the effect an answer may have. Don't worry about being
bulldozed or embarrassed; counsel will protect you. If you
know the answer to a question, state it as precisely and
succinctly as you can. The best protection against extensive
cross-examination is to be brief, absolutely accurate, and
entirely calm.
Unless you are testifying as an expert, the hearing officer or judge
will permit only testimony, based upon direct knowledge, as to the facts.
You usually will not be allowed to testify about what someone else has told
you (hearsay), and will not be allowed to provide your opinions or
conclusions.
Always be polite, even to the attorney for the opposing party.
Do not be a smart aleck or cocky witness. This will cost you your
credibility and the respect of the trier of the facts in the case.
Do not exaggerate or embroider your testimony.
Stop instantly when the judge or hearing officer interrupts, or when
the other attorney objects to what you say. Do not try to "sneak" your
answer into the record.
34
-------
Do not nod your head for a "yes" or "no" answer. Speak out dearly.
The reporter must hear an answer to record it.
If the question is about distances or time and your answer is only an
estimate, be certain that you say it is only an estimate.
Listen carefully to the question asked of you. No matter how nice the
other attorney may seem on cross-examination, he may be trying to hurt
you as a witness. Understand the question. Have it repeated if necessary;
then give a thoughtful, considered answer. Do not give a snap answer
without thinking. You cannot be rushed into answering, although, of
course, it would look bad to take so much time on each question that the
judge, hearing officer or jury would think that you are making up the
answers.
Answer the question that is asked, not the question that you think the
examiner (particularly the cross-examiner) intended to ask. The printed
record shows only the question asked, not what was in the examiner's
mind and a-nonresponsive answer may be very detrimental to your side's
case. This situation exists when the witness thinks "I know what he is
after but he hasn't asked for it." Answer only what is asked.
Explain your answers if necessary. This is better than a simple "yes"
or "no." Give an answer in your own words. If a question cannot be
answered truthfully with a "yes" or "no," you have a right to explain the
answer.
Answer directly and simply the question asked you and then stop.
Never volunteer
If by chance your answer was wrong, correct it immediately; if your
answer was not clear, clarify it immediately.
You are sworn to tell the truth. Tell it. Every material truth should
be readily admitted, even if not to the advantage of the party for whom you
are testifying. Do not stop to figure out whether your answer will help or
hurt your side. Just answer the question to the best of your ability.
Give positive, definite answers when at all possible. Avoid saying "I
think," "I believe," "in my opinion." If you do not know, say so. Do not
make up an answer. You can be positive about the important things which
you naturally would remember. If asked about little details which a person
naturally would not remember, it is best to say that you do not remember.
Do not act nervous. Avoid mannerisms which will make it appear
that you are scared, or not telling the truth; or all that you know.
Above all, it is most important that you do not lose your temper.
Testifying at length is tiring. It causes fatigue. You will recognize fatigue
-------
by certain symptoms: (a) tiredness, (b) crossness, (c) nervousness, (d)
anger, (e) careless answers, (f) willingness to say anything or answer any
questions in order to leave the witness stand. When you feel these
symptoms, recognize them and strive to overcome fatigue. Remember that
some attorneys on cross-examination are trying to wear you out so you will
lose your temper and say things that are not correct, or that will hurt you or
your testimony. Do not let this happen.
If you do not want to answer a question, do not ask the judge or
hearing officer member whether you must answer it. If it is an improper
question, your attorney will object for you. Do not ask the presiding officer,
judge or board member for advice.
Do not look at your attorney or at the judge or hearing officer for help
in answering a question. You are on your own. If the question is an
improper one, your attorney will object. If the judge or hearing officer then
says to answer it, do so.
Do not hedge or argue with the opposing attorney.
There are several questions which are known as "trick" questions.
That is, if you answer them the way the opposing attorney hopes you will,
he can make your answer sound bad. Here are two of them:
"Have you talked to anybody about this matter?" If you say "no," the
hearing officer or judge, or a seasoned jury, will know that is not true
because good lawyers always talk to the witnesses before they testily. If you
say "yes," the lawyer may try to imply that you were told what to say. The
best thing to say is that you have talked to the attorney and that you were
just asked what the facts were and to testify truthfully.
"Are you getting paid to testify in this matter?" The lawyer asking
this hopes your answer will be "yes," thereby implying that you are being
paid to say what your side wants you to say. Your answer should be
something like "No, I am not getting paid to testify; I am on salary and
there is no other compensation for my time beyond the reimbursement for
my travel"
35
-------
SAMPLE PACKAGING
AND SHIPPING
PERFORMANCE OBJECTIVES
At the end of this lesson, participants will be able to:
Identify the appropriate U.S. Department of Transportation
(DOT) regulations covering the packaging and shipping of
samples for laboratory analysis
Identify the appropriate table to determine the class and
packing group of a particular sample
Describe the shipping requirements for a sample labeled
"Environmentally hazardous substances, solid, n.o.s."
List the hierarchy of subsidiary risk
Review the necessary documentation for sample transport
-------
NOTES
SAMPLE PACKAGING
AND SHIPPING
RULES GOVERNING
TRANSPORTATION OF SAMPLES
49CFR171-179
New regulations published:
December 21,1990
Effective date:
October 1,1991
NEW RULING
Adopts UN labels and placards
Adopts UN identification numbers for
hazardous materials
Provides packing standards based on
performance criteria
Makes US standards compatible with
international standards
6/93
Sample Packaging and Shipping
-------
NOTES
PACKAGING CLASSES
Packing Group I - great danger
Packing Group II - medium danger
Packing Group III - minor danger
Note: Most samples are in Packing Group
COMPLIANCE DEADLINES
(Performance-Oriented Packaging)
October 1,1991
- Effective date of HM-181 (revised
September 18,1991)
- Hazard communication requirement
for new explosives (mandatory)
COMPLIANCE DEADLINES
(Performance-Oriented Packaging)
October 1, 1992 - Hazard communication
requirement for materials poisonous by
inhalation and for infectious substances
(mandatory)
October 1, 1993 - Hazard communication
requirement for all hazardous materials
Sample Packaging and Shipping
6/93
-------
NOTES
COMPLIANCE DEADLINES
October 1, 1994
- Old DOT-specific packagings are
eliminated under final rule
- New packages must be manufactured
in accordance with Parts 173 and 178
- New placard system required
COMPLIANCE DEADLINES
October 1, 1996 - Marks end of
transition period
TRAINING FOR SAFE TRANSPORTATION
OF HAZARDOUS MATERIALS
49 CFR Part 172.700
Final rule
- Published May 15, 1992
- 57 FR 95 20944
Effective date: July 1,1992
6/93
Sample Packaging and Shipping
-------
NOTES
SCOPE OF TRAINING
REQUIREMENTS
Persons involved in transportation of
hazardous materials
Categories
- General awareness/familiarization
training
- Function-specific training
- Safety training
- Driver training
SCOPE OF TRAINING
REQUIREMENTS
Initial training before October 1, 1993
(if hired before July 2, 1993)
Train within 90 days of employment
Refresher training once every 2 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
Sample Packaging and Shipping
6/93
-------
NOTES
SAMPLES NOT REGULATED
BY DOT
Unpreserved environmental samples
Preserved environmental samples
SAMPLES NOT REGULATED BY DOT
(Preserved Environmental Samples)
Substance in
Water Solution
HCI
HgCI2
HN03
H2S04
NaOH
H3P04
Concentration
<0.04% by weight
0.004%
0.35%
0.35%
0.08%
2
-------
NOTES
MINIMUM REQUIREMENTS FOR
NONREGULATED SAMPLES
40CFR261.4d2HAandB
Date of shipment
Description of sample
Sample packaged to contain leaks or
spills
PACKAGING REQUIREMENTS
FOR LIMITED QUANTITIES
49 CFR 173.155
Inner packagings
- Not over 4.0 L (1 gallon) for liquids
- Not over 5.0 kg (11 Ibs) for solids
Outer packagings
- Not to exceed 30 kg (66 Ibs)
PACKAGING LABORATORY SAMPLES
49 CFR
Determine proper shipping
name, hazard class, and
ID number
Determine packaging
requirements and Ltd Qty
exceptions
Mark package
172.101
(table)
173.24 or
173.150-156
172.301
Sample Packaging and Shipping
6/93
-------
NOTES
PACKAGING LABORATORY SAMPLES
49CFR
Label package and
additional labeling
requirements
Prepare shipping papers
Placard (if necessary)
172.101 (4)
172.402-448
172.200-204
172.500
UNIDENTIFIED SAMPLES FROM
CERCLA/RCRA/DOD SITES
Hazardous Materials Table 172.101
Environmentally hazardous substances,
liquid or solid, n.o.s.
Hazard Class 9
Packing Group III
UNIDENTIFIED SAMPLES FROM
CERCLA/RCRA/DOD SITES
Hazardous Materials Table 172.101
UN 3082 for liquids
UN 3077 for solids
LtdQty
6/93
Sample Packaging and Shipping
-------
NOTES
PACKAGING LTD QTY
Environmentally Hazardous Substances
40CFR173.155(b)
Inner packagings - VOA vials or glass jars
Strong outer packagings
Sufficient absorptive and cushioning
material to prevent breakage and leakage
HAZARD PRIORITY
FOR SUBSIDIARY RISK
49CFR173.2a
1. Radioactive materials
2. Poisonous gases
3. Flammable gases
4. Nonflammable gases
HAZARD PRIORITY
FOR SUBSIDIARY RISK
49CFR173.2a
5. Poisonous liquids or
poisonous-by-inhalation
e. Pyrophoric material
7. Self-reactive material
Sample Packaging and Shipping
6/93
-------
NOTES
HAZARD PRIORITY
FOR SUBSIDIARY RISK
49CFR173.2a
8. Flammable liquids, corrosive materials,
flammable solids, spontaneously
combustible materials, dangerous when
wet materials, oxidizers, or poisonous
liquids or solids
HAZARD PRIORITY
FOR SUBSIDIARY RISK
49CFR173.2a
9. Combustible liquids
10. Miscellaneous hazardous materials
SHIPPING PAPERS
49 CFR 172.200
Required for shipment if sample is a
hazardous material
Must include
- Contents
- Emergency response
telephone number
6/93
Sample Packaging and Shipping
-------
NOTES
SHIPPING PAPERS
Description of Hazardous Materials
Proper shipping name (Table 172.101)
Hazard class or division
Identification number
Packing group
Total quantity (e.g., 40 ml)
SHIPPING PAPERS
Additional Description Requirements
49 CFRSubpartCI 72.200
Exemptions
Ltd Qty
Hazardous substances
Radioactive material
SHIPPING PAPERS
Additional Description Requirements
49 CFR Subpart C 172.200
Empty packaging - residue
Transportation method - air, rail, road,
or water
Dangerous when wet material
Sample Packaging and Shipping
10
6/93
-------
NOTES
SHIPPING PAPERS
Additional Description Requirements
49 CFRSubpartd 72.200
n.o.s.
Poisonous materials
Elevated temperature materials
EPA PACKAGING
RECOMMENDATIONS
EPA PACKAGING
Low-Concentration Sample
The contaminant of highest concentration
is present at <10 ppm
Example: background environmental
samples
Source: A Compendium of Superfund Field Operations
Methods, section 6, page 6-1.
6/93
11
Sample Packaging and Shipping
-------
NOTES
EPA PACKAGING
Medium-Concentration Sample
The contaminant of highest concentration
is present at >10 ppm and <15%
(150,000 ppm)
Example: onsite weathered materials
Source: A Compendium of Superfund Field Operations
Methods, section 6, page 6-1.
EPA PACKAGING
High-Concentration Sample
At least one contaminant is present at a
level >15%
Example: samples from tanks and
drums
Source: A Compendium of Superfund Field Operations
Methods, section 6, page 6-1.
ENVIRONMENTAL SAMPLES
Label and seal sample jar
Place sample jar in plastic bag
Place jars in cooler with vermiculite
and ice
Place shipping papers and chain of
custody in cooler
Sample Packaging and Shipping
12
6/93
-------
NOTES
ENVIRONMENTAL SAMPLES
Tape cooler shut
Affix custody seals on cooler
Ship by fastest available method
HAZARDOUS SAMPLES
Label and seal sample jar
Place sample jar in plastic bag
Place jar in paint can with vermiculite
Place paint cans in cooler with vermiculite
and ice
HAZARDOUS SAMPLES
Place shipping papers and chain of
custody in cooler
Tape cooler shut
Affix custody seals on cooler
Include shipper's certification
Ship by fastest available method
6/93
13
Sample Packaging and Shipping
-------
NOTES
EPA RECOMMENDATIONS
DOT regulations are legally binding
EPA is reconsidering their
recommendations in response to
new DOT regulations
IATA
International Air Transport Association
(IATA) regulations on specific samples
may be more stringent than EPA or DOT
regulations
POTENTIAL PROBLEMS WITH
SAMPLE SHIPMENT AND ANALYSIS
Incorrect or incomplete paperwork
Laboratory receipt of incorrect samples
Insufficient volume for analysis requested
Source: User's Guide to the Contract Laboratory
Program, December 1986.
Sample Packaging and Shipping
14
6/93
-------
NOTES
POTENTIAL PROBLEMS WITH
SAMPLE SHIPMENT AND ANALYSIS
Broken or leaking samples
Matrices other than water or soil
Nonhomogeneous, multiphase water or
soil samples
Source: User's Guide to the Contract Laboratory
Program, December 1986.
6/93
15
Sample Packaging and Shipping
-------
SAMPLE PACKAGING AND SHIPPING
DEPARTMENT OF TRANSPORTATION REGULATIONS
On December 21, 1990, the U.S. Department of Transportation (DOT) published their new
transportation regulations in the Federal Register. These regulations modified the U.S. regulations
to agree more completely with the U.N. transportation regulations. In terms of shipping samples
for laboratory analysis, the regulation changes have caused some changes in the way samples may
be packaged, labeled, and shipped. Figures la and Ib are a decision tree for use when shipping
potentially hazardous samples. This chart is primarily for use when the sample is from an
uncontrolled hazardous waste site, as opposed to an operating industrial facility sampled under the
Resource Conservation and Recovery Act (RCRA). At a RCRA facility, the components of the
sample should be known with some confidence and packaged according to the substance. At an
uncontrolled site, however, little, if anything, may be known about the soil or drum sample.
If a sample is an offsite environmental sample, a background sample, or a sample from a domestic
water well at which no contamination is known, the sample would not fall under DOT regulations
and should be packaged according to the U.S. Environmental Protection Agency (EPA) Contract
Laboratory Program (CLP) protocols. This involves placing the sample in a plastic bag and putting
the bag in a metal or plastic cooler with bagged ice for coolant if necessary. The cooler should then
be filled with enough absorbent material (e.g., vermiculite) around the sample container to absorb
any spillage and prevent breakage. DOT has determined that the levels of preservatives such as
nitric acid in the samples do not cause them to fall under DOT regulations as a hazardous substance.
The package is then labeled and shipped by overnight carrier. Generally, the shipment is identified
as an "Environmental Laboratory Sample."
If the sample is an onsite soil suspected of being contaminated with a known substance or of being
hazardous by characteristic, it should be subjected to the same onsite characterization as a drum
sample. However, if nothing is known about the sample (and it is not hazardous by characteristic),
then it may be shipped as "Environmentally hazardous substances, liquid, n.o.s. or Environmentally
hazardous substances, solid, n.o.s.." Table 1 from 40 CFR 172.102 shows this to be a Class 9,
Packing Group III, substance. The Class 9 label (Figure 2) is affixed to the package. The UN
designation number is UN 3082 for a liquid and UN 3077 for a solid. Class 9 shipments fall under
the limited quantity exception for placarding. A limited quantity is defined as inner packages not
to exceed 4 L for liquids and 5 kg for solids, and strong outer packaging not to exceed 30 kg gross
weight. A metal- or plastic-covered cooler will meet this specification. A shipper's declaration of
dangerous goods (Figure 3) must be included in addition to the standard chain of custody and
laboratory request forms.
6/93 17 Sample Packaging and Shipping
------- An error occurred while trying to OCR this image.
-------
o c
D) tp
03
CO
o
CO
o
E co
_o
+->
CO
0
* 0)
00)^
O) C I C
c
LU
FIGURE IB. PACKAGING DECISION TREE
6/93
19
Sample Packaging and Shipping
------- An error occurred while trying to OCR this image.
-------
FIGURE 2. CLASS 9 LABEL
6/93
21
Sample Packaging and Shipping
------- An error occurred while trying to OCR this image.
-------
Samples from drums, tanks, lagoons, sludge pits, or settling ponds will be the most likely to yield
high concentration or high hazard samples. The first step is to identify the sample by substance
(e.g., benzene). If identification is possible, the sample should be packaged by the substance
according to the hazardous materials table in 40 CFR 172.102. If the substance cannot be identified,
then the sample should be classified by characteristic, such as flammable or corrosive. Field
characterization tests can be performed for most characteristics, including radioactivity, the highest
hazard class. If the substance is hazardous by characteristic, it should be packaged accordingly. If
it is a mixture, the hierarchy of hazards and exceptions in 40 CFR 173.2a should be referred to.
If the sample cannot be identified by substance and if it is not hazardous by characteristic, then it
should be classified as "Environmentally hazardous substances, liquid, n.o.s." or " Environmentally
hazardous substances, solid, n.o.s." and packaged as above.
6/93 23 Sample Packaging and Shipping
-------
PACKAGING, LABELING, AND SHIPPING
taken from:
EPA/540/P-87/001
(OSWER Directive 9355.0-14)
December 1987
A COMPENDIUM OF SUPERFUND
FIELD OPERATIONS METHODS
(Section 6)
OFFICE OF EMERGENCY AND REMEDIAL RESPONSE
OFFICE OF WASTE PROGRAMS ENFORCEMENT
U.S. ENVIRONMENTAL PROTECTION AGENCY
WASHINGTON, DC 20460
6/93 25 Sample Packaging and Shipping
-------
6.2 PACKAGING, LABELING AND SHIPPING
6.2.1 Scope and Purpose
This subsection describes the packaging, labeling and shipping used for environmental and hazardous
samples collected at a waste site.
6.2.2 Definitions
Low-Concentration Sample
The contaminant of highest concentration Is present at less than 10 parts per million (ppm).
Examples include background environmental samples.
Medium-Concentration Sample
The contaminant of highest concentration is present at a level greater than 10 ppm and less
than 15 percent (150.000 ppm). Examples Include material onsite that is obviously weathered.
High-Concentration Sample
At least one contaminant Is present at a level greater than 15 percent. Samples from drums
and tanks are assumed to be high concentration unless information indicates otherwise.
Routine Analytical Services (RAS)
Analysis of a soil or water sample on a 30- to 45-day turnaround time for a list of 126 organics,
23 metals, and cyanide.
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 contractor's employee (see Subsection 1.1).
6/93 27 Sample Packaging and Shipping
-------
6.2.3 Applicability
The procedures described in this subsection apply to samples collected at a waste site. They must be
followed whether shipping to a CLP laboratory or a noncontract laboratory.
The shipment of hazardous materials Is governed by the Transportation Safety Act of 1974. Following
Is a list of references that detail the regulations:
Title 49 CFR
- Parts 100-177 - Shipper Requirements and Hazardous Material Table
- Parts 178-199 - Packaging Specifications
- Section 262.20 - Hazardous Waste Manifest
International Civil Aviation Regulations (ICAO)
- Technical Instructions for the Safe Transport of Dangerous Goods by Air (lists man-
datory international and optional domestic regulations)
I nternational Air Transport Association (IATA)
- Dangerous Goods Regulations (This tariff Incorporates 49 CFR, ICAO, and additional
IATA regulations. Most International and domestic airlines belong to IATA and require
conformance to all applicable regulations.)
Tariff BOE-6000-D (reprint of 49 CFR with updates)
6.2.4 Responsibilities
Detailed responsibilities are described in the procedures subsection. General responsibilities are as-
signed as follows:
Site Managers will state, to the best of their knowledge, whether samples planned for collection are
environmental or hazardous samples.
Equipment manager will procure shipping supplies (metal cans, shipping labels, vermiculite, etc.)
using RSCC whenever needed.
Sampling personnel will properly label and package the samples.
6.2.5 Records
The user should refer to Section 4 for discussion of the records associated with sample collection and
chain-of-custody forms.
The following records are associated with the labeling and shipping process:
Sample tag or label
Traffic report label
Sample Packaging and Shipping 28
-------
Custody seal
Chain-of-custody (COG) form
Bill of lading (airbill or similar document)
Examples of the first four documents are given In Subsections 4.6 and 5.1.6; an example of an airbill is
given in Subsection 6.2.
6.2.6 Procedi-res
The procedures described in this subsection are carried out after the sample preservation described in
Subsection 6.1.6.2. They are generic In nature; an approach to regional differences Is presented in Sub-
section 6.2.7.
6.2.6.1 Environmental Samples
Low-concentration samples are defined as environmental samples and should be packaged for ship-
ment as follows:
1. A sample tag is attached to the sample bottle. Examples of properly completed sample
tags are given in Exhibit 5-7.
2. All bottles, except the volatile organic analysis (VOA) vials, are taped closed with electrical
tape (or other tape as appropriate). Evidence tape may be used for additional sample security.
3. Each sample bottle is placed In a separate plastic bag, which is then sealed. As much air
as possible is squeezed from the bag before sealing. Bags may be sealed with evidence tape
for additional security.
4. A picnic cooler (such as a Coleman or other sturdy cooler) Is typically used as a shipping
container. In preparation for shipping samples, the drain plug Is taped shut from the inside
and outside, and a large plastic bag is used as a liner for the cooler. Approximately 1 inch of
packing material, such as asbestos-free vermiculite, perlite, or styroioam beads, is placed in
the bottom of the liner. Other commercially available shipping containers may be used.
However, the use of such containers (cardboard or fiber boxes complete with separators and
preservatives) should be specified in the sampling plan and approved by the EPA RSCC if CLP
Is used.
5. The bottles are placed in the lined picnic cooler. Cardboard separators may be placed be-
tween the bottles at the discretion of the shipper.
6. Water samples for low or medium-level organics analysis and low-level inorganics analysis
must be shipped cooled to 4ฐC with ice. No Ice is to be used in shipping inorganic low-level
soil samples or medium / high-level water samples, or organic high-level water or soil samples,
or dioxin samples. Ice is not required in shipping soil samples, but may be utilized at the op-
tion of the sampler. All cyanide samples, however, must be shipped cooled to 4ฐC.
29 Sample Packaging and Shipping
-------
7. The lined cooler is filled with packing material (such as asbestos-free vermiculite, perlite, or
styrofoam beads), and the large Inner (garbage bag) liner is taped shut. Sufficient packing
material should be used to prevent sample containers from making contact during shipment.
Again, evidence tape may be used.
8. The paperwork going to the laboratory is placed inside a plastic bag. The bag is sealed and
taped to the inside of the cooler lid. A copy of the COG form should be included In the paper-
work sent to the laboratory. Exhibit 5-4 gives an example of a properly completed COC form.
The last block on the COC form should indicate the overnight carrier and airbill number. The
airbill must be filled out before the samples are handed over to the carrier. The laboratory
should be notified if another sample is being sent to another laboratory for dioxin analysis, or if
the shipper suspects that the sample contains any other substance for which the laboratory
personnel should take safety precautions.
9. The cooler is closed and padlocked or taped shut with strapping tape (filament-type).
10. At least two signed custody seals are placed on the cooler, one on the front and one on
the back. Additional seals may be used if the sampler or shipper thinks more seals are neces-
sary. Exhibit 5-6 gives an example of the two types of custody seals available.
11. The cooler is handed over to the overnight carrier, typically Federal Express. A standard
airbill is necessary for shipping environmental samples. Exhibit 6-4 shows an example of the
standard Federal Express airbill.
6.2.6.2 Hazardous Samples
Medium- and high-concentration samples are defined as hazardous and must be packaged as follows:
1. A sample tag is attached to the sample bottle. Examples of properly completed sample
tags are shown in Exhibit 5-7.
2. All bottles, except the VOA vials, are taped closed with electrical tape (or other tape as ap-
propriate). Evidence tape may be used for additional security.
3. Each sample bottle is placed in a plastic bag, and the bag is sealed. For medium-con-
centration water samples, each VOA vial is wrapped in a paper towel, and the two vials are
placed in one bag. As much air as possible is squeezed from the bags before sealing.
Evidence tape may be used to seal the bags for additional security.
4. Each bottle is placed in a separate paint can, the paint can is filled with vermiculite, and the
lid is fixed to the can. The lid must be sealed with metal clips or with filament or evidence tape;
if clips are used, the manufacturer typically recommends six clips.
5. Arrows are placed on the can to indicate which end is up.
6. The outside of each can must contain the proper DOT shipping name and identification
number for the sample. The information may be placed on stickers or printed legibly. A liquid
sample of an uncertain nature is shipped as a flammable liquid with the shipping name "FLAM-
MABLE LIQUID, N.O.S." and the identification number "UN1993." A solid sample of uncertain
nature is shipped as a flammable solid with the shipping name "FLAMMABLE SOLID, N.O.S."
Sample Packaging and Shipping 39 6/93
-------
Exhibit 6-4
STANDARD FEDERAL EXPRESS AIRBILL
Ad03 NIOIUO
OUVH SSlUd
6/93
31
Sample Packaging and Shipping
-------
and the identification number "UN1325." If the nature of the sample Is known, 49 CFR-171-177
Is consulted to determine the proper labeling and packaging requirements.
7. The cans are placed upright In a cooler that has had its drain plug taped shut Inside and
out, and the cooler has been lined with a garbage bag. Vermicullte is placed on the bottom.
Two sizes of paint cans are used: half-gallon and gallon. The half-gallon paint cans can be
stored on top of each other; however, the gallon cans are too high to stack. The cooler Is filled
with vermiculite, and the liner is taped shut.
8. The paperwork going to the laboratory Is placed Inside a plastic bag and taped to the in-
side of the cooler lid. A copy of the COC form, an example of which is shown in Exhibit 5-4.
should be Included in the paperwork sent to the laboratory. The sampler keeps one copy of
the COC form. The laboratory should be notified if a parallel sample is being sent to another
laboratory for dioxin analysis, or if the sample is suspected of containing any substance for
which laboratory personnel should take safety precautions.
9. The cooler is closed and sealed with strapping tape. At least two custody seals are placed
on the outside of the cooler (one on the front and one on the back). More custody seals may
be used at the discretion of the sampler.
10. The following markings are placed on the top of the cooler:
Proper shipping name (49 CFR172.301)
DOT identification number (49 CFR 172.301)
Shipper's or consignee's name and address (49 CFR-172.306)
'This End Up" legibly written if shipment contains liquid hazardous materials (49 CFR 172.312)
Other commercially available shipping containers may be used. The SM should ascertain that
the containers are appropriate to the type of sample being shipped. The SM should clearly
specify the type of shipping container to be used In the QAPJP.
11. The following labels are required on top of the cooler (49 CFR 172.406e):
Appropriate hazard class label (placed next to the proper shipping name)
"Cargo Aircraft Only" (if applicable as Identified in 49 CFR 172.101)
12. An arrow symbol (s) Indicating 'This Way Up" should be placed on the cooler in addition to
the markings and labels described above.
13. Restricted-article airbills are used for shipment. Exhibit 6-5 shows an example of a
restricted article Federal Express airbill. The "Shipper Certification for Restricted Articles" sec-
tion is filled out as follows for a flammable solid or a flammable liquid:
Sample Packaging and Shipping 32 6/93
-------
Number of packages or number of coolers
Proper shipping name: if unknown, use
- Flammable solid, N.O.S., or
- Rammable liquid, N.O.S.
Classification; If unknown, use
- Rammable solid or
- Rammable liquid
Identification number; if unknown, use
- UN1325 (for flammable solids) or
- UN 1993 (for flammable liquids)
Net quantity per package or amount of substance in each cooler
Radioactive materials section (Leave blank.)
Passenger or cargo aircraft (Cross off the nonapplicable. Up to 25 pounds of flammable solid per
cooler can be shipped on a passenger or cargo aircraft. Up to 1 quart of flammable liquid per
cooler can be shipped on a passenger aircraft, and up to 10 gallons of flammable liquid per cooler
can be shipped on a cargo aircraft.)
Name and title of shipper (printed)
An emergency telephone number at which the shipper can be reached within the following 24 to 48
hours
Shipper's signature
Note: The penalties for improper shipment of hazardous materials are severe; a fine of $25,000 and 5
years imprisonment can be Imposed for each violation. The SM or designee is urged to take adequate
precautions.
6.2.7 Regional Variances
There are no known regional variances for the shipment of hazardous samples. However, regional
variances for the shipment of environmental samples (low concentration) are common. Information in a
compendium on such variances can become dated rapidly. Thus, users are urged to contact the EPA RPM
or the RSCC for the latest regional variances.
1. Region I includes the five-digit laboratory number of each sample In the "Remarks" section
of the chaln-of-custody form to act as a cross check on sample identification.
2. Separators must be placed between the bottles of samples shipped from a Region IV site.
ESD also tapes the VOA vials and uses blue Ice.
6/93 33 Sample Packaging and Shipping
-------
3. Region V tapes the VOA vials and does not line the cooler with a plastic bag. Region V FIT
indicates the OTR / ITR number, bottle lot numbers, sample concentrations, and matrix in the
right-hand portion of the "Remarks" section of the chaln-of-custody form. The custody seal
numbers, airbill number, and "samples shipped via Federal Express" are Included In the lower
right-hand section.
4. Region VI does not tape sample bottles, put sample bottles In plastic bags, or line coolers
with plastic. Glass bottles are wrapped with "bubble wrap" Instead of cardboard separators. In
addition, the traffic report stickers are placed at the liquid level on the sample bottles to allow
the laboratories to check for leakage.
5. Region VIII does not put the sample In a plastic bag.
Because Information on variances can become dated rapidly, the user should contact the EPA RPM or
RSCC for current regional practices and requirements. Future changes and additional regional variances
will be incorporated In Revision 01 of this document.
6.2.8 Information Sources
CH2M HILL REMIFIT Documentation Protocol for Region V. May 1984.
Code of Federal Regulations, Title 49, Parts 171 to 177, Transportation.
U.S. Environmental Protection Agency. Engineering Support Branch Standard Operating Procedures and
Quality Assurance Manual. Region IV, Environmental Services Division. 1 April 1986.
U.S. Environmental Protection Agency. The User's Uuide to the Contract Laboratory Program. Office of
Emergency and Remedial Response. December 1986.
Sample Packaging and Shipping 34
-------
FIELD EXERCISE
PERFORMANCE OBJECTIVES
At the end of this lesson, participants will be able to:
Sample groundwater, soil, sediment, surface water, and
containerized waste using the proper tools and techniques
List the appropriate sampling equipment according to media
and the advantages and disadvantages of each
Properly label all types of sample containers
Properly complete the necessary shipping documentation
Correctly complete the chain of custody for each collected
sample
-------
FIELD EXERCISE DESCRIPTION
STATION ONE: SOIL SAMPLING
The following equipment is available:
Bucket augers
Hand trowels
Soil trier
Push tube sampler
Stainless steel pans
Split spoon sampler
Each team will collect one composite sample for semivolatile analysis and one grab sample for
volatile analysis.
STATION TWO: FIELD DECONTAMINATION
The following equipment will be available:
Isopropyl alcohol
Buckets
Spray and squirt bottles
Catch basins
Brushes
Detergent and water
Aluminum foil
Each team will field decontaminate at least two different pieces of sampling equipment from the soil
and/or groundwater station. Each team will collect a field blank for volatiles.
STATION THREE: SOIL GAS SAMPLING
The following equipment will be demonstrated:
Soil gas probe and slam bar
Gillian pump and desiccator
HW 101 Hnu photoionization detector
STATION FOUR: SURFACE WATER AND SEDIMENT SAMPLING
The following equipment is available:
LaMotte sampler
Bacon bomb
Kemmerer sampler
Gravity corer
Ekman dredge
Ponar dredge
Peristaltic pump
Hand auger
Alpha sampler
Beta sampler
Each team will collect a grab sample of surface water for cyanide analysis and a sediment sample
for metals analysis.
6/93
Field Exercise
-------
STATION FIVE: GROUIMDWATER SAMPLING
The following equipment is available:
Water level indicator
Bladder pump
pH meter
Bailers (PVC, PTFE, stainless steel)
Peristaltic pump
Waterra pump
Each team will collect two 40 mL vials for volatile analysis from each well and take water level and
pH measurements from the appropriate well.
STATION SIX: CONTAINERIZED WASTE SAMPLING-55-GALLON DRUMS
The following equipment is available:
COLIWASA
Bacon bomb
Grain thief
Drum thief
Bung wrenches
Mucksucker
Each team will collect a representative sample from a drum for pesticide/PCB analysis.
Field Exercise
6/93
------- An error occurred while trying to OCR this image.
-------
INDIVIDUAL DRUM LOG SHEET
Job #
Date
Page
of
Client
Drum #
Sample #_
Drum Size:
D 85 Gallon
D 15 Gallon
D 55 Gallon
D 5 Gallon
D 42 Gallon
D Other
D 30 Gallon
Type of Drum: D Fiber D Poly D Steel
Description of Sample:
LAYER 1 (TOP)
n Open
Top
D
Tight
Head
D Other
HNU Reading.
Color
D Uquld
D Solid
Amount (in)_
D Sludge
LAYER 2 (MIDDLE)
Colo r
D Liquid
D Solid
Amount (ln)_
D Sludge
LAYER 3 (BOTTOM)
Color
D Uquld
D Solid
Amount (in)_
D Sludge
a 1/4 a 1/2 a 3/4 a FUH
Amount In Drum: D Empty (< 1" residuals)
Description of Drum (Drum Label, Markings and Conditions): Overpack Needed? D Yes D No
Compatibility Group:
Composite Number,
Time
Sampled by
Witness
nซv. S/15/ซ7
AA6-04-CHM-OM
-------
PROBLEM SESSION: SAMPLE PLAN
DEVELOPMENT EXERCISE
PERFORMANCE OBJECTIVES
At the end of this lesson, participants will be able to:
List the elements of a phased sampling plan
Perform the initial elements of a sampling event from
background data analysis through field data point selection,
collection, and analysis
-------
SAMPLING FOR HAZARDOUS MATERIALS
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, field screening
techniques, and some limited sampling of water and sediment. 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
You will do a thorough background search of the information available. This information will assist
you in establishing the objectives for the remaining phases of the project. This information will be
provided to you and the cost of obtaining the information will be subtracted from your total budget
for Phases I and II. This phase will include a site walkover.
Phase II: Selection and Implementation of Field Screening Techniques
Choose the field screening technique, level of analytical support, and location of sampling points.
Once you have decided where to sample, visit the instructors at the "data table" and purchase your
field data. Your budget for Phases I and II 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 them, and then
decide where to sample next.
Phase III: Development of a Sampling and Analysis Plan
Evaluate your preliminary data from Phases I and II and develop a sampling and analysis plan for
the next step in the investigation of the ACWI site. Select the sample locations, media, analytical
support level, procedures, etc.
Phase IV : Results and Conclusions
Present your 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
6/93 1 Problem Session
-------
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 only briefly summarized.
Problem Session 2 6/93
-------
BUDGET WORKSHEET
Phase I: Background Data Search (Total Cost - $1500.00)
Phase II: Selection and Implementation of Field Screening Techniques
Your estimate indicates the approximate costs for the completion of Phase II.
Mobilization fee $3000.00 $3000.00
Ambient air monitoring
for entire site (OVA-128,
GC mode, tentative
identification) $1100.00
Shallow soil boring,
stratigraphic identification $500.00 ea.
Soil gas survey in
4 x 0.25-acre sets $1000.00/acre
Water analysis of drive points
(volatiles and base/neutral and acid
extractables [BNAs] only) $500.00/point
Surface water and sediment
analysis (volatile organic analysis
[VGA] and BNAs only) $500.00/sample
This price schedule does not take into account any surcharge for higher levels of protection than
Level D. IMPORTANT: you must do an 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.
TOTAL BUDGET FOR PHASES I AND II = $27,000.00
6/93 3 Problem Session
-------
BUDGET WORKSHEET
Phase III: Development of a Sampling and Analysis Plan
Phase IV: Results and Conclusions
Your recommendations may include the following analytical support. The prices provided must be
used to approximate the cost of your recommendations. Calculate the amount spent on each phase,
particularly the cost of your Phase III sampling effort.
Data interpretation,
report preparation $ 5500.00 $ 5500.00
VOAs $ 400.00
BNAs $ 750.00
Pesticides/PCBs $ 440.00
Total inorganics $ 625.00
Benzene, toluene, ethyl-
benzene, and xylenes
(BTEX) $ 100.00
Exploratory borings
Monitoring wells
Heavy equipment
Geophysical surveys
Problem Session 4 6/93
-------
Drilling and sampling will be $50.00 per foot (the same as Phase II). To construct a monitoring well
in the boring, add $500.00 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.
TOTAL BUDGET FOR PHASES I AND II
TOTAL BUDGET FOR PHASE III
TOTAL PROJECT BUDGET
6/93 5 Problem Session
-------
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 and 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., to fill, build upon, or otherwise alter a wetland. No further information is available
regarding ACWI.
Louisiana Geological Survey
Winnfield, Louisiana, is within the Mississippi embayment 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 subbituminous 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.
Information from the Chamber of Commerce
The ACWI site has been operating under various names and owners in this location for about ninety
years. It has been the site of wood-preserving operations since approximately 1910, when it was
bought by the Louisiana Creosoting Company. The major product lines in recent years have been
telephone poles and railroad ties.
Problem Session 6 6/93
-------
Interview with the Site Owner
The site owner's representative refused to divulge any information when he found out your company
was working on a site characterization of ACWI. He suggested you speak with the facility's legal
representative.
State of Louisiana Water Supply Board Files
The State of Louisiana Water Supply Board files indicate that there are no known water supply wells
in the vicinity of the ACWI site. The wells for the city of Winnfield are located over a mile from
the site and are screened in the Sparta formation at a depth of about 600 feet below ground surface.
Information from the Tax Assessor's Office
The American Tie & Telephone Company is located in the town of Winnfield, Louisiana, on a small
access road. It is near several major truck routes and railroad lines. All taxes are currently paid.
The property consists of two large and three small buildings, as well as a number of vertical storage
tanks and pressure vessels.
Climatological Data
The climate in Winnfield, Louisiana, is subtropical. The average temperature (1951-1980) ranges
from 47* in January to 81' in July and August. The average net annual rainfall is 50 inches. 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:
2 yr 30 min 1.7 in.
10 yr 30 min 2.4 in.
100 yr 30 min 3.5 in.
2 yr 1 hr 2.2 in.
10 yr 1 hr 3 in.
100 yr 1 hr 4 in .
2 yr 6 hr 3.5 in.
10 yr 6 hr 5.5 in.
100 yr 6 hr 8 in.
2 yr 24 hr 4.5 in.
10 yr 24 hr 8.5 in.
100yr24hr 11 in.
Mean annual lake evaporation is 48 inches.
6/93 1 Problem Session
-------
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 feet of the ground
surface. Using a limited number of shallow wells 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 general 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 6/93
-------
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 flat, with a total relief of 19 feet. Drainage is to the north and east
into Creosote Branch and is enhanced by the presence of two major drainage ditches (Figure 1).
A third smaller drainage ditch is also present on the site.
Access to the site is limited, largely due to the surrounding wetlands and heavily forested areas. A
perimeter reconnaissance of the site was performed in August 1989. 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 noted in the north, central, and southern portions of
the site. The investigators on the reconnaissance suspected that these areas were covered tar pits.
Five buildings were present on the site. One was used for offices/administrative purposes, one was
used as a laboratory, and the others were used for industrial processing. Six large pressure vessels
were present in the processing buildings. There was some soil staining around the pressure vessels.
Ambient air monitoring of the site indicated elevated levels of volatile organic compounds, with the
highest levels being in the vicinity of the surface tar pit.
A memorandum from a chemical engineer whose specialty is process design was found in some files
left onsite. 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, pentachlorophenol, phenanthrene, anthracene, fluoranthene, pyrene,
benz(a)anthracene, chrysene, benzo(b)fluoranthene, benzo(a)pyrene, indeno(l,2,3-cd)pyrene, as well
as 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
pentachlorophenol 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 from the operations of the 1960s.
6/93 9 Problem Session
-------
Forested Area
Residence
Building/PV
Vertical Tank
Woodchip Pile
FIGURE \. ACWI SITE MAP
Problem Session
10
6/93
-------
APPENDIX A
Removal Program
Representative Sampling Guidance
Volume I: Soil
-------
OSWER Directive 9360.4-10
November 1991
-------
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.
-------
OSWER Directive 9360.4-10
November 1991
REMOVAL PROGRAM
REPRESENTATIVE SAMPLING GUIDANCE
VOLUME 1: SOIL
Interim Final
Environmental Response Branch
Emergency Response Division
Office of Emergency and Remedial Response
Office of Solid Waste and Emergency Response
U.S. Environmental Protection Agency
Washington, DC 20460
Prepared by:
The U.S. EPA Committee on Representative Sampling for the Removal Program
printed i>n 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.
For more information on Soil Sampling and Surface Geophysics procedures, refer to the Compendium ofERT
Soil Sampling and Surface Geophysics Procedures, OSWER directive 9360.4-02, EPA/540/P-91/006. Topics
covered in this compendium include Sampling Equipment Decontamination, Soil Sampling, Soil Gas Sampling,
and General Surface Geophysics. The compendium describes procedures for collecting representative soil
samples and provides a quick means of waste site evaluation. It also addresses the general procedures used to
acquire surface geophysical data.
Questions, comments, and recommendations are welcomed regarding the Removal Program Representative
Sampling Guidance, Volume 1 - Soil. 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 Removal Program Representative Sampling Guidance, Volume 1 - Soil, please
contact:
Superfund Document Center
U.S. EPA - Headquarters
401 M Street, SW
OS-240
Washington, DC 20406
E-mail: OERR/PUBS
-------
Acknowledgments
This document was prepared by the U.S. EPA Committee on Representative Sampling for the Removal Program,
under the direction of Mr. William A. Coakley, the Removal Program QA Coordinator of the Environmental
Response Team, Emergency Response Division. Additional support was provided by the foDowing EPA
Workgroup and under U.S. EPA contract # 68-WO-0036 and U.S. EPA contract * 68-03-3482.
EPA Headquarters
Office of Emergency and Remedial Response
Office of Research and Development
Region 1
Region 4
Region 8
National Enforcement Investigation Center
EPA Regional
EPA Laboratories
EMSL, Las Vegas, NV
Harry Allen
Royal Nadeau
George Prince
John Warren
Alex Sherrin
William Bokey
Jan Rogers
Denise Link
Peter Stevenson
Chuck Ramsey
Delbert Earth
Ken Brown
Evan Englund
George Flatman
Ann Pitchford
Llew Williams
ill
-------
Table of Contents
Page
Notice ii
Acknowledgments iii
List of Tables viii
List of Figures ix
1.0 INTRODUCTION
1.1 Objective and Scope 1
1.2 Removal Program Sampling Objectives 1
13 Representative Sampling 1
1.4 Example Site 2
2.0 SAMPLING DESIGN
2.1 Introduction 3
2.2 Historical Data Review 3
23 Site Reconnaissance 3
2.4 Migration Pathways and Receptors 4
2.4.1 Migration Pathways and Transport Mechanisms 4
2.4.2 Receptors 4
25 Removal Program Sampling Objectives 4
2.6 Data Quality Objectives 5
2.7 Field Analytical Screening and Geophysical Techniques 5
2.8 Parameters for Analysis 6
2.9 Representative Sampling Approaches 6
2.9.1 Judgmental Sampling 6
2.9.2 Random Sampling 6
2.93 Stratified Random Sampling 6
2.9.4 Systematic Grid Sampling 8
2.9.5 Systematic Random Sampling 8
2.9.6 Search Sampling 8
2.9.7 Transect Sampling 9
2.10 Sampling Locations 11
2.11 Example Site 11
2.11.1 Background Information 11
2.11.2 Historical Data Review and Site Reconnaissance 12
2.11.3 Identification of Migration Pathways, Transport Mechanisms and Receptors 14
2.11.4 Sampling Objectives 14
2.11.5 Selection of Sampling Approaches 14
2.11.6 Field Analytical Screening, Geophysical Techniques, and Sampling Locations 15
2.11.7 Parameters for Analysis 17
-------
Table of Contents (continued)
Pagq
3.0 EQUIPMENT
3.1 Introduction 21
3.2 Field Analytical Screening Equipment 21
33 Geophysical Equipment 21
3.4 Selecting Sampling Equipment 21
3.5 Example Site 24
3.5.1 Selection of Sampling Equipment 24
3.5.2 Selection of Field Analytical Screening Equipment 24
3.53 Selection of Geophysical Equipment 24
4.0 FIELD SAMPLE COLLECTION AND PREPARATION
4.1 Introduction 27
4.2 Sample Collection 27
4.2.1 Sample Number 27
4.2.2 Sample Volume 27
43 Removing Extraneous Material 27
4.4 Sieving Samples 28
4.5 Homogenizing Samples 28
4.6 Splitting Samples 28
4.7 Compositing Samples 29
4.8 Final Preparation 30
4.9 Example Site 30
5.0 QUALITY ASSURANCE/QUALITY CONTROL EVALUATION
5.1 Introduction 31
5.2 QA/QC Objectives 31
53 Sources of Error 31
53.1 Sampling Design 31
53.2 Sampling Methodology 32
533 Sample Heterogeneity 32
53.4 Analytical Procedures 32
5.4 QA/QC Samples 32
5.4.1 Field Replicates 33
5.4.2 Collocated Samples 33
5.43 Background Samples 33
5.4.4 Rinsate Blanks 33
5.4.5 Performance Evaluation Samples 33
5.4.6 Matrix Spike Samples 33
5.4.7 Field Blanks 34
5.4.8 Trip Blanks 34
5.5 Evaluation of Analytical Error 34
5.6 Correlation Between Field Screening Results and Confirmation Results 34
5.7 Example Site 35
VI
-------
Table of Contents (continued)
Page
6.0 DATA PRESENTATION AND ANALYSIS
6.1 Introduction 37
62 Data Posting 37
63 Geologic Graphics 37
6.4 Contour Mapping 37
6J Statistical Graphics 37
6.6 Geostatistics 39
6.7 Recommended Data Interpretation Methods 39
6.8 Utilization of Data 39
6.9 Example Site 40
References 45
vu
-------
List of Tables
Table Pjgfi
1 Probability of Missing an Elliptical Hot Spot 10
2 Representative Sampling Approach Comparison 12
3 Portable Field Analytical Screening Equipment 22
4 Geophysical Equipment 23
5 Soil Sampling Equipment 25
vui
-------
List of Figures
Figure Page
1 Random Sampling 7
2 Stratified Random Sampling 7
3 Systematic Grid Sampling 7
4 Systematic Random Sampling 8
5 Search Sampling 9
6 Transect Sampling 11
7 Site Sketch and Phase 1 Soil Sampling Locations, ABC Plating Site 13
8 Phase 2 Soil Sampling and XRF Screening Locations, ABC Plating Site 16
9 Phase 2 Sampling Grid Cell Diagram 17
10 GPR Survey Results, ABC Plating Site 18
11 EM-31 Survey Results, ABC Plating Site 19
12 Phase 2 Sampling Grid Cell Diagram (Grid Sizes > 100 x 100 ft.) 28
13 Quartering to Homogenize and Split Samples 29
14 Sampling Error due to Sampling Design 32
15 Computer-Generated Contour Map, ABC Plating Site (4000 mg/kg Hot Spot) 38
16 Computer-Generated Contour Map, ABC Plating Site (1400 mg/kg Hot Spot) 38
17 Histogram of Surface Chromium Concentrations, ABC Plating Site 41
18 Phase 2 Surface Data Posting for Chromium, ABC Plating Site 42
19 Phase 2 Subsurface Data Posting for Chromium, ABC Plating Site 43
20 Contour Map of Surface Chromium Data (ppm), ABC Plating Site 44
21 Contour Map of Subsurface Chromium Data (ppm), ABC Plating Site 44
IX
-------
1.0 INTRODUCTION
1.1 OBJECTIVE AND SCOPE
This is the first volume in a series of guidance
documents that assist Removal Program On-Scene
Coordinators (OSCs) and other field staff in
obtaining representative samples at removal sites.
The objective of representative sampling is to
ensure that le or a rou o amles
accurately characterizes site conditions. This
document specifically addresses representative
sampling for soil The following chapters are
designed to assist field personnel in representative
sampling within the objectives and scope of the
Removal Program. This includes: assessing
available information; selecting an appropriate
sampling approach; selecting and utilising
geophysical, field analytical screening, and sampling
equipment; utilizing proper sample preparation
techniques; incorporating suitable types and
numbers of QA/QC samples; and interpreting and
presenting the analytical and geophysical data.
As the Superfund program has developed, the
Removal Program has expanded its emphasis
beyond emergency response and short-term
cleanups. Longer, more complex removal actions
must meet a variety of sampling objectives,
including identifying threat, delineating sources and
extent of contamination, and confirming the
achievement of clean-up standards. Many important
and potentially costly decisions are based on the
sampling data, making it very important that OSCs
and field personnel understand how accurately the
sampling data characterize the actual site conditions.
In keeping with this strategy, this document
emphasizes field analytical screening and
geophysical techniques as cost effective approaches
to characterize the site and to select sampling
locations.
1.2 REMOVAL PROGRAM
SAMPLING OBJECTIVES
Although field conditions and removal activities can
vary greatly from site to site, the primary Removal
Program soil sampling objectives include obtaining
data to:
1. Establish threat to public health or welfare or
to the environment;
2. Locate and identify potential sources of
contamination;
3. Define the extent of contamination;
4. Determine treatment and disposal options; and
5. Document the attainment of clean-up goals.
These objectives are discussed in detail in section
15.
1.3 REPRESENTATIVE SAMPLING
Representative soil sampling ensures that a sample
or group of samples accurately reflects the
concentration of the contaminant(s) of concern at a
given time and location. Analytical results from
representative samples reflect the variation in
pollutant presence and concentration throughout a
site.
This document concentrates on the variables that
are introduced in the field ~ namely, those that
relate to the site-specific conditions, the sampling
design approach, and the techniques for collection
and preparation of samples. The following variables
affect the representativeness of samples and
subsequent measurements:
Geological variability Regional and local
variability in the mineralogy of rocks and soils,
the buffering capacity of soils, lithologic
permeability, and in the sorptive capacity of the
vadose zone.
Contaminant concentration variability -
Variations in the contaminant concentrations
throughout the site.
Collection and preparation variability --
Deviations in analytical results attributable to
bias introduced during sample collection,
preparation, and transportation (for analysis).
Analytical variability Deviations in analytical
results attributable to the manner in which the
sample was stored, prepared, and analyzed by
the on-site or off-site laboratory. Although
analytical variability cannot be corrected
-------
through representative sampling, it can falsely
lead 10 the conclusion that error is due to
sample collection and handling procedures.
1.4 EXAMPLE SITE
An example site, presented at
the end of each chapter,
illustrates the development of a
representative soil sampling
plan that meets Removal
Program objectives.
-------
2.0 SAMPLING DESIGN
2.1 INTRODUCTION
The following procedures are recommended for
developing a sound sampling design. Many steps
can be performed simultaneously, and the sequence
is not rigid.
Review existing historical site information;
Perform a site reconnaissance;
Evaluate potential migration pathways and
receptors;
Determine the sampling objectives;
Establish the data quality objectives;
Utilize field screening techniques;
Select parameters for which to be analyzed;
Select an appropriate sampling approach; and
Determine the locations to be sampled.
Real-time field analytical screening techniques can
be used throughout the removal action. The results
can be used to modify the site sampling plan as the
extent of contamination becomes known.
2.2 HISTORICAL DATA REVIEW
Unless the site is considered a classic emergency,
every effort should be made to first thoroughly
review relevant site information. An historical data
review examines past and present site operations
and disposal practices, providing an overview of
known and potential site contamination and other
site hazards. Sources of information include
federal, state and local officials and files (e.g., site
inspection reports and legal actions), deed or tide
records, current and former facility employees,
potentially responsible parties, local residents, and
facility records or files. For any previous sampling
efforts, obtain information regarding sample
locations (on maps, if possible), matrices, methods
of collection and analysis, and relevant contaminant
concentrations. Assess the reliability and usefulness
of existing analytical data. Even data which are not
substantiated by documentation or QA/QC controls
may still be useful.
Collect information that describes any specific
chemical processes used on site, as well as
descriptions of raw materials used, products and
wastes, and waste storage and disposal practices.
Whenever possible, obtain site maps, facility
blueprints, and historical aerial photographs,
detailing past and present storage, process, and
waste disposal locations. The local Agricultural
Extension Agent, a Soil Conservation Service (SCS)
representative, has information on soil types and
drainage patterns. County property and tax records,
and United States Geological Survey (USGS)
topographic maps are also useful sources of site and
regional information.
2.3 SITE RECONNAISSANCE
A site reconnaissance, conducted either prior to or
in conjunction with sampling, is invaluable to assess
site conditions, to evaluate areas of potential
contamination, to evaluate potential hazards
associated with sampling, and to develop a sampling
plan. During the reconnaissance, fill data gaps left
from the historical review by:
Interviewing local residents, and present or past
employees about site-related activities;
Researching facility files or records (where
records are made accessible by
owner/operator);
Performing a site entry, utilizing appropriate
personal protective equipment and
instrumentation. Observe and photo-document
the site; note site access routes; map process
and waste disposal areas such as landfills,
lagoons, and effluent pipes; inventory site
wastes; and map potential transport routes such
as ponds, streams, and irrigation ditches. Note
topographic and structural features, dead
animals and dead or stressed vegetation,
potential safety hazards, and visible label
information from drums, tanks, or other
containers found on the site.
-------
2.4 MIGRATION PATHWAYS AND
RECEPTORS
The historical review and site visit are the initial
steps in defining the source areas of contamination
which could pose a threat to human health and the
environment. This section addresses how to
delineate the spread of contamination away from
the source areas. Included are pollutant migration
pathways and the routes by which persons or the
environment may be exposed to the on-site
chemical wastes.
2.4.1 Migration Pathways and
Transport Mechanisms
Wind dispersion ~
deposited
over or adsorbed onto soil may migrate from a
waste site as airborne particulates. Depending
on the particle-size distribution and associated
settling rates, these particulates may be
deposited downwind or remain suspended,
resulting in contamination of surface soils
and/or exposure of nearby populations.
Human and animal activity - Foot and
vehicular traffic of facility workers, response
personnel, and trespassers can move
contaminants away from a source. Animal
burrowing, grazing, and migration can also
contribute to contaminant migration.
Migration pathways are routes by which
contaminants have moved or may be moved away
from a contamination source. Pollutant migration
pathways may include man-made pathways, surface
drainage, vadosc zone transport, and wind
dispersion. Human activity (such as foot or
vehicular traffic) also transports contaminants away
from a source area. These five transport
mechanisms are described below.
Man-made pathways A site located in an
urban setting has the following man-made
pathways which can aid contaminant migration:
storm and sanitary sewers, drainage culverts,
sumps and sedimentation basins, French drain
systems, and underground utility lines.
Surface drainage Contaminants can be
adsorbed onto sediments, suspended
independently in the water column, or dissolved
in surface water runoff and be rapidly carried
into drainage ditches, streams, rivers, ponds,
lakes, and wetlands. Consider prior surface
drainage routes; historical aerial photographs
can be invaluable for delineation of past surface
drainage patterns. An historical aerial
photograph search can be requested through
the EPA Regional Remote Sensing
Coordinator.
Vadose zone transport - Vadose zone transport
is the vertical or horizontal movement of water
and of soluble and insoluble contaminants
within the unsaturated zone of the soil profile.
Contaminants from a surface source or a
leaking underground storage tank can percolate
through the vadose zone and be adsorbed onto
subsurface soil or reach groundwater.
2.4.2 Receptors
Once the migration pathways have been determined,
identify all receptors (i.e., potentially affected
human and environmental populations) along these
pathways. Human receptors include on-site and
nearby residents and workers. Note the
attractiveness and accessibility of site wastes
(including contaminated soil) to children and other
nearby residents. Environmental receptors include
Federal- or state-designated endangered or
threatened species, habitats for these species,
wetlands, and other Federal- and state-designated
wilderness, critical, and natural areas.
2.5 REMOVAL PROGRAM
SAMPLING OBJECTIVES
Collect samples if any of the following Removal
Program sampling objectives in the scope of the
project are not fulfilled by existing data.
1. Establishing Threat to Public Health or
Welfare or to the Environment The
Comprehensive Environmental Response,
Compensation and Liability Act of 1980
(CERCLA) and the National Contingency Plan
(NCP) establish the funding mechanism and
authority which allow the OSC to activate a
Federal removal action. The OSC must
establish (often with sampling) that the site
poses a threat to public health or welfare or to
the environment.
2. Locating and Identifying Potential Sources of
Contamination Sample to identify the
-------
locations and sources of contamination. Use
the results to formulate removal priorities,
containment and clean-up strategies, and cost
projections.
3. Defining the Extent of Contamination - Where
appropriate, sample to assess horizontal and
vertical extent of contaminant concentrations.
Use the results to determine the site boundaries
(Lc., extent of contamination), define clean
areas, estimate volume of contaminated soil,
establish a clearly defined removal approach,
and assess removal costs and timeframe.
4. Determining Treatment and Disposal Options
Sample to characterize soil for in situ or
other on-site treatment, or excavation and off-
site treatment or disposal.
5. Documenting the Attainment of Clean-up Goals
- During or following a site cleanup, sample to
determine whether the removal goals or clean-
up standards were achieved, and to delineate
areas requiring further treatment or excavation
when appropriate.
2.6 DATA QUALITY OBJECTIVES
Data quality objectives (DQOs) state the level of
uncertainty that is acceptable from data collection
activities. DQOs also define the data quality
necessary to make a certain decision. Consider the
following when establishing DQOs for a particular
project:
Decision(s) to be made or question(s) to be
answered;
Why environmental data are needed and how
the results will be used;
Time and resource constraints on data
collection;
Descriptions of the environmental data to be
collected;
Applicable model or data interpretation method
used to arrive at a conclusion;
Detection limits for analytes of concern; and
Sampling and analytical error.
In addition to these considerations, the quality
assurance components of precision, accuracy (bias),
completeness, representativeness, and comparability
should also be considered. Quality assurance
components are defined as follows:
Precision measurement of variability in the
data collection process.
Accuracy (bias) - measurement of bias in the
analytical process. The term "bias" throughout
this document refers to the QA/QC accuracy
component.
Completeness - percentage of sampling
measurements which are judged to be valid.
Representativeness degree to which sample
data accurately and precisely represent the
characteristics of the site contaminants and
their concentrations.
Comparability - evaluation of the similarity of
conditions (e.g^ sample depth, sample
homogeneity) under which separate sets of data
are produced.
Quality assurance/quality control (QA/QC)
objectives are discussed further in chapter 5.
2.7 FIELD ANALYTICAL
SCREENING AND
GEOPHYSICAL TECHNIQUES
There are two primary types of analytical data
which can be generated during a removal action:
laboratory analytical data and field analytical
screening data. Field analytical screening
techniques (e.&, using a photoionization detector
(PID), portable X-ray fluorescence (XRF) unit, and
hazard categorization kits) provide real-time or
direct reading capabilities. These screening
methods can narrow the possible groups or classes
of chemicals for laboratory analysis and are effective
and economical for gathering large amounts of site
data. Once an area is identified using field
screening techniques, a subset of samples can be
sent for laboratory analysis to substantiate the
screening results. Under a limited sampling budget,
field analytical screening (with laboratory
confirmation) will generally result in more analytical
data from a site than will sampling for off-site
laboratory analysis alone. To minimize the
-------
potential for false negatives (not detecting on-site
contamination), use only those field analytical
screening methods which provide detection limits
below applicable action levels. It should be noted,
that some field analytical screening methods which
do not achieve detection limits below site action
levels can still detect grossly contaminated areas,
and can be useful for some sampling events.
Geophysical techniques may also be utilized during
a removal action to help depict locations of any
potential buried drums or tanks, buried waste, and
disturbed areas. Geophysical techniques include
ground penetrating radar (GPR), magnetometry,
electromagnetic conductivity (EM) and resistivity
surveys.
2.8 PARAMETERS FOR ANALYSIS
If the historical data review yields little information
about the types of waste on site, use applicable field
screening methods to narrow the parameters for
analysis by ruling out the presence of high
concentrations of certain contaminants. If the
screening results are inconclusive, send a subset of
samples from the areas of concern for a full
chemical characterization by an off-site laboratory.
It is advised that samples from known or suspected
source areas be sent to the laboratory for a full
chemical characterization so that all contaminants of
concern can be identified (even at low detection
levels), and future sampling and analysis can then
focus on those substances.
Away from source areas, select a limited number of
indicator parameters (e.g., lead, PAHs) for analysis
based on the suspected contaminants of concern.
This will result in significant cost savings over a full
chemical characterization of each sample. Utilize
EPA-approved methodologies and sample
preparation, where possible, for all requested off-
site laboratory analyses.
2.9 REPRESENTATIVE SAMPLING
APPROACHES
Selecting sampling locations for field screening or
laboratory analysis entails choosing the most
appropriate sampling approach. Representative
sampling approaches include judgmental, random,
stratified random, systematic grid, systematic
random, search, and transect sampling. A
representative sampling plan may combine two or
more of these approaches. Each approach is
defined below.
2.9.1 Judgmental Sampling
Judgmental sampling is the subjective selection of
sampling locations at a site, based on historical
information, visual inspection, and on best
professional judgment of the sampling team. Use
judgmental sampling to identify the
present at areas having the highest concentrations
(i.e., worst-case conditions). Judgmental sampling
has no randomization associated with the sampling
strategy, precluding any statistical interpretation of
the sampling results.
2.9.2 Random Sampling
Random sampling is the arbitrary collection of
samples within defined boundaries of the area of
concern. Choose random sample locations using a
random selection procedure (e.g., using a random
number table). Refer to U.S. EPA, 1984a, for a
random number table. The arbitrary selection of
sampling points requires each sampling point to be
selected independent of the location of all other
points, and results in all locations within the area of
concern having an equal chance of being selected.
Randomization is necessary in order to make
probability or confidence statements about the
sampling results. The key to interpreting these
probability statements is the assumption that the
site is homogeneous with respect to the parameters
being monitored. The higher the degree of
heterogeneity, the less the random sampling
approach will adequately characterize true
conditions at the site. Because hazardous waste
sites are very rarely homogeneous, other statistical
sampling approaches (discussed below) provide ways
to subdivide the site into more homogeneous areas.
These sampling approaches may be more
appropriate for removal activities than random
sampling. Refer to U.S. EPA, February 1989, pages
5-3 to 5-5 for guidelines on selecting sample
coordinates for random sampling. Figure 1
illustrates a random sampling approach.
2.9.3 Stratified Random Sampling
Stratifitd random sampling often relies on historical
information and prior analytical results (or field
screening data) to divide the sampling area into
smaller areas called strata. Each strata is more
-------
Rgure 1: Random Sampling
**
ffi
100-
75-
25-
I I I T I I I I I
25 50 75 100 125 150 175 200 225
FEET
Rgure 2: Stratified Random Sampling
o
IP
-------
homogeneous than the site is as a whole. Strata c* i
be defined based on various factors, including:
sampling depth, contaminant concentration levels,
and contaminant source areas. Place sample
locations within each of these strata using random
selection procedures. Stratified random sampling
imparts some control upon the sampling scheme but
still allows for random sampling within each
stratum. Different sampling approaches may also
be selected to address the different strata at the
site. Stratified random sampling is a useful and
flexible design for estimating the pollutant
concentration within each depth interval or area of
concern. Figure 2 illustrates a stratified random
sampling approach where strata are defined based
on depth. In this example, soil coring devices are
used to collect samples from given depths at
randomly selected locations within the strata.
2.9.4 Systematic Grid Sampling
Systematic grid sampling involves subdividing the
area of concern by using a square or triangular grid
and collecting samples from the nodes (intersections
of the grid lines). Select the origin and direction
for placement of the grid using an initial random
point. From that point, construct a coordinate axis
and grid over the whole site. The distance between
sampling locations in the systematic grid is
determined by the size of the area to be sampled
and the number of samples to be collected.
Systematic grid sampling is often used to delineate
the extent of contamination and to define
contaminant concentration gradients. Refer to U.S.
EPA February 1989, pages 5-5 to 5-12, for
guidelines on selection of sample coordinates for
systematic grid sampling. Figure 3 illustrates a
systematic grid sampling approach.
2.9.5 Systematic Random Sampling
Systematic random sampling is a useful and flexible
design for estimating the average pollutant
concentration within grid cells. Subdivide the area
of concern using a square or triangular grid (as
described in section 2.9.4) then collect samples from
within each cell using random selection procedures.
Systematic random sampling allows for the isolation
of cells that may require additional sampling and
analysis. Figure 4 illustrates a systematic random
sampling approach.
2.9.6 Search Sampling
Search sampling utilizes either a systematic grid or
systematic random sampling approach to search for
areas where contaminants exceed applicable clean-
up standards (hot spots). The number of samples
and the grid spacing are determined on the basis of
the acceptable level of error (i.e., the chance of
missing a hot spot). Search sampling requires that
assumptions be made about the size, shape, and
depth of the hot spots. As illustrated in figure 5,
the smaller and/or narrower the hot spots are, the
Figure 4: Systematic Random Sampling
100-
75-
! 50-
25-
l I T I I I I I I
25 50 75 100 125 150 175 200 225
FEET
After U.S. EPA, February, 1989
LEGEND
^~^~ SAMPLE AREA BOUNDARY
B SELECTED SAMPLE LOCATION
-------
smaller the grid spacing must be in order to locate
them. Also, the smaller the acceptable error of
missing hot spots is, the smaller the grid spacing
must be. This, in effect, means collecting more
samples.
Once grid spacing has been selected, the probability
of locating a hot spot can be determined Using a
systematic grid approach, table 1 lists approximate
probabilities of missing an elliptical hot spot based
on the grid method chosen as well as the
dimensions of the hot spot. The lengths of the long
and short axes (L and S) are represented as a
percentage of the grid spacing chosen. The
triangular grid method consistently shows lower
probabilities of missing a hot spot in comparison to
the block grid method. Table 1 can be used in two
ways. If the acceptable probability of missing a hot
spot is known, then the size of the hot spot which
can be located at that probability level can be
determined. Conversely, if the approximate size of
the hot spot is known, the probability of locating it
can be determined. For example, suppose the block
grid method is chosen with a grid spacing of 25 feet.
The OSC is willing to accept a 10% chance of
missing an elliptical hot spot. Using table 1, there
would be a 90% probability of locating an elliptical
hot spot with L equal to 90% of the grid spacing
chosen and S equal to 40% of the grid spacing
chosen. Therefore the smallest elliptical hot spot
which can be located would have a long axis L =
0.90 x 25ft. = 22J ft. and a short axis S = 0.40 x
25ft. = 10 ft.
Similarly, if the approximate size of the hot spot
being searched for is known, then the probability of
missing that hot spot can be determined. For
example, if a triangular grid method was chosen
with a 25 foot grid spacing and the approximate
shape of the hot spot is known, and L is
approximately 15 feet or 60% of the grid spacing,
and S is approximately 10 feet or 40% of the grid
spacing, then there is approximately a 15% chance
of missing a hot spot of this si/e and shape.
2.9.7 Transect Sampling
Transect sampling involves establishing one or more
transect lines across the surface of a site. Collect
samples at regular intervals along the transect lines
at the surface and/or at one or more given depths.
The length of the transect line and the number of
samples to be collected determine the spacing
between sampling points along the transect.
Multiple transect lines may be parallel or non-
parallel to one another. If the lines are parallel, the
sampling objective is similar to systematic grid
sampling, A primary benefit of transect sampling
over systematic grid sampling is the ease of
establishing and relocating individual transect lines
versus an entire grid. Transect sampling is often
used to delineate the extent of contamination and to
define contaminant concentration gradients. It is
also used, to a lesser extent, in compositing
sampling schemes. For example, a transect
sampling approach might be used to characterize a
Figure 5: Search Sampling
100-
75-
t 50-
u.
25 H
25 50 75 100 125 150 175 200 225
FEET
After: U.S. EPA, February, 1989
LEGEND
^"^ SAMPLE AREA BOUNDARY
3 SELECTED SAMPLE LOCATION
S^T) HOT SPOT
-------
.g.
Lu
C
CO
D)
C
CD
R
CO
o
X
TO LL
.y o
LU
O
Q
ฃ
O
LU
O
B ฃ
2 ^
_ <
"ro
cr
O
X
CO
LL
o
X
o
LU
8
g
S
R
o
8
R
3
C5
p
o
oc
^H
O
>O
8
D
E
O
x
I
CO
i
tn
a>
s
5*5
II
0} JP
CO
ONIOVdS QldO dO 3OVlN30d3d V SV SIXV 9N01 dO H19N31 I
10
-------
linear feature such as a drainage ditch. A transect
line is run down the center of the ditch, along its
full length. Sample aliquots are collected at regular
intervals along the transect line and are then
composited. Figure 6 illustrates transect sampling.
Table 2 summarizes the various representative
sampling approaches and ranks the approaches from
most to least suitable, based on the sampling
objective. Table 2 is intended to provide general
guidelines, but it cannot cover all site-specific
conditions encountered in the Removal Program.
2.10 SAMPUNG LOCATIONS
Once a sampling approach has been selected, the
next step is to select sampling locations. For
statistical (non-judgmental) sampling, careful
placement of each sampling point is important to
achieve representativeness.
Factors such as the difficulty in collecting a sample
at a given point, the presence of vegetation, or
discoloration of the soil could bias a statistical
sampling plan.
Sampling points may be located with a variety of
methods. A relatively simple method for locating
random points consists of using either a compass
and a measuring tape, or pacing, to locate sampling
points with respect to a permanent landmark, such
as a survey marker. Then plot sampling coordinates
on a map and mark the actual sampling points for
future reference. Where the sampling
demands a greater degree of precision, locate each
sample point by means of a survey. After field
sample collection, mark each sample point with a
permanent stake so that the survey team can
identify all the locations.
2.11 EXAMPLE SITE
2.11.1
Background
Information
The ABC Plating Site is located
in Carroll County, Pennsylvania,
approximately 1.5 miles north of the town of
Jonesville (figure 7). The site covers approximately
4 acres, and operated as an electroplating facility
from 1947 to 1982. During its years of operation,
the company plated automobile and airplane parts
with chromium, nickel, and copper. Cyanide
solutions were used in the plating process. ABC
Plating deposited electroplating wastes into two
shallow surface settling lagoons in the northwest
sector of the site. The county environmental health
department was attempting to enforce cleanup by
the site owner, when, in early 1982, a fire on site
destroyed most of the process building. The owner
then abandoned the facility and could not be located
by enforcement and legal authorities. The county
contacted EPA for an assessment of the site for a
possible removal action.
Figure 6: Transect Sampling
25 50 75 100 125 150 175 200 225
After: U.S. EPA, February, 1989
LEGEND
SAMPLE AREA BOUNDARY
SELECTED SAMPLE LOCATION
11
------- An error occurred while trying to OCR this image.
-------
Figure 7: Site Sketch and Phase 1 Soil Sampling Locations
ABC Plating Site
\
HOUSE
TRAILER
'FENCE
SCALE IN FEET
100 50
100
LEGEND
DAMAGED
BUILDING
AREA
+ SAMPLING LOCATIONS
SURFACE FLOW
SfTE BOUNDARY
13
-------
the ground) were leaking and bulging, doe to the
fire. TAT noted many areas of stained soil, which
indicated container leakage, poor waste handling
practices, and possible illegal dumping of wastes.
2.11.3 Identification of Migration
Pathways, Transport
Mechanisms and Receptors
During the site entry, the OSC and TAT noted that
several areas were devoid of vegetation, threatening
wind erosion which could transport heavy metal-
and cyanide-contaminated soil particulates off site.
These particulates could be deposited on residential
property downwind or be inhaled by nearby
residents.
Erosion gullies located on site indicated soil erosion
and fluvial transport due to storms. Surface
drainage sloped towards the northwest TAT
observed stressed and discolored vegetation
immediately off site, along the surface drainage
route. Surface drainage of heavy metals and
cyanide was a direct contact hazard to local
residents. Further downgradient, runoff enters an
intermittent tributary of Little Creek, Little Creek
in turn feeds Barker Reservoir, the primary water
supply for the City of Jonesville and neighboring
communities, which are located 2J> miles
downgradient of the site. The site entry team
observed that the site was not secure and there
were signs of trespass (confirming a neighbor's
claim that children play at the facility). These
activities could lead to direct contact with cyanide
and heavy metal contaminants, in addition to the
potential for chemical burns from direct contact
with strong acids and bases.
2.11.4 Sampling Objectives
The OSC selected three specific sampling objectives,
as follows:
Phase 1 - Determine whether a threat to public
health, welfare, and the environment exists.
Identify sources of contamination to support an
immediate CERCLA-funded activation for
containment of contaminants and security
fencing.
Phase 2 - Define the extent of contamination
at the site and adjacent residential properties.
Estimate the volume of pf>ntปซi inatfd soil and
the associated removal costs.
Phase 3 - After excavation (or treatment),
document the attainment of clean-up goals.
Assess that cleanup was completed to the
selected level.
2.11.5 Selection of Sampling
Approaches
The OSC selected a judgmental sampling approach
for Phase 1. Judgmental sampling supports the
Action Memorandum process by best defining on
site contaminants in the worst-case scenario in
order to evaluate the threat to human health,
welfare, and the environment. Threat is typically
established using a relatively small number of
samples (less than 20) collected from source areas,
or suspected contaminated areas based on the
historical data review and site reconnaissance. For
this site, containerized wastes were screened to
categorize the contents and to establish a worst-
case waste volume, while soil samples were
collected to demonstrate whether a release had
already occurred.
For Phase 2, a stratified systematic grid design was
selected to define the extent of contamination. The
grid can accommodate field analytical screening and
geophysical surveys and allow for contaminated soil
excavation on a cell-by-cell basis. Based on search
sampling conducted at similar sites, the hot spots
being searched for were assumed to be elliptical in
shape and 45 feet by 20 feet in size. Under these
assumptions, a block grid, with a 50 foot grid
spacing, was selected. This grid size ensured a no
more than 10% probability of missing a hot spot
(see table 1). The grid was extended to adjacent
residential properties when contaminated soil was
identified at grid points near the boundary of the
site.
Phase 3 utilized a systematic grid sampling approach
to confirm the attainment of clean-up goals.
Following cleanup, field analytical screening was
conducted on excavated soil areas using a
transportable X-ray fluorescence (XRF) unit
mounted in a trailer (mobile laboratory instrument).
Based on the results, each area was documented as
dean, or was excavated to additional depth, as
necessary.
14
-------
2.11.6 Field Analytical Screening,
Geophysical Techniques,
and Sampling Locations
During Phase 1 operations, containerized wastes
were screened using hazard categorization
techniques to identify the presence of acids, bases,
oxidizers, and flammable substances. Following this
procedure, photoionization detector (FID) and
flame ionization detector (FID) instruments, a
radiation meter, and a cyanide monitor were used
to detect the presence of volatile organic
compounds, radioactive substances, and cyanide,
respectively, in the containerized wastes. Phase 1
screening indicated the presence of strong acids and
bases and the absence of volatile organic
compounds. TAT collected a total of 12 surface soil
samples (0-3 inches) during this phase and sent
them to a laboratory for analysis. The soil sampling
locations included stained soil areas, erosion
channels and soil adjacent to leaking containers.
Background samples were not collected during
Phase 1 because they were unnecessary for
activating funding. Phase 1 sampling locations are
shown in figure 7. Based on Phase 1 analytical
results, consultation with a Regional EPA
toxicologist and with the Agency for Toxic
Substances and Disease Registry (ATSDR), an
action level of 100 ppm for chromium was selected
for cleanup.
During Phase 2 sampling activities, the OSC used a
transportable XRF unit installed in an on-site trailer
to screen samples for total chromium in order to
limit the number of samples to be sent for off-site
laboratory analysis. The transportable XRF (rather
than a portable unit) was selected for field analytical
screening to accommodate the 100 ppm action level
for chromium. Sampling was performed at all grid
nodes at the surface (0-4 inches) and subsurface
(36-40 inches) (figure 8). The 36-40 inch depth was
selected based on information obtained from county
reports and local interviews which indicated the
lagoon wastes were approximately 3 feet below
ground surface. The samples were homogenized
and sieved (discussed in chapter 4), then screened
for chromium using the XRF. The surface and
subsurface samples from areas downgradient of the
original facility (21 grid nodes) and three upgradient
(background) locations were sent for off-site
laboratory analysis following XRF screening. The
analytical results from these samples allowed for
site-specific calibration of the XRF unit. Once grid
nodes with a contamination level greater than the
selected action level were located, composite
samples were collected from each adjoining celL
Surface aliquots were collected and then
composited, sieved, thoroughly homogenized, and
screened using the XRF to pinpoint contaminated
cells. Additionally, four subsurface aliquots were
collected at the same locations as the surface
aliquots. They were also composited, sieved,
thoroughly homogenized, and screened using the
XRF. Figure 9 illustrates a Phase 2 sampling grid
cell diagram. Based on the XRF data, each
adjoining cell was either identified as dean (below
action level), or designated for excavation (at or
above action level).
For Phase 3 sampling, cleanup was confirmed by
collecting and compositing four aliquots from the
surface of each grid cell excavated during Phase 2.
The surface composites were then screened (as in
Phase 2), using the transportable XRF. Ten
percent of the screened samples were also sent to
an off-site laboratory for confirmatory sampling.
Based on the Phase 3 screening and sampling
results, each cell was documented as dean, or,
excavated to additional depth, as necessary.
During Phase 2, the OSC conducted ground
penetrating radar (GPR) and electromagnetic
conductivity (EM) geophysical surveys to help
delineate the buried trench and lagoon areas along
with any other waste burial areas. The GPR survey
was run along the north-south grid axis across the
suspected locations of the trench and lagoons.
Several structural discontinuities, defining possible
disturbed areas, were detected. One anomaly
corresponded with the suspected location and
orientation of the feeder trench. Several
discontinuities were identified in the suspected
lagoon areas; however, the data did not conclusively
pinpoint precise locations. This could be due to a
disturbance of that area during the backfilling
process by the PRP. The GPR survey is illustrated
in figure 10.
For the comprehensive EM survey, the original 50
foot grid spacing was decreased to 25 feet along the
north-south grid axis. The EM survey was run
along the north-south axes and readings were
obtained at the established grid nodes. The EM
survey was utilized throughout the site to detect the
presence of buried metal objects (e.g., buried pipe
leading to the lagoons), and potential subsurface
contaminant plumes. The EM survey identified
several high conductivity anomalies: the suspected
feeder trench location, part of the lagoon area, and
15
-------
Figure 8: Phase 2 Soil Sampling and XRF Screening Locations
ABC Plating Site
Y9
Y7
YS
YS
1
Y4
^9
i Y5
YZ
Y1
(EAST-VEST GRID COORDINATES)
DAMAGES
BUILDING
AREA
.' .'FENCE
SCALE IN FEET
100 50
100
LEGEND
XRF SCREENING LOCATION
A DOWNGRADIENT
^ SAMPLING LOCATION
^_ BACKGROUND
~ SAMPLING LOCATION
SFTE BOUNDARY
16
-------
Figure 9: Phase 2 Sampling Grid
Cell Diagram*
GRID NODE
COMPOSITE ALIQUOTS
a small area west of the process building (figure
11), which could have been an illegal waste dumping
area. Several areas of interference were
encountered due to the presence of large metal
objects at the surface (a dumpster, surface vats and
a junk car).
2.11.7 Parameters for Analysis
During Phase 1 sampling activities, full priority
pollutant metals and total cyanide analyses were
conducted on all samples. Since Phase 1 samples
were collected from the areas of highest suspected
contaminant concentration (i.e., sources and
drainage pathways), Phase 2 samples were run for
total chromium and cyanide, the only analytes
detected during the Phase 1 analyses. During Phase
3, the samples sent to the laboratory for screening
confirmation were analyzed for total chromium and
cyanide. Throughout the removal, it was not
possible to screen soils on site for cyanide, therefore
the OSC requested laboratory cyanide analysis on
the 10% confirmatory samples.
CHROMIUM ABOVE ACTION LEVEL
Surface samples should be taken over a
minimum area of one square foot. Sampling
areas for depth sampling are limited by the
diameter of the sampling equipment (e.g.,
auger, split spoon, or coring devices).
17
-------
Figure 10: GPR Survey Results
ABC Plating Site
DAMAGED
BUILDING
AREA
SCALE IN FEET
100 50 0
100
LEGEND
I STRUCTURAL
DISCONTINUITY (GPR)
SITE BOUNDARY
18
-------
Figure 11: EM-31 Survey Results
ABC Plating Site
DAMAGED
BUILDING
AREA
.' .'FENCE
SCALE IN FEET
100 50
100
LEGEND
EM-31 > 9
MILLIMHOS / METER
SFTE BOUNDARY
19
-------
3.0 EQUIPMENT
3.1 INTRODUCTION
Sample collection requires an understanding of the
capabilities of the sampling equipment, since using
inappropriate equipment may result in biased
samples. This chapter provides information for
selecting field sampling and screening equipment
3.2 FIELD ANALYTICAL
SCREENING EQUIPMENT
Field analytical screening methods provide on-site
measurements of contaminants of concern, limiting
the number of samples which need to be sent to an
off-site laboratory for time-consuming and often
costly analysis. Field screening techniques can also
evaluate soil samples for indications that soil
contamination exists (e.g., X-ray fluorescence
(XRF) for target metals or soil gas survey for
identification of buried wastes or other subsurface
contamination). All field screening equipment and
methods described in this section are portable (the
equipment is hand-held, and generally no external
power is necessary). Examples are photoionization
detectors (PID), flame ionization detectors (FID),
and some XRF devices.
Field screening generally provides analytical data of
suitable quality for site characterization, monitoring
during removal activities, and on-site health and
safety decisions. The methods presented here can
provide rapid, cost-effective, real-time data;
however, results are often not compound-specific
and not quantitative.
When selecting one field screening method over
another, consider relative cost, sample analysis time,
potential interferences or instrument limitations,
detection limit, QA/QC requirements, level of
training required for operation, equipment
availability, and data bias. Also consider which
elements, compounds, or classes of compounds the
field screening instrument is designed to analyze.
As discussed in section 2.7, the screening method
selected should be sensitive enough to minimize the
potential for false negatives. When collecting
samples for on-site analysis (e.g., XRF), evaluate
the detection limits and bias of the screening
method by sending a minimum of 10% of the
samples to an off-site laboratory for confirmation.
Table 3 summarizes the advantages and
disadvantages of selected portable field screening
equipment.
3.3 GEOPHYSICAL EQUIPMENT
Geophysical techniques can be used in conjunction
with field analytical screening to help delineate
areas of subsurface contamination, including buried
drums and tanks. Geophysical data can be obtained
relatively rapidly, often without disturbing the site.
Geophysical techniques suitable for removal
activities include: ground penetrating radar (GPR),
magnetometry, electromagnetic conductivity (EM)
and resistivity. Specific advantages and
disadvantages associated with geophysical equipment
are summarized in table 4. See also EPA ERT
Standard Operating Procedure (SOP) #2159,
General Surface Geophysics (U.S. EPA, January
1991).
3.4 SELECTING SAMPLING
EQUIPMENT
The mechanical method by which a sampling tool
collects the sample may impact representativeness.
For example, if the sampling objective is to
determine the concentrations of contaminants at
each soil horizon interface, using a hand auger
would be inappropriate: the augering technique
would disrupt and mix soil horizons, making the
precise horizon interface difficult to determine.
Depth of sampling is another factor to consider in
the proper selection of sampling equipment. A
trowel, for example, is suitable for unconsolidated
surface soils, but may be a poor choice for sampling
at 12 inches, due to changes in soil consistency with
depth.
All sampling devices should be of sufficient quality
not to contribute contamination to samples (e.g.,
painted surfaces which could chip off into the
sample). In addition, the sampling equipment
should be either easily decontaminated, or cost-
effective if considered to be expendable. Consider
ease of use when selecting sampling equipment.
Complicated sampling procedures usually require
increased training and introduce a greater likelihood
21
-------
Table 3: Portable Field Analytical Screening Equipment
Equipment
Application to
X-ray fluorescence Detects heavy metals
(portable) in soils.
Flame ionization
detector (FID)
Photoionization
detector (PID)
Field test kits
Radiation detector
Semi-quantitativery
detects VOCs in soils.
Detects total concentration
of VOCs and some non-
volatile organics and
inorganics in soils.
Detects specific elements,
compounds, or compound
classes in soils.
Detects the presence of selected
forms of radiation in soils or
other waste materials.
Rapid sample analysis; may be used in situ;
requires trained operator; potential matrix
interferences; may be used with a generic or site-
specific calibration model; detection limit may
exceed action level; detects to ppm level; detection
limit should be calculated on a site-specific basis.
Immediate results; can be used in GC mode to
identify specific organic compounds; detects VOCs
only, detects to ppm level
Immediate results; easy to use; non-compound
specific; results affected by high ambient humidity
and electrical sources such as radios; does not
respond to methane; detects to ppm level
Rapid results; easy to use; low cost; limited number
of kit types available; kits may be customized to
user needs; semi-quantitative; interferences by other
analytes is common; colorimetric interpretation is
needed; detection level dependent upon type of kit
used; can be prone to error.
Easy to use; low cost; probes for one or a
combination of alpha, beta or gamma forms of
radiation; unit and detection limits vary greatly,
detailed site surveys are time intensive and require
experienced personnel to interpret results.
Sources :
U.S. EPA, September 1988a; US. EPA, December 1987; U.S. EPA, 1987.
22
-------
Table 4: Geophysical Equipment
Equipment
Ground penetrating
radar (GPR)
Magnetometer
Electromagnetic
conductivity
meter (EM)
Wadi
Application to
Detects reflection anomalies caused
by lithology changes or buried
objects; varying depths of investi-
gation, 15 to 30 feet, are possible.
Detects presence and areal extent
of ferromagnetic material in
subsurface soils, including buried
metal containers. Single 55-gallon
drums can be identified at depths
up to 10 feet and large masses of
drums up to 30 feet or more.
Detects electrical conductivity
changes in subsurface geologic lith-
ology, pore fluids, and buried
objects. Depth of investigation
varies from 9 feet to 180 feet
depending on instrument used, coil
spacing, and coil configuration.
Detects electrical conductivity
changes in surface and sub-surface
materials utilizing existing very low
frequency (VLF) radio waves.
Advantages and Disadvantages
Capable of high resolution; generates
continuous measurement profile; can survey
large area quickly; site specific: best results are
achieved in dry, sandy soils; clay-rich and water
saturated soils produce poor reflections and
limit depth of penetration; data interpretation
requires a trained geophysicist.
Quick and easy to operate; good initial survey
instrument; readings are often affected by
nearby man-made steel structures (including
above-ground fences, buildings, and vehicles);
data interpretation may require geophysicist.
Rapid data collection; can delineate inorganic
and large-scale organic contamination in sub-
surface fluids; sensitive to man-made structures
(including buried cables, above-ground steel
structures and electrical power lines); survey
planning and data interpretation may require
geophysicist.
Utilizes existing long-distance communication
VLF radio waves (10-30 Khz range): no need to
induce electrical field; directional problems can
be overcome with portable transmitters.
Resistivity meter
Detects electrical resistivity var-
iations in subsurface materials (e.g^
lithology, pore fluids, buried pipe-
lines and drums). Vertical resol-
ution to depths of 100 feet are
possible.
Detects lateral and vertical variations;
instrument requires direct ground contact,
making it relatively labor intensive; sensitive to
outside interference; data interpretation requires
a trained geophysicist.
Sources : Benson, et. al. 1988; NJDEP, 1988.
23
-------
of procedural errors. Standard operating
procedures help to avoid such errors. Sample
volume, is another selection concern. Specific
advantages and disadvantages of soil sampling
equipment are given in table 5. Refer also to EPA
ERT SOP #2012, Soil Sampling (in U.S. EPA,
January 1991) for guidance on using various types of
soil sampling equipment.
3.5 EXAMPLE SITE
3.5.1 Selection of
Sampling
Equipment
Dedicated plastic scoops were
used for Phase 1 soil sampling. For Phase 2, the
OSC used bucket augers for both surface and
subsurface soil sampling because of their ease of
use, good vertical depth range, and uniform surface
sampling volume. Standard operating procedures
were followed to promote proper sample collection,
handling, and decontamination. From the bucket
auger, each sample was placed into a dedicated
plastic pan and mixed using a dedicated plastic
scoop. Samples were further prepared for XRF
screening and laboratory analysis (section 4.8).
3.5.2 Selection of Field Analytical
Screening Equipment
Phase 1 sampling identified the sources and types of
on-site contaminants in order to establish a threat.
Hazard categorization techniques, organic vapor
detecting instruments, and radiation and cyanide
monitors were utilized to tentatively identify
containerized liquid wastestreams in order to select
initial judgmental soil sampling locations. During
Phase 2 sampling, a portable XRF unit was used to
determine the extent of contamination and to
identify additional hot spots. Samples to be sent for
laboratory analysis were then placed into sampling
jars (as discussed in section 4.8). Samples collected
from upgradient grid nodes for XRF screening only
were stored on site for later treatment/disposal.
For Phase 3, the XRF was used to confirm whether
contaminated areas identified during Phase 2 were
sufficiently excavated.
3.5.3 Selection of Geophysical
Equipment
The GPR instrument delineated buried trench and
lagoon boundaries. The EM meter detected
subsurface conductivity changes due to buried metal
containers and contaminants. The EM-31 (a
shallower-surveying instrument than the EM-34)
was selected because expected contaminant depth
was less than 10 feet and because of the
instrument's maneuverability and ease of use.
24
-------
Table 5: Soil Sampling Equipment
Equipment
Trier
Scoop or trowel
Applicability
Soft surface soil
Soft surface soil
d
Tulip bulb planter Soft soil, 0-6 in.
Soil coring device
Soft soil, 0-24 in.
Thin-wall tube sampler Soft soil, 0-10 ft
Split spoon sampler Soil, 0 ln,-bedrock
Shelby tube sampler Soft soil, 0 in.-bedrock
Bucket auger
Hand-operated
power auger
Soft soil, 3 in.-10 ft
Soil, 6 in.-15 ft
Inexpensive; easy to use and decontaminate; difficult to use
in stony, dry, or sandy soil
Inexpensive; easy to use and decontaminate; trowels with
painted surfaces should be avoided.
Easy to use and decontaminate; uniform diameter and
sample volume; preserves soil core (suitable for VOA and
undisturbed sample collection); limited depth capability; not
useful for hard soils.
Relatively easy to use; preserves soil core (suitable for VOA
and undisturbed sample collection); limited depth capability,
can be difficult to decontaminate.
Easy to use; preserves soil core (suitable for VOA and
undisturbed sample collection); may be used in conjunction
with bucket auger, acetate sleeve may be used to help
maintain integrity of VOA samples; easy to decontaminate;
can be difficult to remove cores from sampler.
Excellent depth range; preserves soil core (suitable for VOA
and undisturbed sample collection); acetate sleeve may be
used to help maintain integrity of VOA samples; useful for
hard soils; often used in conjunction with drill rig for
obtaining deep cores.
Excellent depth range; preserves soil core (suitable for VOA
and undisturbed sample collection); tube may be used to
ship sample to lab undisturbed; may be used in conjunction
with drill rig for obtaining deep cores and for permeability
testing; not durable in rocky soils.
Easy to use; good depth range; uniform diameter and sample
volume; acetate sleeve may be used to help maintain
integrity of VOA samples; may disrupt and mix soil horizons
greater than 6 inches in thickness.
Good depth range; generally used in conjunction with bucket
auger for sample collection; destroys soil core (unsuitable for
VOA and undisturbed sample collection); requires 2 or more
equipment operators; can be difficult to decontaminate;
requires gasoline-powered engine (potential for cross-
contamination).
Sources:
NJDEP, 1988; US. EPA, January 1991.
25
-------
4.0 FIELD SAMPLE COLLECTION AND PREPARATION
4.1 INTRODUCTION
In addition to sampling equipment, field sample
collection includes sample quantity and sample
volume. Field sample preparation refers to all
aspects of sample handling after collection, until the
sample is received by the laboratory. Sample
preparation for soils may include, but is not limited
to:
removing extraneous material;
sieving samples;
homogenizing samples;
splitting samples;
compositing samples; and
final preparation.
Sample preparation depends on the sampling
objectives and analyses to be performed. Proper
sample preparation and handling help to maintain
sample integrity. Improper handling can result in a
sample becoming unsuitable for the type of analysis
required. For example, homogenizing, sieving, and
compositing samples all result in a loss of volatile
constituents and are therefore inappropriate when
volatile contaminants are the concern.
4.2 SAMPLE COLLECTION
How a sample is collected can affect its
representativeness. The greater the number of
samples collected from a site and the larger the
volume of each sample, the more representative the
analytical results will be. However, sampling
activities are often limited by sampling budgets and
project schedules. The following sections provide
guidelines on appropriate sample numbers and
volumes.
4.2.1 SAMPLE NUMBER
The number of samples needed will vary according
to the particular sampling approach that is being
used. For example, in grid sampling, one sample is
generally collected at each grid node, regardless of
grid size. As discussed in section 2.11.6, once
contaminated grid node samples are located,
adjoining grid cells can be sampled more thoroughly
to define areas of contamination. Four aliquots
from each grid cell, situated equidistant from the
sides of each cell and each other (as illustrated in
figure 9), are recommended for grid cells measuring
up to 100 x 100 feet. One additional aliquot may be
collected from the center of each cell, making a
total of five aliquots per cell For grid sizes greater
than 100 feet x 100 feet, nine aliquots, situated
equidistant from the sides of each cell and each
other (as illustrated in figure 12), are recommended.
Depending on budget and other considerations, grid
cell aliquots can be analyzed as separate samples or
composited into one or more samples per cell
4.2.2 Sample Volume
Both sample depth and area are considerations in
determining appropriate sample volume.
Depending on the analytes being investigated,
samples are collected at the surface (0-3 in.),
extended surface (0-6 in.), and/or at one-foot depth
intervals. Non-water soluble contaminants such as
dioxin and PCBs are often encountered within the
first six inches of soil. Water-soluble contaminants
such as metals, acids, ketones, and alcohols will be
encountered at deeper depths in most soils except
days. Contaminants in solution, such as PCPs in
diesel fuel and pesticides in solvents, can penetrate
to great depths (e.g., down to bedrock), depending
on soil type.
For surface samples, collect soil over a surface area
of one square foot per sample. A square cardboard
template measuring 12 in. x 12 in., or a round
template with a 12 in. diameter can be used to mark
sampling areas. For subsurface samples, one of
several coring devices may be used (see table 5).
Using a coring device results in a smaller diameter
sampling area than a surface template, and
therefore somewhat lessens the representativeness
of the sample.
4.3 REMOVING EXTRANEOUS
MATERIAL
Identify and discard materials in a field sample
which are not relevant or vital for characterizing the
sample or the site, since their presence may
introduce an error in the sampling or analytical
procedures. Examples of extraneous material in soil
samples include pieces of glass, twigs or leaves.
However, not all non-soil material is extraneous.
27
-------
Figure 12: Phase 2 Sampling Grid Cell
Diagram (Grid Sizes > 100
x 100 ft.)
GRID NODE
COMPOSITE ALIQUOTS
For example, when sampling at a junkyard, lead-
contaminated battery casing pieces should not be
removed from a sample if the casing composes
more than 10% of the sample composition. For a
sample to be representative, it must also incorporate
the lead from the casing. Collect samples of any
material thought to be a potential source of
contamination for a laboratory extraction procedure.
Discuss any special analytical requirements for
extraneous materials with project management,
geologists, and chemists and notify the laboratory of
any special sample handling requirements.
4.4 SIEVING SAMPLES
Sieving is the process of physically sorting a sample
to obtain uniform particle sizes, using sieve screens
of predetermined size. For example, the sampler
may wish to sieve a certain number of samples to
determine if particle size is related to contaminant
distribution. In the Removal Program, sieving is
generally only conducted when preparing soil
samples for XRF screening. For this purpose, a 20-
mesh screen size is recommended.
Be aware of the intent of the sampling episode,
when deciding whether to sieve a sample prior to
analysis. Prior to sieving, samples may need to be
oven-dried Discarding non-soil or non-sieved
materials, as well as the sieving process itself, can
result in physical and chemical kisses. Sieving is not
recommended where volatile compounds are of
concern. Analyze the discarded materials, or a
fraction thereof, to determine their contribution to
the contamination of the site being investigated.
4.5 HOMOGENIZING SAMPLES
Homogenization is the mixing or blending of a soil
sample in an attempt to provide uniform
distribution of contaminants. (Do not homogenize
samples for volatile compound analysis). Ideally,
proper homogenization ensures that portions of the
containerized samples are equal or identical in
composition and are representative of the total soil
sample collected. Incomplete homogenization will
increase sampling error. All samples to be
composited or split should be homogenized after all
aliquots have been combined. Manually
homogenize samples using a stainless steel spoon or
scoop and a stainless steel bucket, or use a
disposable scoop and pan. Quarter and split the
sample as illustrated in figure 12, repeating each
step a minimum of 5 times until the sample is
visually homogenized. Samples can also be
homogenized using a mechanically-operated stirring
device as depicted in ASTM standard D422-63.
4.6 SPLITTING SAMPLES
Splitting samples after collection and field
preparation into two or more equivalent parts is
performed when two or more portions of the same
sample need to be analyzed separately. Split
samples are most often collected in enforcement
actions to compare sample results obtained by EPA
with those obtained by the potentially responsible
party (PRP). Split samples also provide a measure
of the sample variability, and a measure of the
analytical and extraction errors. Before splitting,
follow homogenization techniques outlined above.
Fill two sample collection jars simultaneously with
alternate spoonfuls (or scoopfuls) of homogenized
sample. To simultaneously homogenize and split a
sample, quarter (as illustrated in figure 13) or
mechanically split the sample using a riffle sample
splitter. The latter two techniques are described in
detail in ASTM Standard C702-87.
28
-------
Figure 13: Quartering to Homogenize and Split Samples
Stepl:
Cone Sample on Hard Clean Surface
Mix by Forming New Cone
Step 2:
Quarter After Flattening Cone
Step 3:
Divide Sample
into Quarters
Step 4:
Remix Opposite Quarters
Reform Cone
Repeat a Minimum of 5 Times
After ASTM Standard C702-87
4.7 COMPOSITING SAMPLES
Compositing is the process of physically combining
and homogenizing several individual soil aliquots.
Compositing samples provides an average
concentration of contaminants over a certain
number of sampling points, which reduces both the
number of required lab analyses and the sample
variability. Compositing can be a useful technique,
but must always be implemented with caution.
Compositing is not recommended where volatile
compounds are of concern.
Specify the method of selecting the aliquots that are
composited and the compositing factor in the
sampling plan. The compositing factor is the
number of aliquots to be composited into one
sample (e.g., 3 to 1; 10 to 1). Determine this factor
by evaluating detection limits for parameters of
interest and comparing them with the selected
action level for that parameter. Compositing also
requires that each discrete aliquot be the same in
terms of volume or weight, and that the aliquots be
thoroughly homogenized. Since compositing dilutes
high concentration aliquots, the applicable detection
limits should be reduced accordingly. If the
composite value is to be compared to a selected
action level, then the action level must be divided by
the number of aliquots that make up the composite
in order to determine the appropriate detection
limit (e.g., if the action level for a particular
substance is SO ppb, an action level of 10 ppb
should be used when analyzing a 5-aliquot
composite). The detection level need not be
reduced if the composite area is assumed to be
homogeneous in concentration (for example, stack
emission plume deposits of particulate
contamination across an area, or roadside spraying
of waste oils).
29
-------
4.8 FINAL PREPARATION
Select sample containers on the basis of
compatibility with the material being sampled,
resistance to breakage, and volume. For soil
sampling, use wide-mouth glass containers with
Teflon-lined lids. Appropriate sample volumes and
containers will vary according to the parameter
being analyzed. Keep low and medium
concentration soil samples to be analyzed for
organic constituents at 4ฐC. Actual sample volumes,
appropriate containers, and holding times are
specified in the QA/QC Guidance for Removal
Activities (U.S. EPA, April 1990), in 40 CFR 136,
and in the Compendium of ERT Soil Sampling and
Surface Geophysics (U.S. EPA, January 1991).
Package all samples in compliance with Department
of Transportation (DOT) or International Air
Transport Association (IATA) requirements.
It is sometimes possible to ship samples to the
laboratory directly in the sampling equipment. For
example, the ends of a Shelby tube can be sealed
with caps, taped, and sent to the laboratory for
analysis. To help maintain the integrity of VOA
samples, collect soil cores using acetate sleeves and
send the sleeves to the laboratory. To ensure the
integrity of the sample after delivery to the
laboratory, make laboratory sample preparation
procedures part of all laboratory bid contracts.
4.9 EXAMPLE SITE
After placing each sample in a
dedicated pan and mhring (as
discussed in section 3.5.1), plant
matter, stones, and broken glass
were removed. Soil samples
were oven-dried (at 104* C) and sieved using a 20-
mesh screen in preparation for XRF analysis.
Samples were then homogenized and split using the
quartering technique. Opposite quarters were
remixed and quartering was repeated five times to
ensure thorough homogenization. A portion of
each sample was placed into XRF analysis cups for
screening. The remainder of each sample was
placed into 8-ounce, wide-mouth glass jars with
Teflon-lined lids and sent to a laboratory for
inorganic analysis. The samples were packaged in
compliance with IATA requirements. Chain-of-
custody paperwork was prepared for the samples.
Laboratory paperwork was completed as
appropriate and the samples were shipped to the
predesignated laboratories for analysis.
30
-------
5.0 QUALITY ASSURANCE/QUALITY CONTROL EVALUATION
5.1 INTRODUCTION
The goal of representative sampling is to collect
samples which yield analytical results that accurately
depict site conditions during a given time frame.
The goal of quality assurance/quality control
(QA/QC) is to identify and implement correct
methodologies which limit the introduction of error
into the sampling and analytical procedures,
ultimately affecting the analytical data.
QA/QC samples evaluate the degree of site
variation, whether samples were cross-contaminated
during sampling and sample handing procedures, or
if a discrepancy in sample results is due to
laboratory handling and analysis procedures.
The QA/QC sample results are used to assess the
quality of the analytical results of waste and
environmental samples collected from a site.
5.2 QA/QC OBJECTIVES
Three QA/QC objectives (QA1, QA2, and QA3)
have been defined by the Removal Program, based
on the EPA QA requirements for precision,
accuracy (bias), representativeness, completeness,
comparability, and detection level. The QA1
objective applies when a large amount of data are
needed quickly and relatively inexpensively, or when
preliminary screening data, which do not need to be
analytc or concentration specific, are useful. QA1
requirements are used with data from field
analytical screening methods, for a quick,
preliminary assessment of site contamination.
Examples of QA1 activities include: determining
physical and/or chemical properties of samples;
assessing preliminary on-site health and safety,
determining the extent and degree of contamination;
assessing waste compatibility, and characterizing
hazardous wastes.
QA2 verifies analytical results. The QA2 objective
intends to provide a certain level of confidence for
a select portion (10% or more) of the preliminary
data. This objective allows the OSC to use field
screening methods to quickly focus on specific
pollutants and concentration levels, while at the
same time requiring laboratory verification and
quality assurance for at least 10% of the samples.
QA2 verification methods are analytc specific.
Examples of QA2 activities include: defining the
extent and degree of contamination; verifying site
cleanup; and verifying screening objectives
obtainable with QA1, such as pollutant
identification.
QA3 assesses the analytical error of the
concentration level, as well as the identity of the
anaryte(s) of interest. QA3 data provide the highest
degree of qualitative and quantitative accuracy and
confidence of ail QA objectives by using rigorous
methods of laboratory analysis and quality
assurance. Examples of QA3 activities include:
selecting treatment and disposal options; evaluating
health risk or environmental impact; verifying
cleanup; and identifying pollutant source. The QA3
objective should be used only when determination
of analytical precision in a certain concentration
range is crucial for decision-making.
5.3 SOURCES OF ERROR
Identifying and quantifying the error or variation in
sampling and laboratory analysis can be difficult
However, it is important to limit their effect(s) on
the data. Four potential sources of error are:
sampling design;
sampling methodology,
sample heterogeneity, and
analytical procedures.
5.3.1 Sampling Design
Site variation includes the variation both in the
types and in the concentration levels of
contaminants throughout a site. Representative
sampling should accurately identify and define this
variation. However, error can be introduced by the
selection of a sampling design which "misses" site
variation. For example, a sampling grid with
relatively large distances between sampling points or
a biased sampling approach (i.e., judgmental
sampling) may allow significant contaminant trends
to go unidentified, as illustrated in figure 14.
31
-------
Figure 14: Sampling Error Due
to Sampling Design
LEGEND
X SAMPLING POINTS
CONTAMINATED SOIL
SOURCE OF CONTAMINATION
5.3.2 Sampling Methodology
Error can be introduced by the sampling
methodology and sample handling procedures, as in
cross-contamination from inappropriate use of
sample collection equipment, unclean sample
containers, improper sampling equipment
decontamination and shipment procedures, and
other factors. Standardized procedures for
collecting, handling and shipping samples allow for
easier identification of the source(s) of error, and
can limit error associated with sampling
methodology. The use of standard operating
procedures ensures that all sampling tasks for a
given matrix and anatyte will be performed in the
same manner, regardless of the individual sampling
team, date, or location of sampling activity. Trip
blanks, field blanks, replicate samples, and rinsate
blanks are used to identify error due to sampling
methodology and sample handling procedures.
5.3.3 Sample Heterogeneity
Sample heterogeneity is a potential source of error.
Unlike water, soil is rarely a homogeneous medium
and it exhibits variable properties with lateral
distance and with depth. This heterogeneity may
also be present in the sample container unless the
sample was homogenized in the field or in the
laboratory. The laboratory uses only a small aliquot
of the sample for analysis; if the sample is not
properly homogenized, the analysis may not be truly
representative of the sample and of the
corresponding site. Thoroughly homogenizing
samples, therefore, can limit error associated with
sample heterogeneity.
5.3.4 Analytical Procedures
Error which may originate in analytical procedures
includes cross-contamination, inefficient extraction,
and inappropriate methodology. Matrix spike
samples, replicate samples, performance evaluation
samples, and associated quality assurance evaluation
of recovery, precision, and bias, can be used to
distinguish analytical error from error introduced
during sampling activities.
5.4 QA/QC SAMPLES
This section briefly describes the types and uses of
QA/QC samples that are collected in the field, or
prepared for or by the laboratory. QA/QC samples
are analyzed in addition to field samples and
provide information on the variability and usability
of environmental sample results. They assist in
identifying the origin of analytical discrepancies to
help determine how the analytical results should be
used. They are used mostly to validate analytical
results. Field replicate, collocated, background, and
rinsate blank samples are the most commonly
collected field QA/QC samples. Performance
evaluation, matrix spike, and matrix spike duplicate
samples, either prepared for or by the laboratory,
provide additional measures of control for the data
generated. QA/QC results may suggest the need
for modifying sample collection, preparation,
handling, or analytical procedures if the resultant
data do not meet site-specific quality assurance
objectives. Refer to data validation procedures in
U.S. EPA, April 1990, for guidelines on utilizing
QA/QC analytical results. The following
paragraphs briefly describe each type of QA/QC
sample.
32
-------
5.4.1 Field Replicates
Field replicates are field samples obtained from one
location, homogenized, divided into separate
containers and treated as separate samples
throughout the remaining sample handling and
analytical processes. These samples are used to
assess error associated with sample heterogeneity,
sample methodology and analytical procedures. Use
field replicates when determining total error for
critical samples with contamination concentrations
near the action level For statistical analysis to be
valid in such a case, a minimum of eight replicate
samples would be required.
5.4.2 Collocated Samples
Collocated samples are collected adjacent to the
routine field sample to determine local variability of
the soil and contamination at the site. Typically,
collocated samples are collected about one-half to
three feet away from the selected sample location.
Analytical results from collocated samples can be
used to assess site variation, but only in the
immediate sampling area. Due to the non-
homogeneous nature of soil at sites, collocated
samples should not be used to assess variability
across a site and are not recommended for assessing
error. Determine the applicability of collocated
samples on a site-by-site basis. Collecting many
samples (more than 50 samples/acre), is sufficient
to demonstrate site variation.
5.4.3 Background Samples
Background samples are collected upgradient of the
area(s) of contamination (either on or off site)
where there is little or no chance of migration of
the contaminants of concern. Background samples
determine the natural composition of the soil
(especially important in areas with high
concentrations of naturally-occurring metals) and
are considered "clean" samples. They provide a
basis for comparison of contaminant concentration
levels with samples collected on site. At least one
background soil sample should be collected;
however, more are warranted when site-specific
factors such as natural variability of local soil,
multiple on-site contaminant source areas, and
presence of off-site facilities potentially contributing
to soil contamination exist. Background samples
may be collected for all QA objectives, in order to
evaluate potential error
associated with sampling design, sampling
methodology, and analytical procedures.
5.4.4 Rlnsate Blanks
Rinsate blanks are samples obtained by running
analyte-free water over decontaminated sampling
equipment to test for residual contamination. The
blank is placed in sample containers for handling,
shipment, and analysis identical to the 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 type of sampling device, per day
to meet QA2 and QA3 objectives.
5.4.5 Performance Evaluation
Samples
Performance evaluation (PE) samples evaluate the
overall bias of the analytical laboratory and detect
any error in the analytical method used. These
samples are usually prepared by a third party, using
a quantity of analyte(s) which is known to the
preparer but unknown to the laboratory, and always
undergo certification analysis. The analyte(s) used
to prepare the PE sample is the same as the
analyte(s) of concern. Laboratory procedural error
is evaluated by the percentage of analyte identified
in the PE sample (percent recovery). Even though
they are not available for all analytes, PE samples
are required to achieve QA3 objectives. Where PE
samples are unavailable for an analyte of interest,
QA2 is the highest QA standard achievable.
5.4.6 Matrix Spike Samples
Matrix spike and matrix spike duplicate samples
(MS/MSDs) are environmental samples that are
spiked in the laboratory with a known concentration
of a target analyte(s) to verify percent recoveries.
MS/MSDs are primarily used to check sample
matrix interferences. They can also be used to
monitor laboratory performance. However, a
dataset of at least three or more results is necessary
to distinguish between laboratory performance and
matrix interference.
MS/MSDs can also monitor method performance.
Again, a dataset is helpful to assess whether a
method is performing property. Generally,
33
-------
interference and poor method performance go
together.
MS/MSDs can also evaluate error due to laboratory
bias and precision (when four or more pairs are
analyzed). Analyze one MS/MSD pair to assess
bias for every 20 soil samples. Use the average
percent recovery for the pair. To assess precision,
analyze at least 8 matrix spike replicates from the
same sample, determine the standard deviation and
the coefficient of variation. See pages 9 - 10 of the
QA/QC Guidance for Removal Activities (U.S. EPA,
April 1990) for procedures on calculating analytical
error. MS/MSDs are optional for QA2 and
required to meet QA3 objectives as one of several
methods to determine analytical error.
5.4.7 Field Blanks
Field blanks are samples prepared in the field using
certified dean sand or soil and are then submitted
to the laboratory for analysis. A field blank is used
to evaluate contamination error associated with
sampling methodology and laboratory procedures.
If available, submit field blanks at a rate of one per
day.
5.4.8 Trip Blanks
Trip blanks are samples prepared prior to going
into the field. Trip blanks consist of certified clean
sand or soil and are handled, transported, and
analyzed in the same manner as the other volatile
organic samples acquired that day. Trip blanks are
used to evaluate error associated with sampling
methodology and analytical procedures by
determining if any contamination was introduced
into samples during sampling, sample handling and
shipment, and/or during laboratory handling and
analysis. If available, utilize trip blanks to meet
QA2 and QA3 objectives for volatile organic
analyses only.
5.5 EVALUATION OF ANALYTICAL
ERROR
The percentage and types of QA/QC samples
needed to help identify the error and confidence in
the data is based on the sampling objectives and the
corresponding QA/QC objectives. The acceptable
level of error is determined by the intended use of
the data and the sampling objectives, including such
factors as: the degree of threat to public health,
welfare, or the environment; selected action levels;
litigation concerns; and budgetary constraints.
The use of replicate samples is one method to
evaluate error. To evaluate the total error of
samples with contaminant concentrations near the
selected action level, prepare and analyze a
minimum of eight replicates of the same sample.
Analytical data from replicate samples can also be
used for a quick check on errors associated with
sample heterogeneity, sample methodology and
analytical procedures. Differing analytical results
from two or more replicate samples could indicate
improper sample preparation (e.g., incomplete
homogenization), or that contamination was
introduced during sample collection, preparation,
, shipment, or analysis.
It may be desirable to try to quantify confidence;
however, quantification or analytical data correction
is not always possible. A 95% confidence level (i.e.,
5% acceptable error) should be adequate for most
Removal Program sampling activities. Experience
will provide the best determination of whether to
use a higher (e.g., 99%) or lower (e.g., 90%) level
of confidence. It must be recognized that the use of
confidence levels is based on the assumption that a
sample is homogeneous. See also section 6.8 for
information on total error.
5.6 CORRELATION BETWEEN
FIELD SCREENING RESULTS
AND CONFIRMATION RESULTS
One cost-effective approach for delineating the
extent of site contamination is to correlate
inexpensive 5eld screening data and other field
measurements (e.g., XRF, soil-gas measurements)
with laboratory results. The relationship between
the two methods can then be described by a
regression analysis and used to predict laboratory
results based on field screening measurements. In
this manner, cost-effective field screening results
may be used in addition to, or in lieu of, off-site
laboratory sample analysis.
Statistical regression involves developing a model
(equation) that relates two or more variables at an
acceptable level of correlation. When field
screening techniques, such as XRF, are used along
with laboratory methods (e.g., atomic absorption
(AA)), a regression equation can be used to predict
a laboratory value based on the results of the
34
-------
screening device. The model can also be used to
place confidence limits around predictions.
Additional discussion of correlation and regression
can be found in most introductory statistics
textbooks. A simple regression equation (e.g.,
linear) can be developed on many calculators or
computer databases; however, a statistician should
be consulted to check the accuracy of more complex
models.
Evaluation of the accuracy of a model in part relies
on statistical correlation. Statistical correlation
involves computing an index called the correlation
coefficient (r) that indicates the degree and nature
of the relationship between two or more sets of
values. The correlation coefficient ranges from
-1.0 (a perfect inverse or negative relationship),
through 0 (no relationship), to +1.0 (a perfect
direct, or positive, relationship). The square of the
correlation coefficient, called the coefficient of
determination, or simply R2, is an estimate of the
proportion of variance in one variable (the
dependent variable) that can be accounted for by
the independent variables. The R2 value that is
acceptable depends on the sampling objectives and
intended data uses. As a rule of thumb, statistical
relationships should have an R2 value of at least 0.6
to determine a reliable model; however, for health
or risk assessment purposes, the acceptable R2 value
may be made more stringent (e.g., 0.8). Analytical
calibration regressions have an R2 value of 0.98 or
better.
Once a reliable regression equation has been
derived, the field screening data can be used to
predict laboratory results. These predicted values
can then be located on a base map and contoured
(mapping methods are described in chapter 6).
These maps can be examined to evaluate the
estimated extent of contamination and the adequacy
of the sampling program.
5.7 EXAMPLE SITE
The field screening of
containerized liquid wastes
performed during Phase 1
utilized the QA1 objective. The
purpose of this screening was to
quickly obtain data indicating general chemical
class. The screening did not need to be analyte or
concentration specific nor was confirmation of the
results needed. The Phase 1 sampling was
performed according to the QA2 objective. The
analyses were analyte and concentration specific.
Confirmational analysis was run on 10% of the
samples in order to verify screening results.
Recoveries of matrix spike and matrix spike
duplicate samples indicated no matrix interferences.
Dedicated equipment was used during Phase 1
sampling, making rinsate blanks unnecessary. Phase
2 field screening (XRF) was performed according to
the QA2 objective. During Phase 2, samples were
collected at 30% of the nodes screened with the
XRF. These samples were sent for laboratory AA
analysis. A correlation was established by plotting
the Phase 2 AA and XRF data. This allowed the
XRF data from the other 70% of the nodes to be
used to evaluate the chromium levels across the site.
For Phase 2 and 3 sampling, 10% of the data were
confirmed by running replicate analyses to obtain an
estimate of precision. The results indicated good
correlation. Matrix spikes and matrix spike
duplicate samples indicated no matrix interferences.
During Phase 2, the OSC opted to include
performance evaluation (PE) samples for metals to
evaluate the overall laboratory bias (although not
required for QA2 data quality). The laboratory
achieved 92% recovery, which was within the
acceptable control limits.
During Phases 2 and 3, a rinsate blank was
collected each day. Following the decontamination
of the bucket augers, analyte-free water was poured
over the augers and the rinsate was placed into 1-
liter polyethylene bottles and preserved. The
rinsate blanks were analyzed for total metals and
cyanide to determine the effectiveness of the
decontamination procedures and the potential for
cross-contamination. All rinsate blank samples
were "dean", indicating sufficient decontamination
procedures.
The correlation analysis run on Phase 2 laboratory
(AA) data and corresponding XRF values resulted
in r values of 0.97 for both surface and subsurface
data, which indicated a strong relationship between
the AA and XRF data. Following the correlation
analyses, regression analyses were run and equations
to predict laboratory values based on the XRF data
were developed. The resulting equation for the
surface data was: AA = 0.87 (XRF) + 10.16. The
resulting regression equation for the subsurface data
was: AA * 0.94 (XRF) + 030.
35
-------
6.1 INTRODUCTION
Data presentation and analysis techniques are
performed with analytical, geophysical, or Geld
screening results. The techniques discussed below
can be used to compare analytical values, to
evaluate numerical distribution of data, to
determine and illustrate the location of hot spots
and the extent of contamination across a site, and to
assess the need for removal of contaminated soil
with concentrations at or near the action level The
appropriate methods to present and analyze sample
data depend on the sampling objectives, the number
of samples collected, the sampling approaches used,
and a variety of other considerations.
6.2 DATA POSTING
Data posting involves placement of sample values
on a site basemap. Data posting is useful for
displaying the spatial distribution of sample values
to visually depict extent of contamination and to
locate hot spots. Data posting requires each sample
to have a specific location (e.&, X and Y
coordinates). Ideally, the sample coordinates would
be surveyed values to facilitate placement on a
scaled map.
between sample points. Contour lines can be drawn
manually or be generated by computer using
contouring software. Although the software makes
the contouring process easier, computer programs
have a limitation: they may interpolate between all
data points, attempting to fit a contour interval to
the full range of data values. This can result in a
contour map that does not accurately represent
general site contaminant trends. Typical removal
sites have low concentration/non-detect areas and
hot spots. Computer contouring programs may
represent these features as in figure IS which
illustrates a site that has a 4000 mg/kg hot spot.
Because there is a large difference in concentration
between the hot spot and the surrounding area, the
computer contouring program used a contour
interval that eliminated most of the subtle site
features and general trends. However, if that same
hot spot concentration value is posted at a reduced
value, then the contouring program can select a
more appropriate contour interval to better
illustrate the general site trends. Figure 16 depicts
the same site as in figure 15 but the hot spot
concentration value has been arbitrarily posted at
1400 mg/kg. The map was recontoured and the
contouring program selected a contour interval that
resulted in a map which enhanced the subtle detail
and general site contaminant trends.
6.3 GEOLOGIC GRAPHICS
Geologic graphics include cross-sections and fence
diagrams, which are two- and three-dimensional
depictions, respectively, of soils and strata to a given
depth beneath the site. These types of graphics are
useful for posting subsurface analytical data as well
as for interpreting subsurface geology and
contaminant migration.
6.4 CONTOUR MAPPING
Contour maps are useful for depicting contaminant
concentration values throughout a site. Contour
mapping requires an accurate, to-scale basemap of
the site. After data posting sample values on the
basemap, insert contour lines (or isopleths) at a
specified contour interval, interpolating values
6.5 STATISTICAL GRAPHICS
The distribution or spread of the data set is
important in determining which statistical
techniques to use. Common statistical analyses such
as the t-test relies on normally distributed data.
The histogram is a statistical bar graph which
displays the distribution of a data set. A normally
distributed data set takes the shape of a bell curve,
with the mean and median close together about
halfway between the maximum and minimum
values. A probability plot depicts cumulative
percent against the concentration of the
contaminant of concern. A normally distributed
data set, when plotted as a probability plot, would
appear as a straight line. Use a histogram or
probability plot to see trends and anomalies in the
data prior to conducting more rigorous forms of
statistical analysis.
37
-------
Figure 15: Computer Generated Contour Map (4000 mg/kg Hot Spot)
ABC Plating Site
EAST-UEST COORDINATES
Total Chromium Concentration
Units - mg/kg
Contour Interval - 100 mg/kg
Includes 4000 mg/kg Hot Spot
Figure 16: Computer Generated Contour Map (1400 mg/kg Hot Spot)
ABC Plating Site
Total Chromium Concentration
Units = mg/kg
Contour interval * 100 mg/kg
Includes 1400 mg/kg Hot Spot*
EAST-UEST COORDINATES
1400 mg/kg hot spot is substituted for
4000 mg/kg hot spot (see section 6.4
- Contour Mapping)
-------
6.6 GEOSTATISTICS
6.8 UTILIZATION OF DATA
Geostatistical methods are useful for data analysis
and presentation. The characteristic feature of
geostatisdcs is the use of variograms to quantify and
model the spatial relationship between values at
different sampling locations and for interpolating
(e.g^ kriging) estimated values across a site. The
geostatistical analysis can be broken down into two
phases. First, a model is developed that describes
the spatial relationship between sample locations on
the basis of a plot of spatial variance versus the
distance between pairs of samples. This plot is
called a variogram. Second, the spatial relationship
modeled by the variogram is used to compute a
weighted-average interpolation of the data. The
result of geostatistical mapping by data interpolation
is a contour map that represents estimates of values
across a site, and maps depicting potential error in
the estimates. The error maps are useful for
deciding if additional samples are needed and for
calculating best or worst-case scenarios for site
cleanup. More information on geostatistics can be
found in U.S. EPA, September 1988b and U.S.
EPA, 1990. Geo-EAS and GEOPACK,
geostatistical environmental assessment software
packages developed by U.S. EPA, can greatly assist
with geostatistical analysis methods.
6.7 RECOMMENDED DATA
INTERPRETATION METHODS
The data interpretation method chosen depends on
project-specific considerations, such as the number
of sampling locations and their associated range in
values. A site depicting extremely low data values
(e.g., non-detects) with significantly higher values
(e.g., 5,000 ppm) from neighboring hot spots, with
little or no concentration gradient in-between, does
not lend itself to contouring and geostatistics,
specifically the development of variograms.
However, data posting would be useful at such a
site to illustrate hot spot and clean areas.
Conversely, geostatistics and contour mapping, as
well as data posting, can be applied to site data with
a wide distribution of values (i.e., depicting a "bell
shaped" curve) with beneficial results.
When conducting search sampling to determine the
locations of hot spots (as discussed in section 2.9),
analyze the data using one of the methods discussed
in this chapter. For each node that is determined to
be close to or above the action level, the following
procedure is recommended.
Investigate all neighboring grid cells to determine
which areas must be excavated and/or treated.
From each grid cell, take a composite sample
consisting of four or more aliquots, using the
procedure described in section 2.11.6. Grid cells
with contaminant concentrations significantly above
the action level (e.g^ 20%) should be marked for
removal. Grid cells with contaminant
concentrations significantly less than the action level
should be designated as clean. For grid cells with
contaminant concentrations close to the action level,
it is recommended that additional sampling be done
within that grid cell to determine whether it is truly
a hot spot, or whether the analytical result is due to
sampling and/or analytical procedural error. If
additional sampling is to be performed, one of the
following methods should be considered:
Collect a minimum of four grab samples within
the grid cell in question. Use these samples to
develop a 95% confidence interval around the
mean concentration. If the action level falls
within or below this confidence interval, then
consider removal/treatment of the soil within
that grid celL More information on confidence
intervals and standard deviation can be found
in Gilbert, 1987.
Collect additional composite samples from the
grid cells in question using the technique
discussed in section 2.11.6. From these
additional samples, determine the need for
removal/treatment.
These two practical approaches help to determine
the total error associated with collecting a sample
from a non-homogeneous site. Total error includes
design error, sampling error, non-homogeneous
sampling error, and analytical error.
If additional sampling is being considered, weigh the
cost-effectiveness of collecting the additional
samples versus removing the soil from the areas in
question. This decision must be made on a site-by-
site basis.
39
-------
After removal/treatment of the contaminated soil,
re-investigate the grid cells to verify cleanup below
the action level Each grid cell that had soil
removed must either be composite sampled again,
or have multiple grab samples collected with a 95%
confidence interval set up again. Again, this
decision must be made on a site-by-site basis. The
methodology should be repeated until all grid cells
are determined to have soil concentrations below
the action level
6.9 EXAMPLE SITE
The Phase 2 XRF/atomic
absorption (AA) data were
examined to determine the
appropriate data interpretation
method to use. A histogram
was generated to illustrate the distribution of the
data as depicted in figure 17. The histogram
showed an uneven distribution of the data with most
values less than 50 (approximately 4 on the LN
scale of the histogram). Also, the presence of a
single data point of 4000 (8 on the LN scale) was
shown on the histogram. The data were initially
posted as illustrated in figures 18 and 19. Data
posting was performed manually to give the OSC a
quick depiction of the general site contamination
trends. A contour mapping program was used to
generate contours based on the posted data. Figure
15 illustrates the results of contouring with the 4000
mg/kg hot spot included. This contour map
exaggerated the hot spot while eliminating the
subtle site features and contaminant trends. Figure
16 depicts the same site data with the hot spot
arbitrarily reduced to 1400 mg/kg. The resulting
contour map enhanced more of the subtle site
features and trends while reducing the effects of the
hot spot.
AA concentrations predicted by the regression
equations were kriged and contoured using Gco-
EAS (figures 20 and 21). Both the kriged contours
and the data posting showed the same general site
contaminant trends. However, data posting gave a
more representative depiction of actual levels of
contamination and the OSC used data posting for
decision-making.
For each node with chromium concentrations dose
to or above the 100 ppm action level the adjacent
grid cells were further investigated. Composite
samples consisting of four aliquots of soil were
taken from within each grid cell in question and
analyzed. If the soil concentration level was
below 100 ppm of chromium, the cell
was designated as clean. Each cell that had a soil
concentration level well above the action level was
marked for treatment/removal. Any cells having
soil concentrations close to the action level were
sampled further using the compositing method to
better quantify the actual contaminant
concentration. Since the surrounding area is
residential, on-site landfilling was not considered a
viable treatment option. To expedite
treatment/disposal, all excavated soil from
contaminated cells was stockpiled on site until
treatment/disposal could be accomplished under a
fixed-price contract. The stockpile, placed in the
area of the most highly contaminated grid cells
(where the lagoons were located), was covered until
treatment/disposal could be arranged. Cleanup was
verified with composite sampling in the excavated
cells. Results of the composite sampling were
compared with the action level to verify cleanup.
All action levels were met. The excavation pits
were filled with stone and clean soil covered with
topsoU, graded and seeded.
40
-------
Rgure 17: Histogram of Surface Chromium Concentrations
ABC Plating Site
His to gran
Data file: kri-jsurf .dat Statistics
i ;; i , H T.,*,.! CQ
48.
id
JW
a
9
e
t
y 28.
1
*
18.
* '
0
3
N Hiss 8
N Used 59
Mean 4.368
Variance 1.426
Std. Dev 1.194
X C.U. 27.771
Skeuness 1.219
Kurtosis 3.712
Mininun 3.462
25th x 3.462
Median 3.462
75th X 5.084
tlaximin 8.299
6. 9. 12.
UK CHROMIUM)
41
-------
Figure 18: Phase 2 Surface Data Posting for Chromium
ABC Plating Site
rr
ง
D
rr
DAMAGED
BUILDING
AREA
.i.l...ป..;9:Xซ....J3 X4....XS XR....XZ
.*- GATE (EAST-VEST GRID CDORfllNATTS)
FENCE
I I
SCALE IN FEET
100 50
100
LEGEND
< 100 ppm
100 - 500 ppm
> 500 ppm
SFTE BOUNDARY
42
-------
Figure 19: Phase 2 Subsurface Data Posting for Chromium
ABC Plating Site
rr
I"
3
rs
a
ง
x Y4
n
'~".GATE (EAST-VEST GRIB
DAMAGE!]
BUILDING
AREA
I I
SCALE IN FEET
100 50
10Q
LEGEND
< 100 ppm
100 - 500 ppm
> 500 ppm
SITE BOUNDARY
43
-------
Figure 20: Contour Map of Surface Chromium Data (ppm)
ABC Plating Site
360.
300.
290.
200.
100.
100.
SOJ3
50.0'
40.0-
100. ISO. 200. 290. 300. 390. 4OO.
Eoซt-Wซซt Grid Coordinate*
Figure 21: Contour Map of Subsurface Chromium Data (ppm)
ABC Plating Site
400.
390.
300.
250.
200.
190.
100.
904)
10O. 190. 200. 290. 30O. 390. 400.
44
-------
References
American Society for Testing and Materials. 1987. Standard Practice for Reducing Field Samples of Aggregate
to Testing Size. ASTM C702-87.
American Society for Testing and Materials. 1972. Standard Method for Particle-Size Analysis of Soils. ASTM
D422-63.
Barth, Delbert. 1987. Statistical Considerations to Include the Importance of a Statistics Design for Soil
Monitoring Programs. Proc. Third Annual Solid Waste Testing and Quality Assurance Symposium,
Washington D.C., July 13-17, 1987.
Benson, R., Robert A. Glaccum, and Michael R. NoeL 1988. Geophysical Techniques for Sensing Buried Wastes
and Waste Migration. National Water Well Association: Ohio.
Brady, Nyle C. 1974. The Nature and Properties of Soils. 8th ed. McMillan: New York.
Clark, I. 1979. Practical Geostatistics. Elsevier Science: New York.
Flatman, George T. 1987. QA/QC Considerations to Include Types and Numbers of Samples: Proc Third
Annual Waste Testing and Quality Assurance Symposium, Washington, D.C., July 13-17, 1987.
Gilbert, Richard O. 1987. Statistical Methods for the Environmental Pollution Monitoring. Pacific Northwest
Laboratory. Van Nostrand Reinhold: New York.
Gy, P.M. 1982. Sampling of Particulate Material. Elsevien Amsterdam.
Jernigan, R.W. 1986. A Primer on Kriging. Washington, D.C.: U.S. EPA Statistical Policy Branch. 83 pp.
Journal, A.G. 1989. Geostatistics for the Environmental Sciences. (Draft). Las Vegas: U.S. EPA Environmental
Monitoring Systems Laboratory. 135 pp.
New Jersey Department of Environmental Protection. February 1988. Field Sampling Procedures Manual.
Taylor, J.K. 1987. Quality Assurance of Chemical Measurements.
U.S. Environmental Protection Agency. Office of Emergency and Remedial Response. January 1991.
Compendium of ERT Soil Sampling and Surface Geophysics Procedures. Interim Final. OSWER Directive
9360.4-02.
U.S. Environmental Protection Agency. Office of Emergency and Remedial Response. April 1990. Quality
Assurance/Quality Control Guidance for Removal Activities: Sampling QA/QC Plan and Data Validation
Procedures. Interim Final. EPA/540/G-90/004.
U.S. Environmental Protection Agency. 1990. Geostatistics for Waste Management: A User's Manual for the
GEOPACK (Version 1.0) Geostatistical Software System. Robert S. Kerr Environmental Research
Laboratory, Ada, Oklahoma. EPA/600/8-90/004.
U.S. Environmental Protection Agency. February 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. 1989a. Soil Sampling Quality Assurance User's Guide. 2nd ed. (Draft).
EPA/600/8-89/046. Environmental Monitoring Systems Laboratory, Las Vegas, NV.
45
-------
U.S. Environmental Protection Agency. 198%. Data Quality Objectives Workshop. (Briefing Notes).
U.S. Environmental Protection Agency. December 1988. User's Guide to the Contract Laboratory Program.
EPA/540/8-89/012.
U.S. Environmental Protection Agency. September 1988a. Field Screening Methods Catalog - User's Guide.
EPA/540/2-88/005.
U.S. Environmental Protection Agency. September 1988b. Geo-EAS (Geostatistical Environmental Assessment
Software) User's Guide.
US. Environmental Protection Agency. December 1987. A Compendium of Superfund Field Operations
Methods. EPA/540/P-87/001. OSWER Directive 9355.0-14.
U.S. Environmental Protection Agency. 1987. Data Quality Objectives for Remedial Response Activities.
EPA/540/G-87/004. OSWER Directive 93550.7B.
U.S. Environmental Protection Agency, Region IV. April 1986. Engineering Support Branch Standard Operating
Procedures and Quality Assurance Manual. Environmental Services Division, Athens, Georgia.
U.S. Environmental Protection Agency. 1986. Test Methods for Evaluating Solid Waste. Volume II, Field
Manual Physical/Chemical Methods.
U.S. Environmental Protection Agency. 1984a. Characterization of Hazardous Waste Sites-A Methods Manual.
Volume I, Site Investigations. Section 7: Environmental Monitoring Systems Laboratory, Las Vegas, Nevada.
EPA/600/4-84/075.
U.S. Environmental Protection Agency. 1984b. Characterization of Hazardous Waste Sites A Methods Manual.
Volume n, Available Sampling Methods, Second Edition. Environmental Monitoring Systems Laboratory,
Las Vegas, Nevada. EPA/600/4-84/076.
U.S. Environmental Protection Agency. 1983. Preparation of Soil Sampling Protocol: Techniques and Strategies.
EPA/600/4-83/020.
van EC, J J., LJ. Blume, and T.H. Starks. 1989. A Rationale for the Assessment of Errors in the Sampling of
Soils. Las Vegas: U.S. EPA Environmental Monitoring Systems Laboratory. 59 pp.
46
-------
APPENDIX B
Compendium of ERT
Waste Sampling Procedures
-------
EPA/540/P-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 9360.4-01, 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
-------
Table of Contents
Section Page
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
i
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, Pickaxe, 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
2.7.3 Drum Staging 7
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
111
-------
Section Page
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
3.4 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
3.7.4 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 25
5.5 Equipment/Apparatus 26
5.6 Reagents 26
IV
-------
Section Page
o
5.7 Procedures 26
5.7.1 Preparation 26
5.7.2 Sample Collection 26
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
APPENDDC B - Figures 35
APPENDIX C - Calculations 51
REFERENCES 55
-------
List of Exhibits
Table 1:
Recommended Solvent Rinse for Soluble Contaminants
Drum Data Sheet Form
Figure 1: Univeral Bung Wrench
Figure 2: Drum Deheader
Figure 3: Hand Pick, Pickaxe, and Hand Spike
Figure 4: Backhoe Spike
Figure 5: Hydraulic Drum Opener
Figure 6: Pneumatic Bung Remover
Figure 7: Glass Thief
Figure 8: COLIWASA
Figure 9: Bacon Bomb Sampler
Figure 10: Sludge Judge
Figure 11: Subsurface Grab Sampler
Figure 12: Bailer
Figure 13: Sampling Augers
Figure 14: Sampling Trier
Figure 15: Grain Sampler
Calculation Sheet: Various Volume Calculations
SOP
#2006
#2009
#2009
#2009
#2009
#2009
#2009
#2009
#2009
#2009
#2010
#2010
#2010
#2010
#2017
#2017
#2017
#2010
Page
4
33
36
37
38
39
40
41
42
43
44
45
46
47
48
49
50
52
VI
-------
Acknowledgments
Preparation of this document was directed by William A. Coakley, 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.
VII
-------
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 samplirig 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 include
the use of brushes, air and wet blasting, and high-
pressure water cleaning, followed 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/dcionizcd 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 work 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 towels
galvanized tubs or buckets
tap water
-------
distilled/deionized water
metal/plastic containers for storage and
disposal of contaminated wash solutions
pressurized sprayers for tap and
deionized/distilled water
sprayers for solvents
trash bags
aluminum foil
safety glasses or splash shield
emergency eyewash bottle
1.6 REAGENTS
i
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(1)
acetone (pesticide grade)(2)
hexane (pesticide grade)(2)
methanol
(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 layout 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, involves 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 very fine
abrasives. This method generates a large
amount of waste.
Non-Abrasive Cleaning Methods
Non-abrasive cleaning methods work by forcing the
contaminant off of a surface with pressure. In
general, less of the equipment surface is removed
using non-abrasive methods. The following non-
abrasive methods are available:
-------
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 m/sec (1,000 atm) to 900 m/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 involve 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 include inorganics.
1. 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.
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 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.
-------
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
ซ Metals
Acidic compounds
Phenol
Thiols
Some nitro and sulfonic compounds
Organic Solvents'15 - 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)
(1) - 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 VALIDATION
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 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.
-------
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 4ฐC 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. Placfl 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.
-------
2.5 EQUIPMENT/APPARATUS
The following arc 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 following:
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 be 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 ire usually constructed of brass or a
non-sparkini. !loy with a sharpened point that can
penetrate th.. 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 required for preserving
drum samples. However, reagents are used for
decontaminating sampling equipment.
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 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
-------
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 diked 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 the1 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 pli'3 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.
If the 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.
-------
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 piercer is designed to establish a tight
seal after penetrating the container.
Remote Drum Opening with Pneumatic
Devices
Pneumatically-operated devices ut ilizing compressed
air have been designed to remove drum bungs
remotely (Figure 6, Appendix B).
2.7.5 Drum Sampling
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 I.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 does
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.
Cap the sample container tightly and place
prelabeled sample container in a carrier.
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 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
drum.
8. Log all samples in the site logbook and on field
data sheets.
10
-------
9. Package samples and complete necessary
paperwork.
10. Transport sample to decontamination zone to
prepare it for transport to the analytical
laboratory.
2.8 CALCULATIONS
This section is not applicable to this SOP.
2.9 QUALITY ASSURANCE/
QUALITY CONTROL
The following general quality assurance procedures
apply:
Document all data on standard chain of
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.
2.10 DATA VALIDATION
This section is not applicable to this SOP.
2.11 HEALTH AND SAFETY
When working with potentially hazardous materials,
follow U.S. EPA, OSHA, and specific health and
safety procedures.
The opening of closed containers is one of the most
hazardous site activities. Maximum efforts should
be made to ensure the safety of the sampling team.
Proper protective equipment and a general
awareness of the possible dangers will minimize the
risk inherent in sampling operations. Employing
proper drum-opening techniques and equipment will
also safeguard personnel. Use remote sampling
equipment whenever feasible.
II
-------
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 5-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.
however, be cooled to 4ฐC 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
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,
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
-------
sjU: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, COLIWASA, 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)
cxplosimcler/oxygcn 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
-------
4. Collect air quality measurements for each
potential sample location using an
explosimeter/oxygen meter for a lower
explosive limit (LEL/O2) 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
1. 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
line 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.
5. 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
-------
7. Position the sampler over the sample container
and release its contents by pulling up on the
plunger line.
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.
Sludge Judge
A sludge judge (Figure 10, Appendix B) is used for
obtaining an accurate reading of solids which can
settle, in any liquid, to any depth. The sampler
consists of 3/4-inch plastic pipe in 5-foot sections,
marked at 1-foot increments, with screw-style
fittings. The top section includes a nylon line for
raising the sampler.
1. Lower the sludge judge to the bottom of the
tank.
2. When the bottom has been reached, and the
pipe has filled to surface level, tug slightly on
the rope as you begin to raise the unit. This
will seat the check valve, trapping the column of
material.
3. When the unit has been raised clear of the tank
liquid, the amount of sludge in the sample can
be read using the 1-foot increments marked on
the pipe sections.
4. By touching the pin extending from the bottom
section against a hard surface, the material is
released from the unit.
5. Cap the sample container tightly and place
prelabeled sample container in a carrier.
6. Replace the bung or place plastic over the tank.
7. Log all samples in the site logbook and on field
data sheets and label all samples.
8. Package samples and complete necessary
paperwork.
9. Transport sample to decontamination zone to
prepare it for transport to the analytical
laboratory.
Subsurface Grab Sampler
Subsurface grab samplers (Figure 11, Appendix B)
are designed to collect samples of liquids at various
depths. The sampler is usually constructed of
aluminum or stainless steel tubing with a
polypropylene or Teflon head that attaches to a 1-
liter sample container.
1. Screw the sample bottle onto the sampling
head.
2. Lower the sampler to the desired depth.
3. Pull the ring at the top which opens the spring-
loaded plunger in the head assembly.
4. When the bottle is full, release the ring, lift
sampler, and remove sample bottle.
5. Cap the sample container tightly and place
prelabeled sample container in a carrier.
6. Replace the bung or place plastic over the tank.
7. Log all samples in the site logbook and on field
data sheets and label all samples.
8. Package samples and complete necessary
paperwork.
9. Transport sample to decontamination zone to
prepare it for transport to the analytical
laboratory.
Glass Thief
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 I.D. and 48 inches long.
1. Remove cover from sample container.
2. Insert glass tubing almost to the bottom of the
16
-------
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, bailers 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 bottle.
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 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.
17
-------
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 rqd 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
prclabeled 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 ps
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
18
-------
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), and structural
objects (including baffles/trays in
horizontal/vertical tanks, and overhead
structures).
19
-------
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 surficial 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 (4ฐC)
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
-------
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.
4.7 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
4ฐC.
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
-------
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 ah1 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
4ฐC.
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
48C.
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, /^g/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:
Ah1 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
23
-------
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 411 HEALTH AND SAFETY
analyte of choice. The solvent containing
the standard is allowed to evaporate, and when WQrking ^ potentially hazardous materials,
the foil is wiped in a manner identical to follow y s EPA> QSHA and spedfic heakh and
the other wipe samples. safety procedures.
Specific quality assurance activities for chip and
sweep samples should be determined on a site-
specific basis.
24
-------
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 4ฐC 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.
25
-------
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 include 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)
ce
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 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 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
26
-------
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 are 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 "T" 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 hammerin;
the drill rods to facilitate coring as the
vibrations may cause the boring walls to
collapse.
27
-------
7. Remove the tube sampler, and unscrew the drill
rods.
2. Rotate the trier once or twice to cut a core of
material.
8. Remove the cutting tip and the core from 3.
device.
Slowly withdraw the trier, making sure that the
slot is facing upward.
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 T" 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:
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. Insert the trier (Figure 14, Appendix B) into 1.
the material to be sampled at a 0ฐ to 45ฐ angle
from horizontal. This orientation minimizes
spillage of the sample. Extraction of the
samples might require tilting of the sample
containers.
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
-------
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. When
compositing is complete, place the sample into
appropriate, labeled containers and secure the
caps tightly.
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.
5.8 CALCULATIONS
This section is not applicable to this SOP.
29
-------
APPENDIX A
Drum Data Sheet Form
31
-------
Drum Data Sheet Form
SOP #2009
Drum ID#: 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:
Ha/ard:
Waste ID:
Treatment Disposal Recommendations:
Approval
Lab: Date:
Site Manager: Dale:
* Area of site where drum was originally located.
Based on di Napoli, l')82. Table originally printed in the Proceedings of the National Conference
Management of Uncontrolled Ha/ardous Waste Sites, ll>S2. Available fiom Ha/ardous Materials Control
Research Institute, <>3(X) Columbia Blvd., Silver Spring, MI) 2()ซ>1().
on
-------
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
x
Insert open tube (thief) sampler
in containerized liquid.
3.
Cover top of sampler with gloved
thumb.
4.
X
Remove open tube (thief) sampler
from containerized liquid.
Place open tube sampler over
appropriate sample bottle and
remove gloved thumb.
42
-------
Figures: COLIWASA
SOP #2009
T handle
lol
Locking block
Stopper
/
/
1,.
6.35
152 c
1
cn<
n(6C
2.86
17.8 cn<7')
/ti
T
10.16 cn<4'>
Pipe, PVC, translucent
4.13 end3/*') I.D.,
4.26 end7/* ') D.D.
Stopper rod, PVC,
0.95 cn<3/8'> D.D.
Stopper, neoprene, #9, tapered,
0.95 cn(3/8') PVC lock nut
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
Uo
Uo
0 0
CD CD
46
-------
Figure 12: Bailer
SOP #2010
STAINLESS WIRE
CABLE
-1-i/4" O.D.Xn.D.TEFLON
EXTRUDED TUBING,
18 TO 36" LONG
DIAMETER
GLASS OR TEFLON
L-1" DIAMETER TEFLON
EXTRUDED ROD
5/16" DIAMETER
HOLE
47
-------
Figure 13: Sampling Augers
SOP #2017
3 I I 0
TUBE
AUGER
BUCKET
AUGER
48
-------
Figure 14: Sampling Trier
SOP #2017
ฐT
i V
SS,
1.27-2.54 cm
(1/2--1")
49
-------
Figure 15: Grain Sampler
SOP #2017
61-100 cm
(24-40")
V
1.27-2.54 em
(1/2-r)
50
-------
APPENDIX C
Calculations
51
-------
Various Volume Calculations
SOP #2010
SPHERE
ELLIPTICAL CONTAINER
ANY RECTANGULAR CONTAINER
i
Total Volume
V=1/6 TvD3 = 0.523498D3
Partial Volume
V=1/3 nd2 (3/2 D-d)
I
Total Volume
V= ^BDH
Partial Volume
V=
h
w
Total Volume
V=HLW
Partial Volume
V=hl_W
V
b
TRIANGULAR CONTAINER
Total Volume
V=1/2 HBL
RIGHT CYLINDER
T
H
_L
H
J_
Case 1
Partial Volume
V=1/2 hBL
Case 2
Partial Volume
V=1/2 L(HB-hB)
Total Volume
V=1/4nD2 H
Partial Volume
D2 h
52
-------
Various Volume Calculations (Cont'd)
FRUSTUM OF A CONE
Case 1 Case 2
CONE
Case 1 Case 2
PARABOLIC CONTAINER
- n -1
D 1
/
\_^/\
hH
b^
^N
\
B -j
a 1
L
Total Volume
V=2/3 HDL
i >
rh
i
1 i
rh
i
u
1 \
Total Volume
2
V= TV/12 H(D1Z + D, D2+D22 )
Partial Volume
V= TV/12 hCD,2 t-D, d+d2)
Total Volume
V= n/12-D2H
Partial Volume Case 1
V= Tv/12-d2h
Partial Volume Case 2
V= TV/12-(D2H-d2h)
Case 1
Partial Volume
V=2/3 hdL
Case 2
Partial Volume
V=2/3 (HD-hd)-L
53
-------
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. II, 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.
U.S. Government Printing Office: 1991 548-187/40582 55
-------
APPENDIX C
Compendium of ERT Soil Sampling and
Surface Geophysics Procedures
-------
EPA/540/P-91/006
OSWER Directive 9360.4-02
January 1991
COMPENDIUM OF ERT SOIL SAMPLING AND
SURFACE GEOPHYSICS PROCEDURES
Sampling Equipment Decontamination
Soil Sampling
Soil Gas Sampling
General Surface Geophysics
Interim Final
Environmental Response Team
Emergency Response Di\ision
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 9360.4-01, EPA/540/G-90/004.
Questions, comments, and recommendations are welcomed regarding the Compendium of ERT Soil Sampling
and Surface Geophysics 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 Soil Sampling and Surface Geophysics Procedures, please
contact:
National Technical Information Service (NTIS)
U.S. Department of Commerce
5285 Port Royal Road
Springfield, VA 22161
(703) 487-4600
-------
Table of Contents
Section Page
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 SOIL SAMPLING: SOP #2012
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 5
2.6 Reagents 5
2.7 Procedures 6
2.7.1 Preparation 6
2.7.2 Sample Collection 6
2.8 Calculations 9
2.9 Quality Assurance/Quality Control 9
2.10 Data Validation 9
2.11 Health and Safety 9
3.0 SOIL GAS SAMPLING: SOP #2149
3.1 Scope and Application 11
3.2 Method Summary 11
3.3 Sample Preservation, Containers, Handling, and Storage 11
3.3.1 Tcdlar Bag 11
3.3.2 Tcnax Tube 11
3.3.3 SUMMA Canister 11
111
-------
Page
3.4 Interferences and Potential Problem 12
3.41 HNU Measurements 12
3.4.2 Factors Affecting Organic Concentrations in Soil Gas 12
3.4.3 Soil Probe Clogging 12
3.4.4 Underground Utilities 12
3.5 Equipment/Apparatus 12
3.5J Slam Bar Method 12
3.5.2 Power Hammer Method 13
3.6 Reagents 13
3.7 Procedures 13
3.7.1 Soil Gas Well Installation 13
3.7.2 Screening with Field Instruments 14
3.7.3 Tedlar Bag Sampling 14
3.7.4 Tenax Tube Sampling 14
3.7.5 SUMMA Canister Sampling 16
3.8 Calculations 16
3.8.1 Field Screening Instruments 16
3.8.2 Photovac GC Analysis 16
3.9 Quality Assurance/Quality Control 16
3.9.1 Field Instrument Calibration 16
3.9.2 Gilian Model HFS113A Air Sampling Pump Calibration 16
3.9.3 Sample Probe Contamination 16
3.9.4 Sample Train Contamination 16
3.9.5 Field Blank 16
3.9.6 Trip Standard 16
3.9.7 Tedlar Bag Check 17
3.9.8 SUMMA Canister Check 17
3.9.9 Options 17
3.10 Data Validation 17
3.11 Health and Safety 17
IV
-------
Page
4.0
SOIL SAMPLING AND SURFACE GEOPHYSICS: SOP #2159
4.1 Scope and Application
4.2 Method Summary
4.2J Magnetics
4.2.2 Electromagnetics
4.2.3 Electrical Resistivity
4.2.4 Seismic
4.2.5 Ground Penetrating Radar
4.3 Sample Preservation, Containers, Handling and Storage
4.4 Interferences and Potential Problems
4.5 Equipment/Apparatus
4.5.1 Magnetics
4.5.2 Electromagnetics
4.5.3 Electrical Resistivity
4.5.4 Seismic
4.5.5 Ground Penetrating Radar
4.6 Reagents
4.7 Procedures
4.8 Calculations
4.9 Quality Assurance/Quality Control
4.10 Data Validation
4.11 Health and Safety
19
19
19
20
20
21
22
23
23
24
24
24
24
24
24
24
24
24
24
24
24
APPENDIX A - Figures
APPENDIX B - HNU Field Protocol
REFERENCES
25
29
-------
List of Exhibits
Exhibit SOP Page
Table 1: Recommended Solvent Rinse for Soluble Contaminants #2006 4
Figure 1: Sampling Augers #2012 26
Figure 2: Sampling Trier #2012 27
Figure 3: Sampling Train Schematic #2149 28
-------
Acknowledgments
Preparation of this document was directed by William A. Coakley, 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.
-------
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 jn 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 include
the use of brushes, air and wet blasting, and high-
pressure water cleaning, followed 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 work 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 technique's
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 persona) protective clothing
non-phosphate detergent
selected solvents
long-handled brushes
drop cloths/plastic sheeting
trash container
paper towels
galvanized tubs or buckets
tap water
-------
distilled/deionized water
metal/plastic containers for storage and
disposal of contaminated wash solutions
pressurized sprayers for 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 following solvents are
utilized for decontamination purposes:
10% nitric acid(1)
acetone (pesticide grade)(2)
hexane (pesticide grade)(2)
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 layout 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 cither 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, involves 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 cleaning methods work by forcing the
contaminant off of a surface with pressure. In
general, less of the equipment surface is removed
using non-abrasive methods. The following non-
abrasive methods arc available:
-------
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
(atrn) 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 m/sec (1,000 atm) to 900 m/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 involve 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 include inorganics.
1. 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.
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 removaJ 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 raises 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 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.
-------
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 Solvents0' - 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 analytc-free
(i.c, dcionized) water which is passed over and
through a field decontaminated sampling device and
placed in a clean sample container.
Rinsaic blanks should he run for all parameters of
interest at a rate of 1 per 20 for each parameter,
even if samples arc not shipped that day. Rinsate
blanks arc not required if dedicated sampling
equipment :s used.
1.10 DATA VALIDATION
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 ha/.ards under certain
circumstances even (hough 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 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 contac;. 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
ha/ard, measures should be taken to protect
personnel or the methods should be modified to
eliminate the ha/ard.
-------
2.0 SOIL SAMPLING: SOP #2012
2.1 SCOPE AND APPLICATION
The purpose of this Standard Operating Procedure
(SOP) is to describe the procedures for collecting
representative soil samples. Analysis of soil samples
may determine whether concentrations of specific
soil pollutants exceed established action levels, or if
the concentrations of, soil pollutants present a risk
to public health, welfare, or the environment.
2.2 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 versus undisturbed), and the type of soil.
Near-surface soils may be easily sampled using a
spade, trowel, and scoop. Sampling at greater
depths may be performed using a hand auger, a
trier, a split-spoon, or, if required, a backhoe.
2.3 SAMPLE PRESERVATION,
CONTAINERS, HANDLING, AND
STORAGE
Chemical preservation of solids is not generally
recommended. Refrigeration to 4ฐC, supplemented
by a minimal holding time, is usually the best
approach.
2.4 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.
2.5 EQUIPMENT/APPARATUS
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
sampling trier
thin-wall tube sampler
Vehimeycr soil sampler outfit
- tubes
- points
- drive head
- drop hammer
- puller jack and grip
backhoe
2.6 REAGENTS
Reagents are not used for the preservation of soil
samples. Decontamination solutions are specified in
-------
ERT SOP #2006,
Decontamination.
Sampling Equipment
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 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, buoys, or flagging to identify and
mark all sampling locations. Consider specific
site factors, including extent and nature of
contaminant, 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.
2.7.2 Sample Collection
Surface Soil Samples
Collect samples from near-surface soil 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.
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 sampling team member. 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. Avoid the use of devices plated with
chrome or other materials. Plating is particularly
common with garden implements such as potting
trowels.
Follow these procedures to collect surface soil
samples.
1. 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 a portion of the sample directly into an
appropriate, labeled sample container(s) with a
stainless steel lab spoon, plastic lab spoon, or
equivalent and secure the cap(s) 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 an appropriate, labeled
container(s) and secure the cap(s) 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 container(s)
and secure the cap(s) tightly.
Sampling at Depth 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 (Appendix A, Figure 1). 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 at the
completion depth. The system is withdrawn and the
core collected from the thin-wall tube sampler.
Several types of augers are available. These
include: bucket, continuous flight (screw), and
pesthole 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-feet
intervals. The continuous flight augers are
satisfactory for use when a composite of the
complete soil column is desired. Pesthole augers
have limited utility for sample collection as they are
designed to cut through fibrous, rooted, swampy
soil.
Follow these procedures for collecting soil samples
with the auger and a thin-wall tube sampler.
1. 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 3 to 6 inches of
surface soil for an area approximately 6 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 sample
after the auger is removed from boring and
proceed to Step 10.
5. Remove auger tip from drill rods and replace
with a pre-cleaned thin-wall tube sampler.
Install proper cutting tip.
6. Carefully lower the tube sampler down the
borehole. Gradually force the tube sampler
into the 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.
8. Remove the cutting tip and the core from the
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(s). Sample
homogenization is not required.
10. If volatile organic analysis is to be performed,
transfer a portion of the sample directly into an
appropriate, labeled sample container(s) with a
stainless steel lab spoon, plastic lab spoon, or
equivalent and secure the cap(s) 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 an appropriate, labeled
container(s) and secure the cap(s) 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 the appropriate, labeled
container(s) and secure the cap(s) 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.
12. Abandon the hole according to applicable state
regulations. Generally, shallow holes can
simply be backfilled with the removed soil
material.
Sampling at Depth with a Trier
The system consists of a trier, and a T" handle.
The auger is driven into the soil to be sampled and
used to extract a core sample from the appropriate
depth.
Follow these procedures to collect soil samples with
a sampling trier.
1. Insert the trier (Appendix A, Figure 2) into the
material to be sampled at a 0ฐ to 45ฐ 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 a portion of the sample directly into an
appropriate, labeled sample container(s) with a
stainless steel lab spoon, plastic lab spoon, or
equivalent and secure the cap(s) 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 an appropriate, labeled
container(s) and secure the cap(s) tightly; or, if
composite samples are to be collected, place a
sample from another sampling interval into the
homogenizatior. container and mix thoroughly.
When compositing is complete, place the
sample into an appropriate, labeled container(s)
and secure the cap(s) tightly.
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 tube sampling is performed to gain
geologic information, all work should be performed
in accordance with ASTM D 1586-67 (reapproved
1974).
Follow these procedures for collecting soil samples
with a split spoon.
1. Assemble the sampler by aligning both sides of
the barrel and then screwing the bit onto the
bottom and the heavier head piece onto the
top.
2. Place the sampler in a perpendicular position
on the sample material.
3. Using a sledge hammer or well ring, if
available, 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. If a
split sample is desired, a cleaned, stainless steel
knife should be used to divide the tube contents
in half, longitudinally. This sampler is typically
available in diameters of 2 and 3 1/2 inches.
However, hi order to obtain the required
sample volume, use of a larger barrel may be
required.
6. Without disturbing the core, transfer it to an
appropriate labeled sample container(s) and
seal tightly.
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.
Follow these procedures for collecting soil samples
from test pit/trench excavations.
1. Prior to any excavation with a backhoe, it is
important to ensure that all sampling locations
are clear of utility lines and poles (subsurface
as well as above surface).
2. Using the backhoe, dig a trench to
approximately 3 feet in width and
approximately 1 foot below the cleared
sampling location. Place removed or excavated
soils on plastic sheets. Trenches greater than
5 feet deep must be sloped or protected by a
shoring system, as required by OSHA
regulations.
3. Use a shovel to remove a 1- to 2-inch layer of
soil from the vertical face of the pit where
sampling is to be done.
4. Take samples 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 a portion of the sample directly into an
appropriate, labeled sample container(s) with a
stainless steel lab spoon, plastic lab spoon, or
equivalent and secure the cap(s) 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 an appropriate, labeled
container(s) and secure the cap(s) 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 container(s)
and secure the cap(s) tightly.
6. Abandon the pit or excavation according to
applicable state regulations. Generally, shallow
excavations can simply be backfilled with the
removed soil material.
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 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.
2.10 DATA VALIDATION
This section is not applicable to this SOP.
2.11 HEALTH AND SAFETY
When working with potentially hazardous materials,
follow U.S. EPA, OSHA, and specific health and
safety procedures.
-------
3.0 SOU GAS SAMPLING: SOP #2149
3.1 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 EPA/ERT in installing soil gas
wells'; measuring organic levels in the soil gas using
an HNU PI 101 Portable Photoionization Analyzer
and/or other air monitoring devices; and sampling
the soil gas using Tedlar bags, Tenax sorbent tubes,
and SUMMA canisters.
3.2 METHOD SUMMARY
A 3/8-inch diameter hole is driven into the ground
to a depth of 4 to 5 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 1/4-inch O.D. stainless steel probe
is inserted into the hole. The hole is then sealed at
the top around the probe using modeling clay. The
gas contained in the interstitial spaces of the soil is
sampled by pulling 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
CGI/02 Meter, Model 260) and the organic vapor
analyzer (Foxboro OVA, Model 128), can also be
used depending 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-inch O.D. steel probes) can be
driven to the desired depth using a power hammer
(e.g., Bosch Demolition Hammer). 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.
3.3 SAMPLE PRESERVATION,
CONTAINERS, HANDLING, AND
STORAGE
3.3.1 Tedlar Bag
Soil gas samples are generally contained in 1-L
Tedlar bags. Bagged samples are best stored in
coolers to protect the bags from any damage that
may occur in the field or in transit. In addition,
coolers ensure 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 to 48 hours.
3.3.2 Tenax Tube
Bagged samples can also be drawn into Tenax or
other sorbent tubes to undergo lab GC/MS 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 samplers
must wear nylon or other lint-free gloves. After
sampling, each tube should be sloreii 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 3.7.4.).
3.3.3 SUMMA Canister
The SUMMA canisters used for soil gas sampling
have a 6-L sample capacity and arc certified clean
by GC/MS analysis before being ulili/cd in the
field. After sampling is completed, ihcy arc stored
and shipped in travel cases.
11
-------
3.4 INTERFERENCES AND
POTENTIAL PROBLEMS
3.4.1 HNU Measurements
A number of factors can affect the response of the
HNU PI 101. 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 occurring 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.
3.4.2 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 theory, 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.
3.4.3 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 sound of the pump laboring. This
problem can usually be eliminated by using a wire
cable to clear the probe (see procedure #3 in
Section 3.7.1).
3.4.4 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.
3.5 EQUIPMENT/APPARATUS
3.5.1 Slam Bar Method
slam bar (one per sampling team)
soil gas probes, stainless steel tubing, 1/4-
inch O.D., 5 foot length
flexible wire or cable used for clearing the
tubing during insertion into the well
"quick connect" fittings to connect sampling
probe tubing, monitoring instruments, and
Gilian pumps to appropriate fittings on
vacuum box
modeling clay
vacuum box for drawing a vacuum around
Tedlar bag for sample collection (one per
sampling team)
Gilian pump Model HFS113A adjusted to
approximately 3.0 L/min (one to two per
sampling team)
1/4-inch Teflon tubing, 2 to 3 foot lengths,
for replacement of contaminated sample
line
Tedlar bags, 1 liter, at least one bag per
sample point
soil gas sampling labels, field data sheets,
logbook, etc.
HNU Model PI 101, or other field air
monitoring devices, (one per sampling
team)
ice chest, for carrying equipment and for
protection of samples (two per sampling
team)
metal detector or magnetometer, for
detecting underground utilities/
pipes/drums (one per sampling team)
Photovac GC, for field-lab analysis of
bagged samples
SUMMA canisters (plus their shipping
cases) for sample, storage and
transportation
12
-------
3.5.2 Power Hammer Method
Bosch demolition hammer
1/2-inch O.D. steel probes, extensions, and
points
dedicated aluminum sampling points
Teflon tubing, 1/4-inch O.D.
"quick connect" fittings to connect sampling
probe tubing, monitoring instruments, and
Gilian pumps to appropriate fittings on
vacuum box
modeling clay
vacuum box for drawing a vacuum around
Tedlar bag for sample collection (one per
sampling team)
Gilian pump Model HFS113A adjusted to
approximately 3.0 L/min (one to two per
sampling team)
1/4-inch Teflon tubing, 2 to 3 foot lengths,
for replacement of contaminated sample
line
Tedlar bags, 1 liter, at least one bag per
sample point
soil gas sampling labels, field data sheets,
logbook, etc.
HNU Model PI 101, or other field air
monitoring devices, (one per sampling
team)
ice chest, for carrying equipment and for
protection of samples (two per sampling
team)
metal detector or magnetometer, for
detecting underground utilities/
pipes/drums (one per sampling team)
Photovac GC, for field-lab analysis of
bagged samples
SUMMA canisters (plus their shipping
cases) for sample. storage and
transportation
generator with extension cords
high lift jack assembly for removing probes
3.6 REAGENTS
HNU Systems Inc. Calibration Gas for
HNU Model PI 101, and/or calibration gas
for other field air monitoring devices
deionizcd organic-free water, for
decontamination
methanol, HPLC grade, for
decontamination
ultra-zero grade compressed air, for field
blanks
standard gas preparations for Photovac GC
calibration and Tedlar bag spikes
3.7 PROCEDURES
3.7.1 Soil Gas Well Installation
1. Initially, make a hole slightly deeper than the
desired depth. For sampling up to 5 feet, use
a 5-foot single piston slam bar. For deeper
depths, use a piston slam bar with threaded 4-
foot-long extensions. Other techniques can be
used, so long as holes are of narrow diameter
and no contamination is introduced.
2. After the hole is made, carefully withdraw the
slam bar to prevent collapse of the walls of the
hole. Then insert the soil gas probe.
3. It is necessary to prevent plugging of the probe,
especially for deeper holes. Place a metal wire
or cable, slightly longer than the probe, into the
probe prior to inserting into the hole. Insert
the probe to full depth, then pull it up 3 to 6
inches, then clear it by moving the cable up and
down. The cable is removed before sampling.
4. Seal the top of the sample hole 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. Use the generator-powered
demolition hammer to drive the probe to the
desired depth (up lo 12 feet may be attained
with extensions). Pull the probe up 1 to 3
inches if the retractable point is used. No clay
is needed to seal the hole. After sampling,
retrieve the probe using the high lift jack
assembly.
6. If semi-permanent soil gas wells are required,
use the dedicated aluminum probe points.
Insert these points into the bottom of the
power-driven probe and attach it to the Teflon
tubing. Insert the probe as in step 5. When
the probe is removed, the point and Teflon
tube remain in the hole, which may be scaled
bv backfilling with sand, bcntonite, or soil.
13
-------
3.7.2 Screening with Field
instruments
1. The well volume must be evacuated prior 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. Turn
the pump on, and a vacuum is pulled through
the probe for approximately 15 seconds. A
longer time is required for sample wells of
greater depths.
2. After evacuation5, connect the monitoring
instrument(s) to the probe using a Teflon
connector. When the reading is stable, or
peaks, record the reading. For detailed
procedures on HNU field protocol, see
appendix B, and refer to the manufacturer's
instructions.
3. Some readings may be above or below the
range set on the field instruments. The range
may be reset, or the response recorded as a
figure greater than or less than the range.
Consider the recharge rate of the well with soil
gas when sampling at a different range setting.
3.7.3 Tedlar Bag Sampling
1. Follow step 1 in section 3.7.2 to evacuate well
volume. If air monitoring instrument screening
was performed prior to sampling, evacuation is
not necessary.
2. Use the vacuum box and sampling train (Figure
3 in Appendix A) 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.
3. Place the Tedlar bag inside the vacuum box,
and attach it to the sampling port. Attach the
sample probe to the sampling port via Teflon
tubing and a "quick connect" fitting.
4. Draw a vacuum 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. Label bag,
record data on data sheets or in logbooks.
Record the date, time, sample location ID, and
the HNU, or other instrument reading(s) on
sample bag label.
CAUTION: 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.
3.7.4 Tenax Tube Sampling
Samples collected in Tedlar bags may be sorbcd
onto Tenax tubes for further analysis by GC/MS.
Additional Apparatus
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 being drawn
onto the sorbent tube.
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-inch to 1/16-inch O.D.
- Swagelok cat. # SS-400-6-ILV or
equivalent) with a length of 1/4-inch O.D.
Teflon tubing replacing the nut on the 1/6-
inch (Tedlar bag) side. A 1/4-inch I.D.
silicone O-ring replaces the ferrules in the
nut on the 1/4-inch (sorbent tube) side of
the union.
The adapter attaching the sampling syringe
to the sorbcnt tube consists of a reducing
union (1/4-inch to 1/16-inch O.D. -
Swagelok Cat. # SS-400-6-ILV or
equivalent) with a 1/4-inch I.D. silicone
O-ring replacing the ferrules in the nut on
the 1/4-inch (sorbent tube) side and the
needle of a luer-lock syringe needle
inserted into the 1/16-inch side (held in
place with a 1/16-inch ferrule). The
14
-------
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.
Two-stage glass sampling cartridge (1/4-
inch O.D. x 1/8-inch I.D. x 5 1/8 inch)
contained in a flame-sealed tube
(manufactured by Supelco Custom
Tenax/Spherocarb Tubes or equivalent)
containing two sorbent sections retained by
glass wool:
Front section: 150 mg of Tenax-GC
Back section: 150 mg of CMS
(Carbonized Molecular Sieve)
Sorbent tubes may also be prepared in the
lab and stored in either Teflon-capped
culture tubes or stainless steel tube
containers. Sorbent tubes stored in this
manner should not be kept more than 2
weeks without reconditioning. (See SOP
#2052 for Tenax/CMS sorbent tube
preparation).
Teflon-capped culture tubes or stainless
steel tube containers for sorbent tube
storage. These containers should be
conditioned by baking at 120ฐC for at least
2 hours. The culture tubes should contain
a glass wool plug to prevent sorbent tube
breakage during transport. Reconditioning
of the containers should occur between
usage or after extended periods of disuse
(i.e., 2 weeks or more).
Nylon gloves or lini-free cloth. (Hewlett
Packard Part # 8650-0030 or equivalent.)
Sample Collection
1. Handle sorbent tubes with care, using nylon
gloves (or other lint-free material) to avoid
contamination.
2. Immediately before sampling, break one end of
the sealed tube and remove the Tenax
cartridge. For in-house prepared tubes, remove
cartridge from its container.
3. Connect the valve on the Tcdlar bag to the
sorbent tube adapter. Connect the sorbent tube
to the sorbent tube adapter with the Tenax
4.
Awhile 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 very tight.
5. Open the valve on the Tedlar bag.
6. Open the on/off valve of the sampling syringe.
7. Draw a predetermined volume of sample onto
the sorbent tube. (This may require closing the
syringe valve, emptying the syringe and then
repeating the procedure, depending upon the
syringe capacity and volume of sample
required.)
8. 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.
9. Place the sorbent tube in a conditioned
stainless steel tube holder or culture tube.
Culture tube caps should be sealed with Teflon
tape.
Sample Labeling
Each sample tube container (not tube) must be
labeled with the site name, sample station number,
sample date, and sample volume.
Chain of custody forms must accompany all samples
to the laboratory.
Quality Assurance
Before field use, a QA check should be performed
on each batch of sorbent tubes by analyzing a tube
with thermal desorption/cryogenic trapping
GC/MS.
At least one blank sample must be submiltcd wiih
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.
15
-------
3.7.5 SUMMA Canister Sampling
1. Follow item 1 in step 3.7.2 to evacuate well
volume. If HNU analysis was performed prior
to taking a sample, evacuation is not necessary.
2. Attach a certified clean, evacuated 6-L
SUMMA canister via the 1/4-inch Teflon
tubing.
3. Open the valve on SUMMA canister. The soil
gas sample is drawn into the canister by
pressure equilib'ration. The approximate
sampling time for a 6-L canister is 20 minutes.
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.
3.8 CALCULATIONS
3.8.1 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
3.8.2 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, Photovac GC Analysis for Soil,
Water and Air/Soil Gas.
3.9 QUALITY ASSURANCE/
QUALITY CONTROL
3.9.1 Field Instrument Calibration
Consult the manufacturers' manuals for correct use
and calibration of all instrumentation. The HNU
should be calibrated at least once a day.
3.9.2 Gilian Model HFS113A Air
Sampling Pump Calibration
Flow should be set at approximately 3.0 L/min;
accurate flow adjustment is not necessary. Pumps
should be calibrated prior to bringing into the field.
3.9.3 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 HNU PI 101. If HNU 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. Having more than one
probe per sample team will reduce lag times
between .sample stations while probes are
decontaminated.
3.9.4 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 immediately. When sampling in highly
contaminated areas, the sampling train 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 HNU, or other field monitoring device, to
establish the cleanliness of the Teflon line.
3.9.5 Field Blank
Each cooler containing 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 form must accompany each cooler of
samples and should include the blank that is
dedicated to that group of samples.
3.9.6 Trip Standard
Each cooler containing samples should contain a
Tedlar bag of standard gas to calibrate the
16
-------
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 form should
accompany each cooler of samples and should
include the trip standard that is dedicated to that
group of samples.
3.9.7 Tedlar Bag Check
Prior 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.
3.9.8 SUMMA 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
rc-cvacuatcd and all four canisters from that lot arc
available for sampling.
If the chosen canister is contaminated, then the
entire lot of four SUMMA canisters must be
rcclcancd, and a single canister is rc-analy/.cd by
GC/MS for certification.
3.9.9 Options
Duplicate Samples
A minimum of 5% of all samples should be
collected in duplicate (i.e., if a total of 100 samples
arc to be collected, five samples should be
duplicated). In choosing which samples to
duplicate, the following criterion applies: if, after
filling the first Tedlar bag, and, evacuating ihe well
for 15 seconds, the second HNU (or other field
monitoring device being used) reading matches or
is close to (within 50%) the first reading, a
duplicate sample may be taken.
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 attained 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.
3.10 DATA VALIDATION
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 criteria
apply to target compounds detected in the Tedlar
bag pre-sampling contamination check.
3.11 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, unless the sampling location is
within the hot zone of a site, which requires Level
B or Level C protection. However, to ensure that
the proper level of protection is utilized, constantly
monitor the ambient air using the HNU PI 101 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.
Also, perform an underground utility search prior to
sampling (sec section 3 4.4). When working with
potentially ha/ardous materials, follow U.S. EPA,
OSHA, and specific health and safety procedures.
17
-------
4.0 General Surface Geophysics: SOP #2159
4.1 SCOPE AND APPLICATION
This Standard Operating Procedure (SOP) describes
the general procedures used to acquire surface
geophysical data. This data is used for delineating
subsurface waste, and for interpreting geologic,
hydrogeologic or other data related to hazardous
waste site characterization.
The media pertinent to these surface geophysical
methods are soil/rock and groundwater. The
sensitivity or minimum response of a given method
depends on the comparison of the object or area of
study to that of its background (i.e., what the
media's response would be like without the object
of study). Therefore, the suitability of surface
geophysical methods for a given investigation must
be judged on the object's ability to be measured and
the extent to which the specific setting of the study
interferes with the measurement.
The surface geophysical method(s) selected for
application at a site are dependent on site
conditions, such as depth to bedrock, depth to
target, urban disturbances (fences, power lines,
surface debris, etc.) and atmospheric conditions.
Detectability of the target is dependent on the
sensitivity of the instrument and the variation of the
field measurement from the ambient noise.
Ambient noise is the pervasive noise associated with
an environment. Therefore, the applicability of
geophysical methods at a given site is dependent on
the specific setting at that site.
Five geophysical methods may be utilized in
hazardous waste site characterization:
magnetometry, electromagnetics, resistivity,
seismology and ground penetrating radar (GPR).
Magnetometers may be used to locate buried
ferrous metallic objects and geologic information.
Electromagnetic methods can be used to determine
the presence of metals, electrical conductivity of the
terrain, and geologic information. Resistivity
methods are used to determine the electrical
resistivity of the terrain and geologic information.
Seismic methods are useful in determining geologic
stratigraphy and structure. GPR may be used to
locate disturbance in the soil (i.e., trenches, buried
utilities and fill boundaries) and some near-surface
geologic information.
These procedures may be varied or changed as
required, dependent on site conditions, equipment
limitations or limitations imposed by the procedure.
In all instances, the procedures employed should be
documented and associated with the final report.
4.2 METHOD SUMMARY
4.2.1 Magnetics
A magnetometer is an instrument which measures
magnetic field strength in units of gammas
(nanoteslas). Local variations, or anomalies, in the
earth's magnetic field are the result of disturbances
caused mostly by variations in concentrations of
ferromagnetic material in the vicinity of the
magnetometer's sensor. A buried ferrous object,
such as a steel drum or tank, locally distorts the
earth's magnetic field and results in a magnetic
anomaly. The objective of conducting a magnetic
survey at a hazardous waste or groundwater
pollution site is to map these anomalies and
delineate the area containing buried sources of the
anomalies.
Analysis of magnetic data can allow an experienced
geophysicist to estimate the areal extent of buried
ferrous targets, such as a steel tank or drum.
Often, areas of burial can be prioriii?cd upon
examination of the data, with high priority areas
indicating a near certainty of buried ferrous
material. In some instances, estimates of depth of
burial can be made from the data. Most of these
depth estimates are graphical methods of
interpretation, such as slope techniques and half-
width rules, as described by Nettleton (1976). The
accuracy of these methods is dependent upon tho
quality of the data and the skill of the interpreting
geophysicist. An accuracy of 10 to 20 percent is
considered acceptable. The magnetic method may
also be used to map certain geologic features, such
as igneous intrusions, which may play an important
role in the hydrogeology of a groundwater pollution
site.
Advantages
Advantages of using the magnetic method for the
initial assessment of hazardous waste sites arc the
19
-------
relatively low cost of conducting the survey and the
relative ease of completing a survey in a short
amount of time. Little, if any, site preparation is
necessary. Surveying requirements are not as
stringent as for other methods and may be
completed with a transit or Brunton-type pocket
transit and a non-metallic measuring tape. Often,
a magnetic investigation is a very cost-effective
method for initial assessment of a hazardous waste
site where buried steel drums or tanks are a
concern.
Disadvantages
"Cultural noise" is a limitation of the magnetic
method in certain areas. Man-made structures that
are constructed with ferrous material, such as steel,
have a detrimental effect on the quality of the data.
Avoid features such as steel structures, power lines,
metal fences, steel reinforced concrete, pipelines
and underground utilities. When these features are
unavoidable, note their locations in a field notebook
and on the site map.
Another limitation of the magnetic method is the
inability of the interpretation methods to
differentiate between various steel objects. For
instance, it is not possible to determine if an
anomaly is the result of a steel tank, or a group of
steel drums, or old washing machines. Also, the
magnetic method does not allow the interpreter to
determine the contents of a buried tank or drum.
4.2.2 Electromagnetics
The electromagnetic method is a geophysical
technique based on the physical principles of
inducing and detecting electrical current flow within
geologic strata. A receiver detects these induced
currents by measuring the resulting time-varying
magnetic field. The electromagnetic method
measures bulk conductivity (the inverse of
resistivity) of geologic materials beneath the
transmitter and receiver coils. Electromagnetics
should not be confused with the electrical resistivity
method. The difference between the two techniques
is in the method which the electrical currents are
forced to flow in the earth. In the electromagnetic
method, currents are induced by the application of
time-varying magnetic fields, whereas in the
electrical resistivity method, current is injected into
the ground through surface electrodes.
Electromagnetics can be used to locate pipes, utility
lines, cables, buried steel drums, trenches, buried
waste, and concentrated contaminant plumes. The
method can also be used to map shallow geologic
features, such as lithologic changes and fault zones.
Advantages
Electromagnetic measurements can be collected
rapidly and with a minimum number of field
personnel. Most electromagnetic equipment used in
groundwater pollution investigations is lightweight
and easily portable. The electromagnetic method is
one of the more commonly used geophysical
techniques applied to groundwater pollution
investigations.
Disadvantages
The main limitation of the electromagnetic method
is "cultural noise". Sources of "cultural noise" can
include: large metal objects, buried cables, pipes,
buildings, and metal fences.
The electromagnetic method has limitations in areas
where the geology varies laterally. These can cause
conductivity anomalies or lineations, which might be
misinterpreted as contaminant plumes.
4.2.3 Electrical Resistivity
The electrical resistivity method is used to map
subsurface electrical resistivity structure, which is in
turn interpreted by the geophysicist to determine
the geologic structure and/or physical properties of
the geologic materials. Electrical resistivities of
geologic materials are measured in ohm-meters, and
are functions of porosity, permeability, water
saturation and the concentration of dissolved solids
in the pore fluids.
Resistivity methods measure the bulk resistivity of
the subsurface, as do the electromagnetic methods.
The difference between the two methods is in the
way that electrical currents arc forced to flow in the
earth. In the electrical resistivity method, current is
injected into the ground through surface electrodes,
whereas in electromagnetic methods currents are
induced by application of time-varying magnetic
fields.
Advantages
The principal advantage of the electrical resistivity
method is that quantitative modeling is possible
20
-------
using either computer software or published master
curves. The resulting models can provide accurate
estimates of depths, thicknesses and resistivities of
subsurface layers. The layer resistivities can then be
used to estimate the resistivity of the saturating
fluid, which is related to the total concentration of
dissolved solids in the fluid.
Disadvantages
The limitations of using the resistivity method in
groundwater pollution site investigations are largely
due to site characteristics, rather than in any
inherent limitations of the method. Typically,
polluted sites are located in industrial areas that
contain an abundance of broad spectrum electrical
noise. In conducting a resistivity survey, the
voltages are relayed to the receiver over long wires
that are grounded at each end. These wires act as
antennae receiving the radiated electrical noise that
in turn degrades the quality of the measured
voltages.
Resistivity surveys require a fairly large area, far
removed from pipelines and grounded metallic
structures such as metal fences, pipelines and
railroad tracks. This requirement precludes using
resistivity on many polluted sites. However, the
resistivity method can often be used successfully off-
site to map the stratigraphy of the area surrounding
the site. A general "rule of thumb" for resistivity
surveying is that grounded structures be at least half
of the maximum electrode spacing distance away
from the axis of the survey line.
Another consideration in the resistivity method is
that the fieldwork tends to be more labor intensive
than some other geophysical techniques. A
minimum of two to three crew members are
required for the fieldwork.
4.2.4 Seismic
Surface seismic techniques used in groundwater
pollution site investigations are largely restricted to
seismic refraction and seismic reflection methods.
The equipment used for both methods is
fundamentally the same and both methods measure
the travel-time of acoustic waves propagating
through the subsurface. In the refraction method,
the travel-time of waves refracted along an acoustic
interface is measured, and in the reflection method,
the travel-time of a wave which reflects or echoes
off an interface is measured.
The interpretation of seismic data will yield
subsurface velocity information, which is dependent
upon the acoustic properties of the subsurface
material. Various geologic materials can be
categorized by their acoustic properties or velocities.
Depth to geologic interfaces are calculated using the
velocities obtained from a seismic investigation.
The geologic information gained from a seismic
investigation is then used in the hydrogeologic
assessment of a groundwater pollution site and the
surrounding area. The interpretation of seismic
data indicates changes in lithology or stratigraphy,
geologic structure, or water saturation (water table).
Seismic methods are commonly used to determine
the depth and structure of geologic and
hydrogeologic units, to estimate hydraulic
conductivity, to detect cavities or voids, to determine
structure stability, to detect fractures and fault
zones, and to estimate ripability. The choice of
method depends upon the information needed and
the nature of the study area. This decision must be
made by a geophysicist who is experienced in both
methods, is aware of the geologic information
needed by the hydrogeologist, and is also aware of
the environment of the study area. The refraction
technique has been used more often than the
reflection technique for hazardous waste site
investigations.
Seismic Refraction Method
Seismic refraction is most commonly used at sites
where bedrock is less than 500 feet below the
ground surface. Seismic refraction is simply the
travel path of a sound wave through an upper
medium and along an interface and then back to the
surface. A detailed discussion of the seismic
refraction technique can be found in Dobrin (1976),
Telford, et. al. (1985), and Musgrave (1967).
Advantages: Seismic refraction surveys are more
common than reflection surveys for site
investigations. The velocities of each layer can be
determined from refraction data, and a relatively
precise estimate of the depth to different interfaces
can be calculated.
Refraction surveys add to depth information in-
between boreholes. Subsurface information can be
obtained between boreholes at a fraction of the cost
of drilling. Refraction data can be used to
determine the depth to the water table or bedrock.
In buried valley areas, refraction surveys map the
depth to bedrock. The velocity information
21
-------
obtained from a refraction survey can be related to
various physical properties of the bedrock. Rock
types have certain ranges of velocities and these
velocities are not always unique to a particular rock
type. However, they can allow a geophysicist to
differentiate between certain units, such as shales
and granites.
Disadvantages: The seismic refraction method
is based on several assumptions. To successfully
resolve the subsurface using the refraction method,
the conditions of the geologic environment must
approximate these assumptions:
the velocities of the layers increase with
depth,
the velocity contrast between layers is
sufficient to resolve the interface, and
the geometry of the geophones in relation
to the refracting layers will permit the
detection of thin layers.
These conditions must be met for accurate depth
information.
Collecting and interpreting seismic refraction data
has several disadvantages. Data collection can be
labor intensive. Also, large line lengths are needed;
therefore, as a general rule, the distance from the
shot, or seismic source, to the first geophone station
must be at least three times the desired depth of
exploration.
Seismic Reflection Method
The seismic reflection method is not as commonly
used on groundwatcr pollution site investigations as
seismic refraction. In the seismic reflection method,
a sound wave travels down to a geologic interface
and reflects back to the surface. Reflections occur
at an interface where there is a change in the
acoustic properties of the subsurface material.
Advantages: The seismic reflection method
yields information that allows the interpreter to
discern between fairly discrete layers, so it is useful
for mapping stratigraphy. Reflection data is usually
presented in profile form, and depths to interfaces
are represented as a function of time. Depth
information can be obtained by converting time
sections into depth measurements using velocities
obtained from seismic refraction data, sonic logs, or
velocity logs. The reflection technique requires
much less space than refraction surveys. The long
offsets of the seismic source from the geophones,
common in refraction surveys, are not required in
the reflection method. In some geologic
environments, reflection data can yield acceptable
depth estimates.
Disadvantages: The major disadvantage to
using reflection data is that a precise depth
determination cannot be made. Velocities obtained
from most reflection data are at least 10% and can
be 20% of the true velocities. The interpretation of
reflection data requires a qualitative approach. In
addition to being more labor intensive, the
acquisition of reflection data is more complex than
refraction data.
The reflection method places higher requirements
on the capabilities of the seismic equipment.
Reflection 'data is commonly used in the petroleum
exploration industry and requires a large amount of
data processing time and lengthy data collection
procedures. Although mainframe computers are
often used in the reduction and analysis of large
amounts of reflection data, recent advances have
allowed for the use of personal computers on small
reflection surveys for engineering purposes. In most
cases, the data must be recorded digitally or
converted to a digital format, to employ various
numerical processing operations. The use of high
resolution reflection seismic methods relies heavily
on the geophysicist, the computer capacity, the data
reduction and processing programs, resolution
capabilities of the seismograph and geophones, and
the ingenuity of the interpreter. Without these
capabilities, reflection surveys are not
recommended.
4.2.5 Ground Penetrating Radar
The ground penetrating radar (GPR) method is
used for a variety of civil engineering, groundwater
evaluation and hazardous waste site applications.
This geophysical method is the most site-specific of
all geophysical techniques, providing subsurface
information ranging in depth from several tens of
meters to only a fraction of a meter. A basic
understanding of the function of the GPR
instrument, together with a knowledge of the
geology and mineralogy of the site, can help
determine if GPR will be successful in the site
assessment. When possible, the GPR technique
should be integrated with other geophysical and
22
-------
geologic data to provide the most comprehensive
site assessment.
The GPR method uses a transmitter that emits
pulses of high-frequency electromagnetic waves into
the subsurface. The transmitter is either moved
slowly across the ground surface or moved at fixed
station intervals. The penetrating electromagnetic
waves are scattered at points of change in the
complex dielectric permittivity, which is a property
of the subsurface material dependent primarily upon
the bulk density, clay content and water content of
the subsurface (Olhoeft, 1984). The
electromagnetic energy which is scattered back to
the receiving antenna on the surface is recorded as
a function of time.
Depth penetration is severely limited by attenuation
of the transmitted electromagnetic waves into the
ground. Attenuation is caused by the sum of
electrical conductivity, dielectric relaxation, and
geometric scattering losses in the subsurface.
Generally, penetration of radar frequencies is
minimized by a shallow water table, an increase in
the clay content of the subsurface, and in
environments where the electrical resistivity of the
subsurface is less than 30 ohm-meters (Olhoeft,
1986). Ground penetrating radar works best in dry
sandy soil above the water table. At applicable
sites, depth resolution should be between 1 and 10
meters (Benson, 1982).
The analog plot produced by a continuously
recording GPR system is analogous to a seismic
reflection profile; that is, data is represented as a
function of horizontal distance versus time. This
representation should not be confused with a
geologic cross section which represents data as a
function of horizontal distance versus depih.
Because very high-frequency electromagnetic waves
in the megahertz range are used by radar systems,
and time delays are measured in nanoseconds (10ฐ
seconds), very high resolution of the subsurface is
possible using GPR. This resolution can be as high
as 0.1 meter. For depth determinations, it is
necessary to correlate the recorded features with
actual depth measurements from boreholes or from
the results of other geophysical investigations.
When properly interpreted, GPR data can optimally
resolve changes in soil horizons, fractures, water
insoluble contaminants, geological features, man-
made buried objects, and hydrologjc features such
as water table depth and wetting fronts.
Advantages
Most GPR systems can provide a continuous display
of data along a traverse which can often be
interpreted qualitatively in the field. GPR is
capable of providing high resolution data under
favorable site conditions. The real-time capability
of GPR results in a rapid turnaround, and allows
the geophysicist to quickly evaluate subsurface site
conditions.
Disadvantages
One of the major limitations of GPR is the site-
specific nature of the technique. Another limitation
is the cost of site preparation which is necessary
prior to the survey. Most GPR units are towed
across the ground surface. Ideally, the ground
surface should be flat, dry, and clear of any brush or
debris. The quality of the data can be degraded by
a variety of factors, such as an uneven ground
surface or various cultural noise sources. For these
reasons, it is mandatory that the site be visited by
the project geophysicist before a GPR investigation
is proposed. The geophysicist should also evaluate
all stratigraphic information available, such as
borehole data and information on the depth to
water table in the survey area.
4.3 SAMPLE PRESERVATION,
CONTAINERS, HANDLING AND
STORAGE
This section is not applicable to this SOP.
4.4 INTERFERENCES AND
POTENTIAL PROBLEMS
See section 4.2.1 for a discussion of limitations of
the magnetic method.
See section 4.2.2 for a discussion of limitations of
the electromagnetic method.
See section 4.2.3 for a discussion of limitations of
the electrical resistivity method.
See section 4.2.4 for a discussion of limitations of
the seismic refraction method and the seismic
reflection method.
23
-------
See section 4.2.5 for a discussion of limitations of
the ground penetrating radar (GPR) method.
4.5 EQUIPMENT/APPARATUS
4.5.1 Magnetics
GEM GSM-19G
magnetometer/gradiometer, EDA OMNI
IV magnetometer/gradiometer,
Geonics 856AGX (with built-in datalogger)
or equivalent
magnetometer base station
300-foot tape measure
non-ferrous survey stakes (wooden or
plastic)
4.5.2 Electromagnetics
Geonics EM-31, EM-34 or equivalent
Polycorder datalogger
Dat 31Q software (data dump software)
300-foot tape measure
survey stakes
4.5.3 Electrical Resistivity
DC resistivity unit (non-specific)
4 electrodes and appropriate cables (length
dependent on depth of survey)
1 or 2 ]2-volt car batteries
300-foot tape measure
4.5.4 Seismic
12- or 24-channcl seismograph (Geometries
2401 or equivalent)
30 lOHz to 14Hz gcophoncs (for
refraction)
30 50H-/. or greater gcophones (for
reflection)
300-foot tape measure
survey stakes
sledge hammer and metal plate or
explosives
4.5.5 Ground Penetrating Radar
GSSI SIR-8 or equivalent
80 Mhz, 100 Mh/. or
antenna/receiver pit
200-foot cable
300-foot tape measure
300 Mh/.
4.6 REAGENTS
This section is not applicable to this SOP.
4.7 PROCEDURES
Refer to the manufacturer's operating manual for
specific procedures relating to operation of the
equipment.
4.8 CALCULATIONS
Calculations vary based on the geophysical method
employed. Refer to the instrument-specific users
manual for specific formulae.
4.9 QUALITY ASSURANCE/
QUALITY CONTROL
The following general quality assurance activities
apply to the implementation of these procedures.
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.
Method-specific quality assurance procedures may
be found in the user's manual.
4.10 DATA VALIDATION
Evaluate data as per the criteria established in
section 4.9 above.
4.11 HEALTH AND SAFETY
When working with potentially ha/.ardous materials,
follow U.S. EPA, OSHA and specific health and
safety procedures.
24
-------
APPENDIX A
Figures
25
-------
Figure 1: Sampling Augers
SOP #2012
U
"JBE
2(5
-------
Figure 2: Sampling Trier
SOP #2012
fl
:.27-2.5-1 cm
(1/2--1")
27
-------
Figure 3: Sampling Train Schematic
SOP #2149
VACUUM
BOX
EVACUATION
PORT
SAMPLING
PORT
PORT
^
r
^rRFFMiMr;
GILIAN
PUMP
l
1/4
1/4" TEFLON TUBING
1/4" I.D. THIN WALL-
TEFLON TUBING
"QUICK CONNECT'
FITTING
1/4" S.S.
SAMPLE PROBE
43
MODELING
/ CLAY
b
SAMPLE
.'/ELL
28
-------
APPENDIX B
HNU Field Protocol
29
-------
HNU Field Protocol
SOP #2149
Startup Procedure
1. 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 socket: do
not force it.
2. Turn the function switch to the battery check
position. The needle on the meter should read
within or above the green area on the scale. If
not, recharge the battery. If the red indicator
light comes on, the battery needs recharging.
3. Turn the function switch to any range setting.
For no more than 2 to 3 seconds, look into the
end of the probe to see if the lamp is on. If it
is on, you will see a purple glow. Do not stare
into the probe any longer than three seconds.
Long term exposure to UV light can damage
the eyes. Also, listen for the hum of the fan
motor.
4. 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
1. Follow the startup procedure.
2. With the instrument set on the 0-20 range, hold
a solvent-based Magic Marker near the probe
tip. If the meter deflects upscale, the
instrument is working.
Field Calibration Procedure
1. Follow the startup procedure and the
operational check.
2. Set the function switch to the range setting for
the concentration of the calibration gas.
3. Attach a regulator (HNU 101-351) to a
disposable cylinder of isobutylene gas. Connect
the regulator to the probe of the HNU with a
piece of clean Tygon tubing. Turn the valve on
the regulator to the "on" position.
4. After 15 seconds, adjust the span dial until the
meter reading equals the concentration of the
calibration gas used. The calibration gas is
usually 100 ppm of isobutylene Ln zero air. The
cylinders are marked in benzene equivalents for
the 10.2 eV probe (approximately 55 ppm
benzene equivalent) and for the 11.7 eV probe
(approximately 65 ppm benzene equivalent).
Be careful to unlock the span dial before
adjusting it. If the span has to be set below 3.0
calibration, the lamp and ion chamber should
be inspected and cleaned as appropriate. For
cleaning of the 11.7 eV probe, only use an
electronic-grade, oil-free freon or similar water-
free, grease-free solvent.
5. Record in the field log: the instrument ID #
(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 used; and the name of the person
who calibrated the instrument.
Operation
1. Follow the startup procedure, operational
check, and calibration check.
2. 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 as necessary.
3. 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.
4. When the activity is completed or at the end of
the day, carefully clean the outside of the HNU
with a damp disposable towel to remove any
30
-------
visible dirt. Return the HNU to a secure area plastic to prevent it from becoming contaminated
and place on charge. and to prevent water from getting inside in the
event of precipitation.
5. With the exception of the probe's inlet and
exhaust, the HNU can be wrapped in clear
31
-------
References
SOPs#2006, 2012, 2149
American Standards for Testing and Materials. 1988. Standard Method for Preparing Test and Split-
Barrel Sampling of Soils: Annual Book of ASTM Standards. Section 4, Volume 4.08. ASTM
D1586-84.
Earth, D.S. and B J. Mason. 1984. Soil Sampling Quality Assurance User's Guide. EPA/600/4-
84/043.
de Vera, E.R., B.Pf Simmons, R.D. Stephen, and D.L. Storm. 1980. Samplers and Sampling
Procedures for Hazardous Waste Streams. EPA/600/2-80/018.
Gilian Instrument Corp. 1983. Instruction Manual for Hi Flow Sampler: HFS 113, HFS 113 T, HFS
113 U, HFS 113 UT.
HNU Systems, Inc. 1975. Instruction Manual for Model PI 101 Photoionization Analyzer.
Mason, B.J. 1983. Preparation of Soil Sampling Protocol: Technique and Strategies. EPA/600/4-
83/020.
National Institute for Occupational Safety and Health. October, 1985. Occupational Safety and Health
Guidance Manual for Hazardous Waste Site Activities. NIOSH/OSHA/USCG/EPA.
New Jersey Department of Environmental Protection. February, 1988. Field Sampling Procedures
Manual.
Roy F. Weston, Inc. 1987. Weston Instrumentation Manual, Volume I.
U.S. Environmental Protection Agency. December, 1984. Characterization of Hazardous Waste Sites -
A Methods Manual: Volume II, Available Sampling Methods, 2nd Edition. EPA/600/4-
84/076.
U.S. Environmental Protection Agency. April 1, 1986. Engineering Support Branch Standard
Operating Procedures and Quality Assurance Manual. U.S. EPA Region IV.
U.S. Environmental Protection Agency. 1987. A Compendium of Superfund Field Operations
Methods. EPA/540/P-87/001. Office of Emergency and Remedial Response. Washington,
D.C. 20460.
SOP #2159
Magnetics
Breincr, S. 1973. Applications Manual for Portable Magnetometers: EG&.G GeoMctrics. Sunnyvale,
California.
Fowler, J. and D. Pasicznyk. February, 1985. Magnetic Survey Methods Used in the Initial Assessment
of a Waste Disposal Site: National Water Well Association Conference on Surface and
Borehole Geophysics.
33
-------
Lilley, F. 1968. Optimum Direction of Survey Lines. Geophysics 33(2): 329-336.
Nettleton, L.L. 1976. Elementary Gravity and Magnetics for Geologists and Seismologists: Society of
Exploration Geophysicists. Monograph Series Number L
Redford, M.S. 1964. Magnetic Anomalies over Thin Sheets. Geophysics 29(4): 532-536.
Redford, M.S. 1964. Airborne Magnetometer Surveys for Petroleum Exploration: Aero Service
Corporation. Houston, Texas.
Vacquier, V. and others. 195L Interpretation of Aeromagnetic Maps: Geological Society of America.
Memoir Number 47.
Electromagnetics
Duran, P.B. 1982. The Use of Electromagnetic Conductivity Techniques in the Delineation of
Groundwater Pollution Plumes: unpublished master's thesis, Boston University.
Grant, F.S. and G.F. West. 1965. Interpretation Theory in Applied Geophysics. McGraw-Hill Book
Company, New York, New York.
Greenhouse, J.P., and D.D. Slaine. 1983. The Use of Reconnaissance Electromagnetic Methods to
Map Contaminant Migration. Ground Water Monitoring Review 3(2).
Keller, G.V. and EC. Frischknecht. 1966. Electrical Methods in Geophysical Prospecting. Pergamon
Press, Long Island City, New York.
McNeill, J.D. 1980. Electromagnetic Terrain Conductivity Measurements at Low Induction Numbers.
Technical Note TN-6, Geonics Limited. Mississauga, Ontario, Canada.
McNeill, J.D. 1980. EM34-3 Survey Interpretation Techniques. Technical Note TN-8, Geonics
Limited. Mississauga, Ontario, Canada.
McNeill, J.D. 1980. Electrical Conductivity of Soils and Rocks. Technical Note TN-5, Geonics
Limited. Mississauga, Ontario, Canada.
McNeill, J.D. and M. Bosnar. 1986. Surface and Borehole Electro-Magnetic Groundwater
Contamination Surveys, Pittman Lateral Transect, Nevada: Technical Note TN-22, Geonics
Limited. Mississauga, Ontario, Canada.
Stewart, M.T. 1982. Evaluation of Electromagnetic Methods for Rapid Mapping of Salt Water
Interfaces in Coastal Aquifers. Ground Water 20.
Telford, W.M., L.P. Geldart, R.E. Sheriff, and D.A. Keys. 1977. Applied Geophysics. Cambridge
University Press. New York, New York.
Electrical Resistivity
Bisdorf, RJ. 1985. Electrical Techniques for Engineering Applications. Bulletin of the Association of
Engineering Geologists 22(4).
34
-------
Grant, F.S. and G.F. West. 1965. Interpretation Theory in Applied Geophysics. McGraw-Hill Book
Company, New York, New York.
Keller, G.V. and EC. Frischnecht. 1966. Electrical Methods in Geophysical Prospecting. Pergamon
Press, Long Island City, New York.
Kelly, W.E. and R.K. Frohlich. 1985. Relations between Aquifer Electrical and Hydraulic Properties.
Ground Water 23:2.
Stollar, R. and P. Roux 1975. Earth Resistivity Surveys -- A Method for Defining ^Groundwater
Contamination. Ground Water 13.
Sumner, J.S. 1976i Principles of Induced Polarization for Geophysical Exploration. Elsevier Scientific
Publishing, New York, New York.
Telford, W.M., L.P. Geldart, R.E. Sheriff, and D.A. Keys. 1977. Applied Geophysics. Cambridge
University Press, New York, New York.
Urish, D.W. 1983. The Practical Application of Surface Electrical Resistivity to Detection of Ground
Water Pollution. Ground Water 2L
Van Nostrand, R.E,, and L.K. Cook. 1966. Interpretation of Resistivity Data: U.S. Geological Survey
Professional Paper 499, Washington, D.C.
Zohdy, AA.R. 1975. Automatic Interpretation of Schlumberger Sounding Curves Uusing Modified
Dar Zarrouk Functions. U.S. Geological Survey Bulletin 1313-E, Denver, Colorado.
ismic
Coffeen, J.A. 1978. Seismic Exploration Fundamentals. PennWell Publishing, Tulsa, Oklahoma.
Dobrin, M.B. 1976. Introduction to Geophysical Prospecting; 3rd ed. McGraw-Hill, New York, New
York.
Griffiths, D.H. and R.E. King. 1981. Applied Geophysics for Geologists and Engineers. Second edition.
Pergamon Press, Oxford, England.
Miller, R.D., S.E. Pullan, J.S. Waldner. and F.P. Haeni. 1986. Field Comparison of Shallow Seismic
Sources. Geophysics 51(11): 2067-92.
Musgrave, A.W. 1967. Seismic Refraction Prospecting. The Society of Exploration Geophysicists.
Tulsa, Oklahoma.
Telford, W.M., L.P. Geldant, R.E. Sheriff, and DA. Keys. 1985. Applied Geophysics. Cambridge
University Press, Cambridge, England.
Ground Penetrating Radar
Benson, R.C., R A. Glaccum, and M.R. Noel. 1982. Geophysical TecJiniques for Sensing Buried Wastes
and Waste Migrations. Technos Inc. Miami, Florida. 236 pp.
35
-------
Olehoft, G.R. 1984. Applications and Limitations of Ground Penetrating Radar: Expanded Abstracts,
Society of Exploration Geophysicists. 54th Annual Meeting: December 2-6, 1984. Atlanta,
Georgia. 147-148.
36
-------
APPENDIX D
Compendium of ERT Surface Water and
Sediment Sampling Procedures
-------
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 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 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
-------
Table of Contents
Section Page
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 SURFACE WATER SAMPLING: SOP #2013
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 5
2.6 Reagents 6
2.7 Procedures 6
2.7.1 Preparation 6
2.7.2 Sampling Considerations 6
2.7.3 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
111
-------
Section Page
3.7.1 Preparation 10
3.7.2 Sample Collection 10
3.8 Calculations 13
3.9 Quality Assurance/Quality Control 13
3.10 Data Validation 13
3.11 Health and Safety 14
APPENDIX A - Figures 15
REFERENCES 23
IV
-------
List of Exhibits
Table 1: Recommended Solvent Rinse for Soluble Contaminants
Figure 1: Kemmerer Bottle
Figure 2: Bacon Bomb Sampler
Figure 3: Dip Sampler
Figure 4: Sampling Auger
Figure 5: Ekman Dredge
Figure 6: Ponar Dredge
Figure 7: Sampling Core Device
SOP
#2006
#2013
#2013
#2013
#2016
#2016
#2016
#2016
Page
4
16
17
18
19
20
21
22
-------
Acknowledgments
Preparation of this document was directed by William A. Coakley, 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.
VI
-------
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 include
the use of brushes, air and wet blasting, and high-
pressure water cleaning, followed 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 dislilled/dcioni/.ecl 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 work 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 oulcr 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 tiAvels
galvani/cd tubs or buckets
lap water
-------
distilled/deionized water
metal/plastic containers for storage and
disposal of contaminated wash solutions
pressurized sprayers for 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 following solvents are
utilized for decontamination purposes:
10% nitric acid(1)
acetone (pesticide grade)(2)
hexane (pesticide grade)(2)
methanol
(l) Only if sample is to be analyzed for trace metals.
m 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 layout 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, involves 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 very fine
abrasives. This method generates a large
amount of waste.
Non-Abrasive Cleaning Methods
Non-abrasive cleaning methods work by forcing the
contaminant off of a surface with pressure. In
general, less of the equipment surface is removed
using non-abrasive methods. The following non-
abrasive methods arc available:
-------
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 m/sec (1,000 atm) to 900 m/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 involve 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 include inorganics.
1. 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 distillcd/deionizcd water.
5. Rinse with 10% nitric acid if ihc sample will be
analyzed for trace organics.
6. Rinse with distilled/dcionized 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/deionizcd 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 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 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 rinsatc 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 rinsatc blank can
detect contamination during sample handling,
storage and sample transportation to the laboratory.
-------
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'0 - 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)
(l) - WARNING: Some organic solvents can permeate and/or degrade protective clothing.
A rinsate 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.
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 VALIDATION
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 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.
-------
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.
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.
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
necessary. 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.
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
-------
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 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, flags, 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 Sampling Considerations
Representative Samples
In order to collect a representative sample, the
hydrology and morphometrics (e.g., measurements
of volume, depth, etc.) of a streamer impoundment
should be determined prior to 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 as follows:
-------
1. Using a properly decontaminated Kemmere/
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 clear 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/QC 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.
2.10 DATA VALIDATION
This section is not applicable to this SOP.
-------
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.
-------
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 cither 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, homogenized, and transferred to the
appropriate sample containers. The homogcni/ation
procedure should not be 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.
-------
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 fine 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/Teflon-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 upon: (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
-------
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 iin 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 "TM 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 0ฐ to 45ฐ 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 "T" 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 pesthole augers. Bucket augers are better for
direct sample recovery, are fast, and provide a large
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 "T" handle to the drill extension
rod.
2. Clear the area to be sampled of any surface
debris.
3. Begin augcring, periodically removing any
accumulated sediment from 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 lip from drill rods and replace
with a precleaned thin-wall tube sampler.
Install proper cutting tip.
6. Carefully lower tube sampler down borehole.
Gradually force lube sampler into sediment.
11
-------
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 cpre (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. Raise the sampler and slowly decant any free
liquid through the top of the sampler. Be
careful to retain fine 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 closing 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
-------
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" 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 further than the tip of
the hammer's guide.
9. Record the length of the tube that penetrated
the sample material, and the number 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 drive head. In this position, the
hammer serves as a handle for the sampler.
11. Rotate the sampler at least two revolutions to
shear off the sample at the bottom.
12. Lower the sampler handle (hammer) until it
just clears the two car-like protrusions on the
drive head, and rotate about 90ฐ.
13. Withdraw the sampler by pulling 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 stainJess 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 QUALITY ASSURANCE/
QUALITY CONTROL
There are no specific quality assurance activities
which apply to the implementation of these
procedures. However, the following QA/QC
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
-------
3.11 HEALTH AND SAFETY
When working with potentially hazardous materials
follow U.S. EPA, OSHA and specific health and
safety procedures.
More specifically, when sampling 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
-------
APPENDIX A
Figures
15
-------
Figure 1: Kemmerer Bottle
SOP #2013
MESSENGER
CABLE
TRIP HEAD
UPPER STOPPER
CHAIN'
CENTER ROD
BODY
BOTTOM DRAIN
LOVฃR STOPPER
16
-------
Figure 2: Bacon Bomb Sampler
SOP #2013
17
-------
Figure 3: Dip Sampler
SOP #2013
18
-------
Figure 4: Sampling Auger
SOP #2016
tz
TUBE
AUGER
BUCKE'
AUGER
19
-------
Figure 5: Ekrnan Dredge
SOP #2016
20
-------
Figure 6: Ponar Dredge
SOP #2016
21
-------
Figure 7: Sample Coring .Device
SOP #2016
PLASTIC
TUBE
BRASS
PLASTIC
22
-------
References
Barlh, D.S. and B.J. Mason. 1984. Soil Sampling Quality Assurance User's Guide. EPA-600/4-84/043.
de Vcra, E.R., B.P. Simmons, R.D. Stephen, and D.L. Storm. 1980. Samplers and Sampling Procedures for
Hazardous Waste Streams. EPA/600/2-80/018.
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-87/001.
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
-------
APPENDIX E
Compendium of ERT
Groundwater Sampling Procedures
-------
EPA/540/P-91/007
OSWER Directive 9360.4-06
January 1991
COMPENDIUM OF ERT GROUNDWATER
SAMPLING PROCEDURES
Sampling Equipment Decontamination
Groundwater Well Sampling
Soil Gas Sampling
Monitoring Well Installation
Water Level Measurement
Well Development
Controlled Pumping Test
Slug Test
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 9360.4-01, EPA/540/G-90/004.
Questions, comments, and recommendations are welcomed regarding the Compendium of ERT Groundwater
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 Groundwater Sampling Procedures, please contact:
National Technical Information Service (NTIS)
U.S. Department of Commerce
5285 Port Royal Road
Springfield, VA 22161
(703) 487-4600
-------
Table of Contents
Section Page
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 GROUNDWATER WELL SAMPLING: SOP #2007
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
2.4.1 General 5
2.4.2 Purging 5
2.4.3 Materials 6
2.5 Equipment/Apparatus 6
2.5.1 General 6
2.5.2 Bailer 8
2.5.3 Submersible Pump 8
2.5.4 Non-Gas Contact Bladder Pump 8
2.5.5 Suction Pump 8
2.5.6 Inertia Pump 8
2.6 Reagents 8
2.7 Procedures 8
2.7.1 Preparation 8
2.7.2 Field Preparation 8
2.7.3 Evacuation of Static Water (Purging) 9
2.7.4 Sampling 11
2.7.5 Filtering 13
2.7.6 Post Operation 13
2.7.7 Special Considerations for VOA Sampling 13
111
-------
Section Page
2.8 Calculations 14
2.9 Quality Assurance/Quality Control 14
2.10 Data Validation 15
2.11 Health and Safety 15
3.0 SOIL GAS SAMPLING: SOP #2149
3.1 Scope and Application 17
3.2 Method Summary 17
3.3 Sample Preservation, Containers, Handling, and Storage 17
3.3.1 Tedlar Bag 17
3.3.2 Tenax Tube 17
3.3.3 SUMMA Canister 17
3.4 Interferences and Potential Problems 18
3.4.1 HNU Measurements 18
3.4.2 Factors Affecting Organic Concentrations in Soil Gas 18
3.4.3 Soil Probe Clogging 18
3.4.4 Underground Utilities 18
3.5 Equipment/Apparatus 18
3.5.1 Slam Bar Method 18
3.5.2 Power Hammer Method 19
3.6 Reagents 19
3.7 Procedures 19
3.7.1 Soil Gas Well Installation 19
3.7.2 Screening with Field Instruments 20
3.7.3 Tedlar Bag Sampling 20
3.7.4 Tenax Tube Sampling 20
3.7.5 SUMMA Canister Sampling 22
3.8 Calculations 22
3.8.1 Field Screening Instruments 22
3.8.2 Photovac GC Analysis 22
3.9 Quality Assurance/Quality Control 22
3.9.1 Field Instrument Calibration 22
3.9.2 Gilian Model HFS113A Air Sampling Pump Calibration 22
3.9.3 Sample Probe Contamination 22
3.9.4 Sample Train Contamination 22
3.9.5 Field Blank 22
3.9.6 Trip Standard 22
3.9.7 Tedlar Bag Check 23
3.9.8 SUMMA Canister Check 23
iv
-------
Section Page
3.9.9 Options 23
3.10 Data Validation 23
3.11 Health and Safety 23
4.0 MONITORING WELL INSTALLATION: SOP #2150
4.1 Scope and Application 25
4.2 Method Summary 25
4.2.1 Hollow Stem Augering 25
4.2.2 Cable Tool Drilling 25
4.2.3 Rotary Drilling 25
4.3 Sample Preservation, Containers, Handling, and Storage 25
4.4 Interferences and Potential Problems 26
4.5 Equipment/Apparatus 26
4.6 Reagents 26
4.7 Procedures 26
4.7.1 Preparation 26
4.7.2 Field Preparation 26
4.7.3 Well Construction 28
4.8 Calculations 29
4.9 Quality Assurance/Quality Control 30
4.10 Data Validation 30
4.11 Health and Safety 30
5.0 WATER LEVEL MEASUREMENT: SOP #2151
5.1 Scope and Application 31
5.2 Method Summary 31
5.3 Sample Preservation, Containers, Handling and Storage 31
5.4 Interferences and Potential Problems 31
5.5 Equipment/Apparatus 32
5.6 Reagents 32
5.7 Procedures 32
5.7.1 Preparation 32
5.7.2 Procedures 32
5.8 Calculations 33
5.9 Quality Assurance/Quality Control 33
5.10 Data Validation 33
5.11 Health and Safety 33
-------
Page
6.0 WELL DEVELOPMENT: SOP #2156
6.1 Scope and Application 35
6.2 Method Summary 35
6.3 Sample Preservations, Containers, Handling, and Storage 35
6.4 Interferences and Potential Problems 35
6.5 Equipment/Apparatus 35
6.6 Reagents 36
6.7 Procedures 36
6.7.1* Preparation 36
6.7.2 Operation 36
6.7.3 Post Operation 37
6.8 Calculations 37
6.9 Quality Assurance/Quality Control 37
6.10 Data Validation 38
6.11 Health and Safety 38
7.0 CONTROLLED PUMPING TEST: SOP #2157
7.1 Scope and Application 39
7.2 Method Summary 39
7.3 Sample Preservation, Containers, Handling, and Storage 39
7.4 Interferences and Potential Problems 39
7.5 Equipment/Apparatus 39
7.6 Reagents 40
7.7 Procedures 40
7.7.1 Preparation 40
7.7.2 Field Preparation 40
7.7.3 Pre-Test Monitoring 40
7.7.4 Step Test 40
7.7.5 Pump Test 41
7.7.6 Post Operation 42
7.8 Calculations 43
7.9 Quality Assurance/Quality Control 43
7.10 Data Validation 43
7.11 Health and Safety 43
8.0 SLUG TEST: SOP #2158
8.1 Scope and Application 45
8.2 Method Summary 45
8.3 Sample Preservation, Containers, Handling and Storage 45
8.4 Interferences and Potential Problems 45
8.5 Equipment/Apparatus 45
8.6 Reagents 45
8.7 Procedures 45
vi
-------
Section Page
8.7.1 Field Procedures 45
8.7.2 Post Operation 47
8.8 Calculations 47
8.9 Quality Assurance/Quality Control 47
8.10 Data Validation 48
8.11 Health and Safety 48
APPENDIX A - Sampling Train Schematic 49
APPENDIX B - HNU Field Protocol 51
APPENDIX C - Forms 55
REFERENCES 61
vn
-------
List of Exhibits
Exhibit SOP
Table 1: Recommended Solvent Rinse for Soluble Contaminants #2006
Table 2: Advantages and Disadvantages of Various Groundwater #2007
Sampling Devices
Table 3: Advantages and Disadvantages of Various Drilling #2150
Techniques
Table 4: Time Intervals for Measuring Drawdown in the #2157
Pumped Well
Table 5: Time Intervals for Measuring Drawdown in an #2157
Observation Well
Figure 1: Sampling Train Schematic #2149
Forms: Well Completion Form #2150
Groundwater Level Data Form #2151
Pump/Recovery Test Data Sheet #2157
Slug Test Data Form #2158
Page
4
7
27
41
41
50
56
57
58
60
Vlll
-------
Acknowledgments
Preparation of this document was directed by William A. Coakley, 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.
-------
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 include
the use of brushes, air and wet blasting, and high-
pressure water cleaning, followed 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 work 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 towels
galvanized tubs or buckets
tap water
-------
distilled/deionized water
metal/plastic containers for storage and
disposal of contaminated wash solutions
pressurized sprayers for 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 following solvents are
utilized for decontamination purposes:
10% nitric acid(1>
acetone (pesticide grade)'2'
hexane (pesticide grade)'2'
methanol
(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 safely 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 layout 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
slcrili/ation, 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, involves 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 cleaning methods work by forcing the
contaminant off of a surface with pressure. In
general, less of the equipment surface is removed
using non-abrasive methods. The following non-
abrasive methods arc available:
-------
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 m/sec (1,000 atm) to 900 m/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 involve 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 include inorganics.
1. 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.
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 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 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.
-------
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(1) - 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)
(i)
- 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 VALIDATION
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 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.
-------
2.0 GROUNDWATER WELL SAMPLING: SOP #2007
2.1 SCOPE AND APPLICATION
The objective of this Standard Operating Procedure
(SOP) is to provide general reference information
on sampling of groundwater wells. This guideline is
primarily concerned with the collection of water
samples from the saturated zone of the subsurface.
Every effort must be made to ensure that the
sample is representative of the particular zone of
water being sampled. These procedures are
designed to be used in conjunction with analyses for
the most common types of groundwater
contaminants (e.g., volatile and semi-volatile organic
compounds, pesticides, metals, biological
parameters).
2.2 METHOD SUMMARY
Prior to sampling a monitoring well, the well must
be purged. This may be done with a number of
instruments. The most common of these are the
bailer, submersible pump, non-gas contact bladder
pump and inertia pump. At a minimum, three well
volumes should be purged, if possible. Equipment
must be decontaminated prior to use and between
wells. Once purging is completed and the correct
laboratory-cleaned sample containers have been
prepared, sampling may proceed. Sampling may be
conducted with any of the above instruments, and
need not be the same as the device used for
purging. Care should be taken when choosing the
sampling device as some will affect the integrity of
the sample. Sampling equipment must also be
decontaminated. Sampling should occur in a
progression from the least to most contaminated
well, if this information is known.
2.3 SAMPLE PRESERVATION,
CONTAINERS, HANDLING, AND
STORAGE
The type of analysis for which a sample is being
collected determines the type of bottle, preservative,
holding time, and filtering requirements. Samples
should be collected directly from the sampling
device into appropriate laboratory-cleaned
containers. Check that a Teflon liner is present in
the cap, if required. Attach a sample identification
label. Complete a field data sheet, a chain of
custody form and record all pertinent data in the
site logbook.
Samples shall be appropriately preserved, labelled,
logged, and placed in a cooler to be maintained at
4ฐC. Samples must be shipped well before the
holding time is over and ideally should be shipped
within 24 hours of sample collection. It is
imperative that these samples be shipped or
delivered daily to the analytical laboratory in order
to maximize the time available for the laboratory to
perform the analysis. The bottles should be shipped
with adequate packing and cooling to ensure that
they arrive intact.
Certain conditions may require special handling
techniques. For example, treatment of a sample for
volatile organic (VOA) analysis with sodium
thiosulfate preservative is required if there is
residual chlorine in the water (such as public water
supply) that could cause free radical chlorination
and change the identity of the original contaminants.
However, sodium thiosulfate should not be used if
chlorine is not present in the water. Special
requirements must be determined prior to
conducting fieldwork.
2.4 INTERFERENCES AND
POTENTIAL PROBLEMS
2.4.1 General
The primary goal of groundwater sampling is to
obtain a representative sample of the groundwater
body. Analysis can be compromised by field
personnel in two primary ways: (1) taking an
unrepresentative sample, or (2) by incorrect
handling of the sample. There are numerous ways
of introducing foreign contaminants into a sample,
and these must be avoided by following strict
sampling procedures and only utilizing trained field
personnel.
2.4.2 Purging
In a non-pumping well, there will be little or no
vertical mixing of the water, and stratification will
-------
occur. The well water in the screened section will
mix with the groundwater due to normal flow
patterns, but the well water above the screened
section will remain isolated, become stagnant and
lack the VOAs representative of the groundwater.
Sampling personnel should realize that stagnant
water may contain foreign material inadvertently or
deliberately introduced from the surface, resulting
in an unrepresentative sample. To safeguard
against collecting nonrepresentative stagnant water,
follow these guidelines during sampling:
As a general rule, all monitoring wells
should be pumped or bailed prior to
sampling. Purge water should be
containerized on site or handled as
specified in the site-specific project plan.
Evacuation of a minimum of one volume of
water in the well casing, and preferably
three to five volumes, is recommended for
a representative sample. In a high-yielding
ground water formation and where there is
no stagnant water in the well above the
screened section, evacuation prior to
sample withdrawal is not as critical.
However, in all cases where the monitoring
data is to be used for enforcement actions,
evacuation is recommended.
For wells that can be pumped or bailed to
dryness with the equipment being used, the
well should be evacuated and allowed to
recover prior to sample withdrawal. If the
recovery rate is fairly rapid and the
schedule allows, evacuation of more than
one volume of water is preferred. If
recovery is slow, sample the well upon
recovery after one evacuation.
A nonrepresentative sample can also result
from excessive pre-pumping of the
monitoring well. Stratification of the
Icachate concentration in the groundwater
formation may occur, or hcavicr-than-watcr
compounds may sink to the lower portions
of the aquifer. Excessive pumping can
dilute or increase the contaminant
concentrations from what is representative
of the sampling point of interest.
2.4.3 Materials
Samplers and evacuation equipment (bladders,
pumps, bailers, tubing, etc.) should be limited to
those made with stainless steel, Teflon, and glass in
areas where concentrations are expected to be at or
near the detection limit. The tendency of organics
to leach into and out of many materials make the
selection of materials critical for trace analyses.
The use of plastics, such as PVC or polyethylene,
should be avoided when analyzing for organics.
However, PVC may be used for evacuation
equipment as it will not come in contact with the
sample.
Table 2 on page 7 discusses the advantages and
disadvantages of certain equipment.
2.5 EQUIPMENT/APPARATUS
2.5.1 General
water level indicator
- electric sounder
- steel tape
- transducer
- reflection sounder
- airline
depth sounder
appropriate keys for well cap locks
steel brush
HNU or OVA (whichever is most
appropriate)
logbook
calculator
field data sheets
chain of custody forms
forms and seals
sample containers
Engineer's rule
sharp knife (locking blade)
tool box (to include at least: screwdrivers,
pliers, hacksaw, hammer, flashlight,
adjustable wrench)
leather work gloves
appropriate health and safety gear
5-gallon pail
plastic sheeting
shipping containers
packing materials
bolt cutters
Ziploc plastic bags
containers for evacuation of liquids
decontamination solutions
tap water
non-phosphate soap
several brushes
-------
Table 2: Advantages and Disadvantages
of Various Groundwater Sampling Devices
Device
Advantages
Disadvantages
Bailer
The only practical limitations are size and
materials
No power source needed
Portable
Inexpensive; it can be dedicated and hung in a
well reducing the chances of cross-
contamination
Minimal outgassing of volatile organics while
sample is in bailer
Readily available
Removes stagnant water first
Rapid, simple method for removing small
volumes of purge water
Time consuming, especially for large wells
Transfer of sample may cause aeration
Submersible
Pump
Portable; can be used on an unlimited number
of wells
Relatively high pumping rate (dependent on
depth and size of pump)
Generally very reliable; does not require
priming
Potential for effects on analysis of trace
organics
Heavy and cumbersome, particularly in
deeper wells
Expensive
Power source needed
Susceptible to damage from silt or sediment
Impractical in low yielding or shallow wells
Non-Gas Contact
Bladder Pump
Maintains integrity of sample
Easy to use
Difficult to clean although dedicated tubing
and bladder may be used
Only useful to approximately 100 feet in
depth
Supply of gas for operation (bottled gas
and/or compressor) is difficult to obtain
and is cumbersome
Suction Pump
Portable, inexpensive, and readily available
Only useful to approximately 25 feet or less
in depth
Vacuum can cause loss of dissolved gases
and volatile organics
Pump must be primed and vacuum is often
difficult to maintain
May cause pH modification
Inertia Pump
Portable, inexpensive, and readily available
Rapid method for purging relatively shallow
wells
Only useful to approximately 70 feet or less
in depth
May be lime consuming to use
Labor intensive
WaTerra pump is only effective in 2-inch
diameter wells
-------
pails or tubs
aluminum foil
garden sprayer
preservatives
distilled or deionized water
2.5.2 Bailer
clean, decontaminated bailer(s) of
appropriate size and construction material
nylon line, enough to dedicate to each well
Teflon-coated bailer wire
sharp knife
aluminum foil (to wrap clean bailers)
5-gallon bucket
2.5.3 Submersible Pump
pump(s)
generator (110, 120, or 240 volt) or 12-volt
battery if inaccessible to field vehicle
1-inch black PVC coil pipe -- enough to
dedicate to each well
hose clamps
safety cable
tool box supplement
- pipe wrenches, 2
- wire strippers
- electrical tape
- heat shrink
- hose connectors
- Teflon tape
winch or pulley
gasoline for generator
flow meter with gate valve
1-inch nipples and various plumbing (i.e.,
pipe connectors)
2.5.4 Non-Gas Contact Bladder Pump
non-gas contact bladder pump
compressor or nitrogen gas tank
batteries and charger
Teflon tubing -- enough to dedicate to each
well
Swagclock fitting
toolbox supplements -- same as
submersible pump
2.5.5 Suction Pump
pump
black coil tubing -- enough lo dedicate to
each well
gasoline - if required
toolbox
plumbing fittings
flow meter with gate valve
2.5.6 Inertia Pump
pump assembly (WaTerra pump, piston
pump)
5-gallon bucket
2.6 REAGENTS
Reagents will be utilized for preservation of samples
and for decontamination of sampling equipment.
The preservation required is 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 prcclcan 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
safely plan.
(>. Identify and mark all sampling locations.
2.7.2 Field Preparation
1. Start tit tin- least contaminated veil, if known.
2. Lay plastic sheeting around the well to
minimi/.e likelihood of contamination of
equipment from soil adjacent to the well.
-------
3. Remove locking well cap, note location, time of
day, and date in field notebook or an
appropriate log form.
4. Remove well casing cap.
5. Screen headspace of well with an appropriate
monitoring instrument to determine the
presence of volatile organic compounds and
record in site logbook.
6. Lower water level measuring device or
equivalent (i.e. permanently installed
transducers or airline) into well until water
surface is encountered.
7. Measure distance from water surface to
reference measuring point on well casing or
protective barrier post and record in site
logbook. Alternatively, if there is no reference
point, note that water level measurement is
from top of steel casing, top of PVC riser pipe,
from ground surface, or some other position on
the well head.
8. Measure total depth of well (do this at least
twice to confirm measurement) and record in
site logbook or on log form.
9. Calculate the volume of water in the well and
the volume to be purged using the calculations
in Section 2.8.
10. Select the appropriate purging and sampling
equipment.
2.7.3 Evacuation of Static Water
(Purging)
The amount of flushing a well receives prior to
sample collection depends on the intent of the
monitoring program as well as the hydrogeologic
conditions. Programs where overall quality
determination of water resources are involved may
require long pumping periods to obtain a sample
that is representative of a large volume of that
aquifer. The pumped volume can be determined
prior to sampling so that the sample is a composite
of known volume of the aquifer, or the well can be
pumped until the stabilization of parameters such as
temperature, electrical conductance, or pH has
occurred.
However, monitoring for defining a contaminant
plume requires a representative sample of a small
volume of the aquifer. These circumstances require
that the well be pumped enough to remove the
stagnant water but not enough to induce flow from
other areas. Generally, three well volumes are
considered effective, or calculations can be made to
determine, on the basis of the aquifer parameters
and well dimensions, the appropriate volume to
remove prior to sampling.
During purging, water level measurements may be
taken regularly at 15- to 30-second intervals. This
data may be used to compute aquifer transmissivity
and other hydraulic characteristics.
The following well evacuation devices are most
commonly used. Other evacuation devices are
available, but have been omitted in this discussion
due to their limited use.
Bailer
Bailers are the simplest purging device used and
have many advantages. They generally consist of a
rigid length of tube, usually with a ball check-valve
at the bottom. A line is used to lower the bailer
into the well and retrieve a volume of water. The
three most common types of bailer are PVC,
Teflon, and stainless steel.
This manual method of purging is best suited to
shallow or narrow diameter wells. For deep, larger
diameter wells which require evacuation of large
volumes of water, other mechanical devices may be
more appropriate.
Bailing equipment includes a clean decontaminated
bailer, Teflon or nylon line, a sharp knife, and
plastic sheeting.
1. Determine the volume of water to be purged as
described in Section 2.7.2, Field Preparation.
2. Lay plastic sheeting around the well to prevent
contamination of the bailer line with foreign
materials.
3. Attach the line to the bailer and lower until the
bailer is completely submerged.
4. Pull bailer out ensuring that the line either falls
onto a clean area of plastic sheeting or never
touches the ground.
-------
5. Empty the bailer into a pail until full to
determine the number of bails necessary to
achieve the required purge volume.
6. Thereafter, pour the water into a container and
dispose of purge waters as specified in the site-
specific project plan.
Submersible Pump
Submersible pumps are generally constructed of
plastic, rubber, and metal parts which may affect the
analysis of samples for certain trace organics and
inorganics. As a consequence, submersible pumps
may not be appropriate for investigations requiring
analyses of samples for trace contaminants.
However, they are still useful for pre-sample
purging. However, the pump must have a check
valve to prevent water in the pump and the pipe
from rushing back into the well.
Submersible pumps generally use one of two types
of power supplies, either electric or compressed gas.
Electric pumps can be powered by a 12-volt DC
rechargeable battery, or a 110- or 220-volt AC
power supply. Those units powered by compressed
gas normally use a small electric compressor which
also needs 12-volt DC or 110-volt AC power. They
may also utilize compressed gas from bottles.
Pumps differ according to the depth and diameter
of the monitoring wells.
1. Determine the volume of water to be purged as
described in section 2.7.2, Field Preparation.
2. Lay plastic sheeting around the well to prevent
contamination of pumps, hoses or lines with
foreign materials.
3. Assemble pump, hoses and safety cable, and
lower the pump into the well. Make sure the
pump is deep enough so that purging does not
evacuate all the water. (Running the pump
without water may cause damage.)
4. Attach flow meter to the outlet hose to
measure the volume of water purged.
5. Attach power supply, and purge well until
specified volume of water has been evacuated
(or until field parameters, such as temperature,
pH, conductivity, etc. have stabilized). Do not
allow the pump to run dry. If the pumping rate
6.
exceeds the well recharge rate, lower the pump
further into the well, and continue pumping.
Collect and dispose of purge waters as specified
in the site-specific project plan.
Non-Contact Gas Bladder Pump
For this procedure, an all stainless-steel and Teflon
Middleburg-squeeze bladder pump (e.g., IEA,
TIMCO, Well Wizard, Geoguard, and others) is
used to provide the least amount of material
interference to the sample (Barcelona, 1985).
Water comes into contact with the inside of the
bladder (Teflon) and the sample tubing, also Teflon,
that may be dedicated to each well. Some wells
may have permanently installed bladder pumps (i.e.,
Well Wizard, Geoguard), that will be used to
sample for all parameters.
1. Assemble Teflon tubing, pump and charged
control box.
2. Use the same procedure for purging with a
bladder pump as for a submersible pump.
3. Be sure to adjust flow rate to prevent violent
jolting of the hose as sample is drawn in.
Suction Pump
There are many different types of suction pumps.
They include: centrifugal, peristaltic and diaphragm.
Diaphragm pumps can be used for well evacuation
at a fast pumping rate and sampling at a low
pumping rate. The peristaltic pump is a low-volume
pump that uses rollers to squeeze the flexible
tubing, thereby creating suction. This tubing can be
dedicated to a well to prevent cross-contamination.
Peristaltic pumps, however, require a power source.
1. Assemble the pump, tubing, and power source
if necessary.
2. To purge with a suction pump, follow the exact
procedures outlined for the submersible pump.
Inertia Pump
Inertia pumps, such as the WaTerra pump and
piston pump, are manually operated. They are
appropriate to use when wells are too deep to bail
by hand, but are not inaccessible enough to warrant
an automatic (submersible, etc.) pump. These
10
-------
pumps are made of plastic and may be either
decontaminated or discarded, after use.
1. Determine the volume of water to be purged as
described in Section 2.7.2, Field Preparation.
2. Lay plastic sheeting around the well to prevent
contamination of pumps or hoses with foreign
materials.
3. Assemble pump, and lower to the appropriate
depth in the well.
4. Begin pumping manually, discharging water into
a 5-gallon bucket (or other graduated vessel).
Purge until specified volume of water has been
evacuated (or until field parameters such as
temperature, pH, conductivity, etc. have
stabilized).
5. Collect and dispose of purge waters as specified
in the site-specific project plan.
2.7.4 Sampling
Sample withdrawal methods require the use of
pumps, compressed air, bailers, and samplers.
Ideally, purging and sample withdrawal equipment
should be completely inert, economical to use, easily
cleaned, sterilized, reusable, able to operate at
remote sites in the absence of power resources, and
capable of delivering variable rates for sample
collection.
There are several factors to take into consideration
when choosing a sampling device. Care should be
taken when reviewing the advantages or
disadvantages of any one device. It may be
appropriate to use a different device to sample than
that which was used to purge. The most common
example of this is the use of a submersible pump to
purge and a bailer to sample.
Bailer
The positive-displacement volatile sampling bailer
(by GPI) is perhaps the most appropriate for
collection of 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, bailers can provide an
acceptable sample, providing that sampling
personnel use extra care in the collection process.
1. Surround the monitoring well with clean plastic
sheeting.
2. Attach a line to the bailer. If a bailer was used
for purging, the same bailer and line may be
used for sampling.
3. Lower the bailer slowly and gently into the
well, taking care not to shake the casing sides
or to splash the bailer into the water. Stop
lowering at a point adjacent to the screen.
4. Allow bailer to fill and then slowly and gently
retrieve the bailer from the well, avoiding
contact with the casing, so as not to knock
flakes of rust or other foreign materials into
the bailer.
5. Remove the cap from the sample container and
place it on the plastic sheet or in a location
where it will not become contaminated. See
Section 2.7.7 for special considerations on VOA
samples.
6. Begin pouring slowly from the bailer.
7. Filter and preserve samples as required by
sampling plan.
8. Cap the sample container tightly and place prc-
labeled sample container in a carrier.
9. Replace the well cap.
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 analytical laboratory.
Submersible Pump
Although it is recommended that samples not be
collected with a submersible pump due to the
reasons stated in Section 2.4, there are some-
situations where they may be used.
1. Allow the monitoring well to recharge after
purging, keeping the pump just above the
screened section.
11
-------
2. Attach gate valve to hose (if not already fitted),
and reduce flow of water to a manageable
sampling rate.
3. Assemble the appropriate bottles.
4. If no gate valve is available, run the water down
the side of a clean jar and fill the sample
bottles from the jar.
5. Cap the sample container tightly and place pre-
labeled sample container in a carrier.
6. Replace the well cap.
7. Log all samples in the site logbook and on the
field data sheets and label all samples.
8. Package samples and complete necessary
paperwork.
9. Transport sample to decontamination zone for
preparation for transport to analytical
laboratory.
10. Upon completion, remove pump and assembly
and fully decontaminate prior to setting into the
next sample well. Dedicate the tubing to the
hole.
Non-Gas Contact Bladder Pump
The use of a non-gas contact positive displacement
bladder pump is often mandated by the use of
dedicated pumps installed in wells. These pumps
are also suitable for shallow (less than 100 feet)
wells. They are somewhat difficult to clean, but
may be used with dedicated sample tubing to avoid
cleaning. These pumps require a power supply and
a compressed gas supply (or compressor). They
may be operated at variable flow and pressure rates
making them ideal for both purging and sampling.
Barcelona (1984) and Nielsen (1985) report that the
non-gas contact positive displacement pumps cause
the least amount of alteration in sample integrity as
compared to other sample retrieval methods.
1. Allow well to recharge after purging.
2. Assemble the appropriate bottles.
3. Turn pump on, increase the cycle time and
reduce the pressure to the minimum that will
allow the sample to come to the surface.
4. Cap the sample container tightly and place pre-
labeled sample container in a carrier.
5. Replace the well cap.
6. Log all samples in the site logbook and on field
data sheets and label all samples.
7. Package samples and complete necessary
paperwork.
8. Transport sample to decontamination zone for
preparation for transport to analytical
laboratory.
9. On completion, remove the tubing from the
well and either replace the Teflon tubing and
bladder with new dedicated tubing and bladder
or rigorously decontaminate the existing
materials.
10. Collect non-filtered samples directly from the
outlet tubing into the sample bottle.
11. For filtered samples, connect the pump outlet
tubing directly to the filter unit. The pump
pressure should remain decreased so that the
pressure build-up on the filter does not blow
out the pump bladder or displace the filter.
For the Geotech barrel filter, no actual
connections are necessary so this is not a
concern.
Suction Pump
In view of the limitations of suction pumps, they are
not recommended for sampling purposes.
Inertia Pump
Inertia pumps may be used to collect samples. It is
more common, however, to purge with these pumps
and sample with a bailer.
1. Following well evacuation, allow the well to
recharge.
2. Assemble the appropriate bottles.
12
-------
3. Since these pumps are manually operated, the
flow rate may be regulated by the sampler.
The sample may be discharged from the pump
outlet directly into the appropriate sample
container.
4. Cap the sample container tightly and place pre-
labeled sample container in a carrier.
5. Replace the well cap.
6. Log all samples in (he site logbook and on field
data sheets and label all samples.
7. Package samples and complete necessary
paperwork.
8. Transport sample to decontamination zone for
preparation for transport to analytical
laboratory.
9. Upon completion, remove pump and
decontaminate or discard, as appropriate.
2.7.5 Filtering
For samples that require filtering, such as samples
which will be analyzed for total metals, the filter
must be decontaminated prior to use and between
uses. Filters work by two methods. A barrel filter
such as the "Geotech" filter works with a bicycle
pump, which is used to build up positive pressure in
the chamber containing the sample. The sample is
then forced through the filter paper (minimum size
0.45 fjm) into a jar placed underneath. The barrel
itself is filled manually from the bailer or directly
via the hose of the sampling pump. The pressure
must be maintained up to 30 psi by periodic
pumping.
A vacuum type filter involves two chambers, the
upper chamber contains the sample and a filter
(minimum size 0.45 /^m) divides the chambers.
Using a hand pump or a Gilian type pump, air is
withdrawn from the lower chamber, creating a
vacuum and thus causing the sample to move
through the filter into the lower chamber where it
is drained into a sample jar, repeated pumping may
be required to drain all the sample into the lower
chamber. If preservation of the sample is necessary,
this should be done after filtering.
2.7.6 Post Operation
After all samples are collected and preserved, the
sampling equipment should be decontaminated prior
to sampling another well. This will prevent
cross-contamination of equipment and monitoring
wells between locations.
1. Decontaminate all equipment.
2. Replace sampling equipment in storage
containers.
3. Prepare and transport water samples to the
laboratory. Check sample documentation and
make sure samples are properly packed for
shipment.
2.7.7 Special Considerations for VOA
Sampling
The proper collection of a sample for volatile
organics requires minimal disturbance of the sample
to limit volatilization and therefore a loss of
volatiles from the sample.
Sample retrieval systems suitable for the valid
collection of volatile organic samples are: positive
displacement bladder pumps, gear driven
submersible pumps, syringe samplers and bailers
(Barcelona, 1984; Nielsen, 1985). Field conditions-
and other constraints will limit the choice of
appropriate systems. The focus of concern must be
to provide a valid sample for analysis, one which has
been subjected to the least amount of turbulence
possible.
The following procedures should be followed:
1. Open the vial, set cap in a clean place, and
collect the sample during the middle of the
cycle. When collecting duplicates, collect both
samples at the same time.
2. Fill the vial to just overflowing. Do not rinse
the vial, nor excessively overfill it. There
should be a convex meniscus on the top of the
vial.
3. Check that the cap has not been contaminated
(splashed) and carefully cap the vial. Place the
cap directly over the top and screw down
firmly. Do not overtighten and break the cap.
13
-------
4. Invert the vial and tap gently. Observe vial for
at least 10 seconds. If an air bubble appears,
discard the sample and begin again. It is
imperative that no entrapped air is in the
sample vial.
5. Immediately place the vial in the protective
foam sleeve and place into the cooler, oriented
so that it is lying on its side, not straight up.
6. The holding time for VOAs is 7 days. Samples
should be shipped or delivered to the laboratory
daily so as not' to exceed the holding time.
Ensure that the samples remain at 4ฐC, but do
not allow them to freeze.
2.8 CALCULATIONS
There are no calculations necessary to implement
this procedure. However, if it is necessary to
calculate the volume of the well, utilize the
following equation:
Well volume = nr2h (cf) [Equation 1]
where:
n
r
h
cf =
radius of monitoring well (feet)
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.]
conversion factor (gal/ft3) = 7.48
gal/ft3 [In this equation, 7.48
gal/ft3 is the necessary conversion
factor.]
Monitoring wells are typically 2, 3, 4, or 6 inches in
diameter. If you know the diameter of the
monitoring 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 monitoring well diameters can be
calculated as follows:
v = nr2 (cf) [Equation 2]
where:
v = volume in gallons per linear foot
n = pi
r = radius of monitoring well (feet)
cf = conversion factor (7.48 gal/ft3)
For a 2-inch diameter well, the volume in gallons
per linear foot can be calculated as follows:
v = nr2 (cf) [Equation 2]
= 3.14 (1/12 ft)2 7.48 gal/ft3
= 0.1632 gal/ft
Remember that if you have a 2-inch diameter, well
you must convert this to the radius in feet to be
able to use the equation.
The volume in gallons per linear foot for the
common size monitoring wells are as follows:
Well Diameter
2 inches
3 inches
4 inches
6 inches
v (volume in gal/ft.)
0.1632
0.3672
0.6528
1.4688
If you utilize the conversion factors above, Equation
1 should be modified as follows:
Well volume = (h)(v) [Equation 3]
where:
h
v
2.9
= height of water column (feet)
= volume in gallons per linear foot as
calculated from Equation 2
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 as
supplied by the manufacturer, unless
14
-------
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.
2.11 HEALTH AND SAFETY
i
When working with potentially hazardous materials,
follow U.S. EPA, OSHA and specific health and
safety procedures. More specifically, depending
upon the site-specific contaminants, various
protective programs must be implemented prior to
sampling the first well. The site health and safety
plan should be reviewed with specific emphasis
placed on the protection program planned for the
well sampling tasks. Standard safe operating
practices should be followed such as minimizing
contact with potential contaminants in both the
vapor phase and liquid matrix through the use of
respirators and disposable clothing.
For volatile organic contaminants:
Avoid breathing constituents venting from
the well.
Pre-survey the well head-space with an
FID/PID prior to sampling.
If monitoring results indicate organic
constituents, sampling activities may be
conducted in Level C protection. At a
minimum, skin protection will be afforded
by disposable protective clothing.
Physical hazards associated with well sampling are:
Lifting injuries associated with pump and
bailer retrieval; moving equipment.
Use of pocket knives for cutting discharge
hose.
Heat/cold stress as a result of exposure to
extreme temperatures (may be heightened
by protective clothing).
Slip, trip, fall conditions as a result of
pump discharge.
Restricted mobility due to the wearing of
protective clothing.
15
-------
3.0 SOIL GAS SAMPLING: SOP #2149
3.1 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 EPA/ERT in installing soil gas
wells; measuring organic levels in the soil gas using
an HNU PI 101 Portable Photoionization Analyzer
and/or other air monitoring devices; and sampling
the soil gas using Tedlar bags, Tenax sorbent tubes,
and SUMMA canisters.
3.2 METHOD SUMMARY
A 3/8-inch diameter hole is driven into the ground
to a depth of 4 to 5 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 1/4-inch O.D. stainless steel probe
is inserted into the hole. The hole is then sealed at
the top around the probe using modeling clay. The
gas contained in the interstitial spaces of the soil is
sampled by pulling 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
CGI/02 Meter, Model 260) and the organic vapor
analyzer (Foxboro OVA, Model 128), can also be
used depending on specific site conditions.
Measurement of soil temperature using a
temperature probe may also be desirable. Bagged
samples arc 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-inch O.D. steel probes) can be
driven to the desired depth using a power hammer
(e.g., Bosch Demolition Hammer). 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.
3.3 SAMPLE PRESERVATION,
CONTAINERS, HANDLING, AND
STORAGE
3.3.1 Tedlar Bag
Soil gas samples are generally contained in 1-L
Tedlar bags. Bagged samples are best stored in
coolers to protect the bags from any damage that
may occur in the field or in transit. In addition,
coolers ensure 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 to 48 hours.
3.3.2 Tenax Tube
Bagged samples can also be drawn into Tenax or'
other sorbent tubes to undergo lab GC/MS 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 samplers
must wear 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 3.7.4.).
3.3.3 SUMMA Canister
The SUMMA canisters used for soil gas sampling
have a 6-L sample capacity and are certified clean
by GC/MS analysis before being utilized in the
field. After sampling is completed, they arc stored
and shipped in travel cases.
17
-------
3.4 INTERFERENCES AND
POTENTIAL PROBLEMS
3.4.1 HNU Measurements
A number of factors can affect the response of the
HNU PI 101. 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 occurring 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.
3.4.2 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 theory, 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.
3.4.3 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 sound of the pump laboring. This
problem can usually be eliminated by using a wire
cable to clear the probe (see procedure #3 in
Section 3.7.1).
3.4.4 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.
3.5 EQUIPMENT/APPARATUS
3.5.1 Slam Bar Method
slam bar (one per sampling team)
soil gas probes, stainless steel tubing, 1/4-
inch O.D., 5 foot length
flexible wire or cable used for clearing the
tubing during insertion into the well
"quick connect" fittings to connect sampling
probe tubing, monitoring instruments, and
Gilian pumps to appropriate fittings on
vacuum box
modeling clay
vacuum box for drawing a vacuum around
Tedlar bag for sample collection (one per
sampling team)
Gilian pump Model HFS113A adjusted to
approximately 3.0 L/min (one to two per
sampling team)
1/4-inch Teflon tubing, 2 to 3 foot lengths,
for replacement of contaminated sample
line
Tedlar bags, 1 liter, at least one bag per
sample point
soil gas sampling labels, field data sheets,
logbook, etc.
HNU Model PI 101, or other field air
monitoring devices, (one per sampling
team)
ice chest, for carrying equipment and for
protection of samples (two per sampling
team)
metal detector or magnetometer, for
detecting underground utilities/
pipes/drums (one per sampling team)
Photovac GC, for field-lab analysis of
bagged samples
SUMMA canisters (plus their shipping
cases) for sample, storage and
transportation
18
-------
3.5.2 Power Hammer Method
Bosch demolition hammer
1/2-inch O.D. steel probes, extensions, and
points
dedicated aluminum sampling points
Teflon tubing, 1/4-inch O.D.
"quick connect" fittings to connect sampling
probe tubing, monitoring instruments, and
Gilian pumps to appropriate fittings on
vacuum box
modeling clay
vacuum box for drawing a vacuum around
Tedlar bag for sample collection (one per
sampling team)
Gilian pump Model HFS113A adjusted to
approximately 3.0 L/min (one to two per
sampling team)
1/4-inch Teflon tubing, 2 to 3 foot lengths,
for replacement of contaminated sample
line
Tedlar bags, 1 liter, at least one bag per
sample point
soil gas sampling labels, field data sheets,
logbook, etc.
HNU Model PI 101, or other field air
monitoring devices, (one per sampling
team)
ice chest, for carrying equipment and for
protection of samples (two per sampling
team)
metal detector or magnetometer, for
detecting underground utilities/
pipes/drums (one per sampling team)
Photovac GC, for field-lab analysis of
bagged samples
SUMMA canisters (plus their shipping
cases) for sample, storage and
transportation
generator with extension cords
high lift jack assembly for removing probes
3.6 REAGENTS
HNU Systems Inc. Calibration Gas for
HNU Model PI 101, and/or calibration gas
for other field air monitoring devices
deionized organic-free water, for
decontamination
methanol, HPLC grade, for
decontamination
ultra-zero grade compressed air, for field
blanks
standard gas preparations for Photovac GC
calibration and Tedlar bag spikes
3.7 PROCEDURES
3.7.1 Soil Gas Well Installation
1. Initially, make a hole slightly deeper than the
desired depth. For sampling up to 5 feet, use
a 5-foot single piston slam bar. For deeper
depths, use a piston slam bar with threaded 4-
foot-long extensions. Other techniques can be
used, so long as holes are of narrow diameter
and no contamination is introduced.
2. After the hole is made, carefully withdraw the
slam bar to prevent collapse of the walls of the
hole. Then insert the soil gas probe.
3. It is necessary to prevent plugging of the probe,
especially for deeper holes. Place a metal wire
or cable, slightly longer than the probe, into the
probe prior to inserting into the hole. Insert
the probe to full depth, then pull it up 3 to 6
inches, then clear it by moving the cable up and
down. The cable is removed before sampling.
4. Seal the top of the sample hole 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. Use the generator-powered
demolition hammer to drive the probe to the
desired depth (up to 12 feet may be attained
with extensions). Pull the probe up 1 to 3
inches if the retractable point is used. No clay
is needed to seal the hole. After sampling,
retrieve the probe using the high lift jack
assembly.
6. If semi-permanent soil gas wells arc required,
use the dedicated aluminum probe points.
Insert these points into the bottom of the
power-driven probe and attach it to the Teflon
tubing. Insert the probe as in step 5. When
the probe is removed, the point and Teflon
tube remain in the hole, which may be scaled
by backfilling with sand, bcntonitc, or soil.
-------
3.7.2 Screening with Field
Instruments
1. The well volume must be evacuated prior 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. Turn
the pump on, and a vacuum is pulled through
the probe for approximately 15 seconds. A
longer time is required for sample wells of
greater depths.
2. After evacuation, connect the monitoring
instrument(s) to the probe using a Teflon
connector. When the reading is stable, or
peaks, record the reading. For detailed
procedures on HNU field protocol, see
' appendix B, and refer to the manufacturer's
instructions.
3. Some readings may be above or below the
range set on the field instruments. The range
may be reset, or the response recorded as a
figure greater than or less than the range.
Consider the recharge rate of the well with soil
gas when sampling at a different range setting.
3.7.3 Tedlar Bag Sampling
1. Follow step 1 in section 3.7.2 to evacuate well
volume. If air monitoring instrument screening
was performed prior to sampling, evacuation is
not necessary.
2. Use the vacuum box and sampling train (Figure
3 in Appendix A) 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.
3. Place the Tedlar bag inside the vacuum box,
and attach it to the sampling port. Attach the
sample probe to the sampling port via Teflon
tubing and a "quick connect" fitting.
4. Draw a vacuum 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. Label bag,
record data on data sheets or in logbooks.
Record the date, time, sample location ID, and
the HNU, or other instrument reading(s) on
sample bag label.
CAUTION: 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.
3.7.4 Tenax Tube Sampling
Samples collected in Tedlar bags may be sorbed
onto Tenax tubes for further analysis by GC/MS.
Additional Apparatus
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 being drawn
onto the sorbent tube.
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-inch to 1/16-inch O.D.
-- Swagelok cat. # SS-400-6-ILV or
equivalent) with a length of 1/4-inch O.D.
Teflon tubing replacing the nut on the 1/6-
inch (Tedlar bag) side. A 1/4-inch I.D.
silicone O-ring replaces the ferrules in the
nut on the 1/4-inch (sorbent tube) side of
the union.
The adapter attaching the sampling syringe
to the sorbent tube consists of a reducing
union (1/4-inch to 1/16-inch O.D. -
Swagelok Cat. # SS-400-6-ILV or
equivalent) with a 1/4-inch I.D. silicone
O-ring replacing the ferrules in the nut on
the 1/4-inch (sorbent tube) side and the
needle of a luer-lock syringe needle
inserted into the 1/16-inch side (held in
place with a 1/16-inch ferrule). The
20
-------
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.
Two-stage glass sampling cartridge (1/4-
inch O.D. x 1/8-inch I.D. x 5 1/8 inch)
contained in a flame-sealed tube
(manufactured by Supelco Custom
Tenax/Spherocarb Tubes or equivalent)
containing two sorbent sections retained by
glass wool:
Front section: 150 mg of Tenax-GC
Back section: 150 mg of CMS
(Carbonized Molecular Sieve)
Sorbent tubes may also be prepared in the
lab and stored in either Teflon-capped
culture tubes or stainless steel tube
containers. Sorbent tubes stored in this
manner should not be kept more than 2
weeks without reconditioning. (See SOP
#2052 for Tenax/CMS sorbent tube
preparation).
Teflon-capped culture tubes or stainless
steel tube containers for sorbent tube
storage. These containers should be
conditioned by baking at 120ฐC for at least
2 hours. The culture tubes should contain
a glass wool plug to prevent sorbent tube
breakage during transport. Reconditioning
of the containers should occur between
usage or after extended periods of disuse
(i.e., 2 weeks or more).
Nylon gloves or lint-free cloth. (Hewlett
Packard Part # 8650-0030 or equivalent.)
Sample Collection
1. Handle sorbent tubes with care, using nylon
gloves (or other lint-free material) to avoid
contamination.
2. Immediately before sampling, break one end of
the sealed tube and remove the Tenax
cartridge. For in-house prepared lubes, remove
cartridge from its container.
3. Connect the valve on the Tcdlar bag to the
sorbcnt tube adapter. Connect the sorbent lube
to the sorbcnt tube adapter with the Tcnax
4.
(white granular) side of the tube facing the
Tedlar bag.
Connect the sampling syringe assembly to the
CMS (black) side of the sorbcnt tube. Fittings
on the adapters should be very tight.
5. Open the valve on the Tedlar bag.
6. Open the on/off valve of the sampling syringe.
7. Draw a predetermined volume of sample onto
the sorbent tube. (This may require closing the
syringe valve, emptying the syringe and then
repeating the procedure, depending upon the
syringe capacity and volume of sample
required.)
8. After sampling, remove the tube from1 the
sampling train with gloves or a clean cloth. Do
not label or write on the Tenax/CMS tube.
9. Place the sorbent tube in a conditioned
stainless steel tube holder or culture tube.
Culture tube caps should be sealed with Teflon
tape.
Sample Labeling
Each sample tube container (not tube) must be
labeled with the site name, sample station number,
sample date, and sample volume.
Chain of custody forms must accompany all samples
to the laboratory.
Quality Assurance
Before field use, a QA check should be performed
on each batch of sorbcnt tubes by analyzing a tube
with thermal dcsorplion/cryogcnic trapping
GC/MS.
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.
21
-------
3.7.5 SUMMA Canister Sampling
1. Follow item 1 in step 3.7.2 to evacuate well
volume. If HNU analysis was performed prior
to taking a sample, evacuation is not necessary.
2. Attach a certified clean, evacuated 6-L
SUMMA canister via the 1/4-inch Teflon
tubing.
3. Open the valve on SUMMA canister. The soil
gas sample is drawn into the canister by
pressure equilibration. The approximate
sampling time foV a 6-L canister is 20 minutes.
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.
3.8 CALCULATIONS
3.8.1 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
3.8.2 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, Photovac GC Analysis for Soil,
Water and Air/Soil Gas.
3.9 QUALITY ASSURANCE/
QUALITY CONTROL
3.9.1 Field Instrument Calibration
Consult the manufacturers' manuals for correct use
and calibration of all instrumentation. The HNU
should be calibrated at least once a day.
3.9.2 Gilian Model HFS113A Air
Sampling Pump Calibration
Flow should be set at approximately 3.0 L/min;
accurate flow adjustment is not necessary. Pumps
should be calibrated prior to bringing into the field.
3.9.3 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 HNU PI 101. If HNU 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. Having more than one
probe per sample team will reduce lag times
between sample stations while probes are
decontaminated.
3.9.4 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 immediately. When sampling in highly
contaminated areas, the sampling train 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 HNU, or other field monitoring device, to
establish the cleanliness of the Teflon line.
3.9.5 Field Blank
Each cooler containing 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 form must accompany each cooler of
samples and should include the blank that is
dedicated to that group of samples.
3.9.6 Trip Standard
Each cooler containing samples should contain a
Tedlar bag of standard gas to calibrate the
22
-------
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 form should
accompany each cooler of samples and should
include the trip standard that is dedicated to that
group of samples.
3.9.7 Tedlar Bag Check
Prior 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.
3.9.8 SUMMA 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
rc-cvacuated and all four canisters from that lot are
available for sampling.
If the chosen canister is contaminated, then the
entire lot of four SUMMA canisters must be
rcclcancd, and a single canister is rc-analy/cd by
GC/MS for certification.
3.9.9 Options
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 criterion applies: if, after
filling the first Tedlar bag, and, evacuating the well
for 15 seconds, the second HNU (or other field
monitoring device being used) reading matches or
is close to (within 50'/'<>) the first reading, a
duplicate sample may be taken.
Spikes
A Tedlar bag spike and Yenax 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 attained 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.
3.10 DATA VALIDATION
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 criteria
apply to target compounds detected in the Tedlar
bag pre-sampling contamination check.
3.11 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, unless the sampling location is
within the hot zone of a site, which requires Level
B or Level C protection. However, to ensure that
the proper level of protection is utilized, constantly
monitor the ambient air using the HNU PI 101 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.
Also, perform an underground utility search prior to
sampling (sec section 3.4.4). When working with
potentially hazardous materials, follow U.S. EPA,
OSHA, and specific health and safety procedures.
-------
4.0 MONITORING WELL INSTALLATION: SOP #2150
4.1 SCOPE AND APPLICATION
The purpose of this Standard Operating Procedure
(SOP) is to provide an overview of the methods
used for monitoring well installation. Monitoring
well installation creates a permanent access for the
collection of samples to determine groundwater
quality and the hydrogeologic properties of the
aquifer in which the contaminants exist. Such wells
should not alter the medium which is being
monitored.
The most commonly used drilling methods are: (1)
hollow-stem augers, (2) cable tool drills, and (3)
rotary drills. Rotary drilling can be divided into a
mud rotary or air rotary method.
4.2 METHOD SUMMARY
There is no ideal monitoring well installation
method for all conditions; therefore, hydrogeologic
conditions at the site and project objectives must be
considered before deciding which drilling method to
use.
4.2.1 Hollow-Stem Augering
Hollow-stem augering is fast and relatively less
expensive than cable tool or rotary drilling methods.
It is possible to drill several hundred feet of
borehole per day in unconsolidated formations.
4.2.2 Cable Tool Drilling
Cable tool drilling method involves lifting and
dropping a heavy, solid chisel-shaped bit, suspended
on a steel cable. This bit pounds a hole through
soil and rock. Temporary steel casing is used while
drilling to keep the hole open and to isolate strata.
The temporary casing is equipped with a drive shoe,
which is attached to the lower end, and which aids
the advancement of the casing by drilling out a
slightly larger diameter borehole than the hole
made by the drill bit alone.
Water is sometimes used when drilling above the
saturated zone to reduce dust and to form a slurry
with the loosened material. This facilitates removal
of cuttings using a bailer or a sand pump. Potable
water or distilled/deionized water should be used to
prevent the introduction of contamination into the
borehole.
4.2.3 Rotary Drilling
Mud Rotary Method
In the mud rotary method, the borehole is advanced
by rapid rotation of the drill bit, which cuts and
breaks the material at the bottom of the hole into
smaller pieces. Cuttings are removed by pumping
drilling fluid (water, or water mixed with bentonite)
down through the drill rods and bit, and up the
annulus between the borehole and the drill rods.
The drilling fluid also serves to cool the drill bit and
prevent the borehole from collapsing in
unconsolidated formations.
Air Rotary Method
The air rotary method is the same as the mud
rotary except that compressed air is pumped down
the drill rods and returns with the drill cuttings up
through the annulus. Air rotary method is generally
limited to consolidated and semi-consolidated
formations. Casing is sometimes used to prevent
cavings in semi-consolidated formations. The air
must be filtered to prevent introduction of
contamination into the borehole.
4.3 SAMPLE PRESERVATION,
CONTAINERS, HANDLING, AND
STORAGE
Often, a primary object of the drilling program is to
obtain representative lithologic or environmental
samples. Lithologic samples are taken in order to
determine the geologic or hydrogeologic regime at
a site. The most common techniques for retrieving
lithologic samples in unconsolidated formations arc
described below.
Split spoon sampling, carried out
continuously or at discrete intervals during
drilling, is used to make a field description
of the sample and create a log of each
boring.
-------
Shelby tube sampling, is used when an
undisturbed sample is required from clayey
or silty soils, especially for geotechnical
evaluation or chemical analysis.
Cuttings description is used when a general
lithologic description and approximate
depths are sufficient.
The most common techniques for retrieving
lithologic sampling in consolidated formations are
described below.
Rock coring is carried out continuously or
at discrete intervals during drilling and
enables the geologist to write a field
description of the sample, create a log of
each boring, and map occurrences and
orientation of fractures.
Cuttings description is used when a general
lithologic description and approximate
depths are sufficient.
4.4 INTERFERENCES AND
POTENTIAL PROBLEMS
Table 3 on page 27 displays the advantages and
disadvantages of the various drilling techniques.
4.5 EQUIPMENT/APPARATUS
The drilling contractor will provide all operational
equipment for the drilling program which is
outlined. The geologist should bring:
well log sheets
metal case (container for well logs)
ruler
depth sounder
water level indicator
all required health and safety gear
sample collection jars
trowels
description aids (Munsell, grain si/.c charts,
etc.)
4.6 REAGENTS
No chemical reagents are used in this procedure.
Decontamination of drilling equipment should
follow ERT SOP #2006, Sampling Equipment
Decontamination and the site-specific work plan.
4.7 PROCEDURES
4.7.1 Preparation
The planning, selection and implementation of any
monitoring well installation program should include
the following steps.
1. Review 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.
2. Visit the site to observe field geology and
potential access problems for drill rig, to
establish water supply, and drill equipment and
materials storage area.
3. Prepare site safety plan.
4. Define project objectives; select drilling, well
development, and sampling methods.
5. Select well construction materials including well
construction specifications (i.e., casing and
screen materials, casing and screen diameter,
screen length and screen interval, filter pack
and screen size).
6. Determine need for containing drill
cuttings/fluids and their disposal.
7. Prepare work plan including all of the above.
8. Prepare and execute the drilling contract.
9. Implement the drilling program.
10. Prepare the final report, including background
data, project objective, field procedure, well
construction data including well logs and well
construction.
All drilling and well installation programs must be
planned and supervised by a professional
gcologist/hydrogeologist.
4.7.2 Field Preparation
1. Prior to the mobili/ation of the drill rig,
-------
Table 3: Advantages and Disadvantages of Various Drilling Techniques
Drilling Type
Advantages
Disadvantages
Auger
Allows sampling from different strata
during drilling.
Less potential for cross-contamination
between strata than in other
techniques.
Large diameter borehole may be
drilled for multiple-well completion.
Less well development is generally needed
than in mud rotary because f the
relatively large diameter boi. 'iole, the
ability to emplace a large and effective
gravel pack, and because no drilling fluids
are introduced into the borehole.
Very slow or impossible in coarse
materials such as cobbles and boulders.
Cannot drill hard rock formations and is
generally not suited for wells deeper than
100 feet.
Not good in caving formations.
Potential for disturbing large volume of
subsurface materials around the borehole;
therefore affecting local permeabilities
and creating annular channels for
contaminant movement between different
strata.
Cable Tool
Allows for easy and accurate detection of
the water table.
Driven casing seals off formation,
minimizing the threat of cross-
contamination in pollution investigation.
Especially successful for drilling in glacial
till.
Extremely slow rate of drilling.
Can lose casing in deep wells.
Mud Rotary
Quite fast, more than 100 feet of borehole
advancement per day is possible.
Geophysical logs such as resistivity (which
must be run in an uncased borehole) can
be run before well construction.
Potential cross-contamination of strata
exposed to the circulating drilling fluid
during drilling.
Difficulty in removing mud residues
during well development.
Drilling mud may alter the groundwater
chemistry by binding metals, sorbing
organic compounds and by altering pH,
cation exchange capacity and chemical
oxidation demand of native fluids.
Drilling mud may change local
permeability of the formation.
Air Rotary
Like mud rotary method, more than 100
feet of borehole advancement a day is
possible.
Sampling different strata during drilling is
possible if temporary casing is advanced.
In contaminated formations, the use of
high pressure air may pose a significant
hazard to the drill crew due to rapid
transport of contaminated material up the
borehole during drilling.
Introduction of air to ground water could
reduce concentration of volatile organic
compounds locally.
-------
thoroughly decontaminate the rig and all
associated equipment to remove all oil, grease,
mud, etc.
2. Before drilling each boring, steam-clean and
rinse all the "down-the-hole" drill equipment
with potable water to minimize cross-
contamination. Special attention should be
given to the thread section of the casings, and
to the drill 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.
3. Record lithologic descriptions and all field
measurements and comments on the well log
form (Appendix C). Include well construction
diagrams on the well log form for each well
installed. At a minimum, the well construction
information should show depth from surface
grade, the bottom of the boring, the screened
interval, casing material, casing diameter, gravel
pack location, grout seal and height of riser
pipe above the ground. Also record the actual
compositions of the grout and seal on the well
log form.
4.7.3 Well Construction
The most commonly used casing materials include
stainless steel, polyvinyl chloride (PVC) and Teflon.
Monitoring wells are constructed with casings and
materials that are resistant to the subsurface
environment. The selection of well construction
material is based on the material's long-term
interaction with the contaminated groundwater.
Construction materials should not cause an
analytical bias in the interpretation of the chemical
analysis of the water samples.
Well casing material should also be judged from a
structural standpoint. Material should be rigid and
nonporous, with a low surface-area-to-water ratio in
the wellbore relative to the formation materials
(U.S. EPA, 1987).
1. Fill the annular space between the well screen
and the boring with a uniform gravel/sand pack
to serve as a filter media. For wells deeper
than approximately 50 feet, or when
recommended by the site geologist, emplace the
sand pack using a tremie pipe (normally
consisting of a 1.25-inch PVC or steel pipe).
Pump sand slurry composed of sand and
potable water through the tremie pipe into the
annulus throughout the entire screened interval,
and over the top of the screen. It is necessary
to pump sufficient sand/gravel slurry to cover
the screen after the sand/gravel pack has
settled and become dense.
2. Determine the depth of the top of the sand
using the tremie pipe, thus verifying the
thickness of the sand pack. Add more sand to
bring the top of the sand pack to approximately
2-3 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.
3. In materials that will not maintain an open
hole, withdraw the temporary or outer casing
gradually during placement of sand pack/grout
to the extent practical.
For example, after filling 2 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 there is no locking of
the permanent (inner) casing in the outer
casing.
4. Emplace a bentonite seal, composed of pellets,
between the sand pack and grout to prevent
infiltration of cement into the filter pack and
the well screen.
These pellets should have a minimum purity of
90% montmorillonite clay, and a minimum dry
bulk density of 75 lb/ft3 for 1/2-inch pellets, as
provided by American Colloid, or equivalent.
Bentonite pellets shall be poured directly down
the annulus.
Care must be taken to avoid introducing pellets
into the well bore. A cap placed over the top
of the well casing before pouring the bentonite
pellets from the bucket will prevent this. To
ensure even application, pour the pellets from
different points around the casing. To avoid
bridging of pellets, they should not be
introduced at a rate faster than they can settle.
A tremie pipe may be used to redistribute and
-------
level out the top of the seal,
5. If using a slurry of bentonite as an annular seal,
prepare it 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, add a few handfuls of
bentonite pellets to solidify the bentonite slurry
surface.
6. Place a mixture of cement and bentonite grout
from the top of the bentonite seal to the
ground 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:
Neat cement, a maximum of 6 gallons of
water per 94-pound bag of cement
Granular bentonite, 1.5 pounds of
bentonite per 1 gallon of water
Cement-bentonite, 5 pounds of pure
bentonite per 94-pound bag of cement with
7-8 gallons of water; 13-14 pounds weight,
if dry mixed
Cement-bentonite, 6 to 8 pounds of pure
bentonite per 94-pound bag of cement with
8-10 gallons of water, if water mixed
Non-expandable cement, mixed at 7.5
gallons of water to 1/2 teaspoon of
aluminum hydroxide, 94 pounds of neat
cement (Type I) and 4 pounds of bentonite
Non-expandable cement, mixed at 7 gallons
of water to 1/2 teaspoon of aluminum
hydroxide, 94 pounds of neat cement (Type
I and Type II)
7. Pump grout through a tremie pipe to the
bottom of the open annulus until undiluted
grout flows from the annulus at the ground
surface.
8. 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.
9. 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.
10. Place the protective casing. Protective casings
should be installed around all monitoring wells.
Exceptions are on a case-by-case basis. The
minimum elements in the protection design
include:
A protective steel cap to keep precipitation
out of the protective casing, secured to the
casing by padlocks.
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
cement grout. The pipe diameter should
be 8 inches for 4-inch wells, and 6 inches
for 2-inch wells (depending on approved
borehole size). A 0.5-inch drain hole near
ground level is permitted.
The installation of guard posts in addition
to the protective casing, in areas where
vehicular traffic may pose a hazard. These
guard posts consist of 3-inch diameter steel
posts or tee-bar driven steel posts. Groups
of three are radially located 4 feet around
each well 2 feet below and 4 feet above
ground surface, with flagging in areas of
high vegetation. Each post is cemented in-
place.
A flush mount of protective casing may
also be used in areas of high traffic or
where access to other areas would be
limited by a well with stickup.
After the grout sets (about 48 hours), fill any
depression due to settlement with a grout mix
similar to that described above.
4.8 CALCULATIONS
To maintain an open borehole using sand or water
rotary drilling, the drilling fluid must exert a
pressure greater than the formation pore pressure.
Typical pore pressure for an unconfincd aquifer is
-------
0.433 psi/ft and for a confined aquifer is 0.465
psi/ft.
The calculation for determining the hydrostatic
pressure of the drilling fluid is:
Hydrostatic Pressure (psi) = Fluid Density
(Ib/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 (ft3) = Vol of Borehole (ft3) -
Vol of Casing (ft3)
= L( r/- rc2)
where:
rB = radius of boring (ft)
rc = radius of casing (ft)
L = length of borehole to be grouted (ft)
4.9 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 standard
well completion forms, field data sheets or
within field/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.
4.10 DATA VALIDATION
This section is not applicable to this SOP.
4.11 HEALTH AND SAFETY
When working with potentially hazardous materials,
follow U.S. EPA, OSHA, and specific health and
safety procedures.
-------
5.0 WATER LEVEL MEASUREMENT: SOP #2151
5.1 SCOPE AND APPLICATION
The purpose of this Standard Operating Procedure
(SOP) is to set guidelines for the determination of
the depth to water in an open borehole, cased
borehole, monitoring well or piezometer.
Generally, water level measurements from
boreholes, piezometers, or monitoring wells are
used to construct water table or potentiometric
surface maps. Therefore, all water level
measurements at a given site should be collected
within a 24-hour period. 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
atmospheric pressure changes
aquifers which are tidally influenced
aquifers affected by river stage,
impoundments, and/or unlined ditches
aquifers stressed by intermittent pumping
of production wells
aquifers being actively recharged due to
precipitation events
5.2 METHOD SUMMARY
A survey mark should be placed on the casing for
use as a reference point for measurement. Many
times 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 (see Appendix C).
Water levels in piezometers and monitoring wells
should be allowed to stabilize for a minimum of 24
hours after well construction and development, prior
to measurement. In low yield situations, recovery
may take longer.
Working with decontaminated equipment, proceed
from the least to the most contaminated wells.
Open the well and monitor headspace with the
appropriate monitoring instrument to determine the
presence of volatile organic compounds. Lower the
water level measurement device into the well until
water surface or bottom of casing is encountered.
Measure distance from water surface to the
reference point on the well casing and record in the
site logbook and/or groundwater level data form.
Remove all downhole equipment, decontaminate as
necessary, and replace well casing cap.
5.3 SAMPLE PRESERVATION,
CONTAINERS, HANDLING AND
STORAGE
This section is not applicable to this SOP.
5.4 INTERFERENCES AND
POTENTIAL PROBLEMS
The chalk used on
contaminate the well.
steel tape may
Cascading water may obscure the water
mark or cause it to be inaccurate.
Many types of electric sounders use metal
indicators at 5-foot intervals around a
conducting wire. These intervals should be
checked with a surveyor's tape to ensure
accuracy.
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. Determining the
thickness and density of the oil layer may
be warranted, in order to determine the
correct water level.
Turbulence in the well and/or cascading
water can make water level determination
difficult with either an electric sounder or
steel tape.
-------
An airline measures drawdown during
pumping. It is only accurate to 0.5 foot
unless it is calibrated for various
"drawdowns".
5.5 EQUIPMENT/APPARATUS
There are a number of devices which can be used to
measure water levels, such as steel tape or airlines.
The device should be adequate to attain an accuracy
of 0.01 feet.
The following equipment is needed to measure
water levels:
air monitoring equipment
water level measurement device
electronic water level indicator
metal tape measure
airline
steel tape
chalk
ruler
notebook
paper towels
decontamination solution and equipment
groundwater level data forms
5.6 REAGENTS
No chemical reagents are used in this procedure,
with the exception of decontamination solutions.
Where decontamination of equipment is required,
refer to ERT 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 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.
5.7.2 Procedures
1. Make sure water level measuring equipment is
in good operating condition.
2. If possible and where applicable, start at those
wells that are least contaminated and proceed
to those wells that are most contaminated.
3. Clean all equipment entering the well by the
following decontamination procedure:
Triple rinse equipment with deionized
water.
Wash equipment with an Alconox solution
followed by a deionized water rinse.
Rinse with an approved solvent (e.g.,
methanol, isopropyl alcohol, acetone) as
per the work plan, if organic contamination
is suspected.
Place equipment on clean surface such as
a Teflon or polyethylene sheet.
4. Remove locking well cap, note location, time of
day, and date in site notebook or an
appropriate groundwater level data form.
5. Remove well casing cap.
6. If required by site-specific condition, monitor
headspace of well with PID or 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
tranducers 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 field logbook. In addition, note that the
-------
9.
water level measurement was from the top of
the steel casing, top of the PVC riser pipe,
from the ground surface, or from some other
position on the well head.
The groundwater level data form in Appendix
C should be completed as follows:
site name
logger name: person taking field notes
date: the date when the water levels are
being measured
location: monitor well number and
physical location
time: the military time at which the water
level measurement was recorded
depth to water: the water level
measurement in feet, or in tenths or
hundreds of feet, depending on the
equipment used
comments: any information the
personnel feels to be applicable
field
measuring point: marked measuring point
on PVC riser 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
notebook or on log form.
11. Remove all downhole equipment, replace well
casing cap and lock steel caps.
12. Rinse all downhole equipment and store for
transport to next well.
13. Note any physical changes such as erosion or
cracks in protective concrete pad or variation in
total depth of well in field notebook and on
field data sheets.
14. Decontaminate all equipment as outlined in
Step 3 above.
5.8 CALCULATIONS
To determine groundwater elevation above mean
sea level, use the following equation:
Ew = E-D
where:
5.9
Ew = Elevation of water above mean sea
level
E = Elevation above sea level at point
of measurement
D = Depth to water
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 personal/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.
Each well should be tested at least twice in
order to compare results.
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.
-------
6.0 WELL DEVELOPMENT: SOP #2156
6.1 SCOPE AND APPLICATION
The purpose of monitoring 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, and overpumping.
Surging involves raising and lowering a surge block
or surge plunger inside the well. The resulting
motion surges water into the formation and loosens
sediment to be pulled from the formation into the
well. Occasionally, sediment 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 around 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 during surging
(Keely and Boateng, 1987).
Jetting involves lowering a small diameter pipe into
the well to 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 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.
Overpumping is not as vigorous as surging and
jetting and is probably the most desirable for
monitoring well development.
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
(e.g. head space air monitoring 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
sediment. Containerize all discharge water from
known or suspected contaminated areas. Record
final measurements in the logbook. Decontaminate
equipment as appropriate prior to use in the next
well.
6.3 SAMPLE PRESERVATION,
CONTAINERS, HANDLING, AND
STORAGE
This section is not applicable to this Standard
Operating Procedure (SOP).
6.4 INTERFERENCES AND
POTENTIAL PROBLEMS
The following interferences or problems may occur
during well development:
The possibility of disturbing the filter pack
increases with surging and jetting well
development methods.
The introduction of external water or air by
jetting may alter the hydrochemistry of the
aquifer.
6.2 METHOD SUMMARY
Development of a well should occur as soon as
practical after installation, but not sooner than 48
hours after grouting is completed, if a rigorous well
development is being used. If a less rigorous
method, such as bailing, is used for development, it
may be initiated shortly after installation. The main
6.5 EQUIPMENT/APPARATUS
The type of equipment used for well development is
dependent on the diameter of the well. For
example, submersible pumps cannot be used for
well development unless the wells are 4 inches or
greater in diameter, because the smallest
-------
submersible pump has a 3 1/4 inch O.D.
In general, the well should be developed shortly
after it is drilled. Most drilling rigs have air
compressors or pumps that may be used for the
development process.
6.6 REAGENTS
No chemical reagents are used in this procedure
except for decontamination solutions. For
guidelines on equipment decontamination, refer to
ERT SOP #2006, Sampling Equipment
Decontamination and the site-specific work plan.
6.7 PROCEDURES
6.7.1 Preparation
1. Coordinate site access and obtain keys to the
monitoring well security cap locks.
2. Obtain information on each well to be
developed (i.e., drilling, method, well diameter,
depth, screened interval, anticipated
contaminants, etc.).
3. Obtain a water level meter, air monitoring
equipment, materials for decontamination, pH
and electrical conductivity meters, a
thermometer, and a stopwatch.
4. Assemble containers for temporary storage of
water produced during 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 (e.g. activated carbon) may be used to
decontaminate the purge water.
6.7.2 Operation
The development should be performed as soon as
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.
1. Assemble necessary equipment on a plastic
sheet around the well.
2. Record pertinent information in field logbook
(personnel, time, location ID, etc.).
3. Open monitoring well, and take air monitoring
readings at the top of casing and in the
breathing zone as appropriate.
4. Measure depth to water and the total depth of
the monitoring well from the same datum
point.
5. Measure the initial pH, temperature, and
specific conductivity of the water and record in
the logbook.
6. Develop the well until the water is clear and
appears to be free of sediment. Note the initial
color, clarity and odor of the water.
7. All water produced by development in
contaminated or suspected contaminated areas
must be containerized or treated. Clearly label
each container with the location ID.
Determination of the appropriate disposal
method will be based on the first round of
analytical results from each well.
8. No water should be added to the well to assist
development without prior approval by the site
geologist. 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 ensure that all injected water is removed
from the formation.
9. Note the final color, clarity and odor of the
water.
10. Measure the final pH, temperature and specific
conductance of the water and record in the
field logbook.
11. Record the following data in the field logbook:
well designation (location ID)
date(s) of well installation
date(s) and time of well development
static water level before and after
-------
development
quantity of water removed and time of
removal
type and size/capacity of pump and/or
bailer used
description of well development techniques
used
6.7.3 Post Operation
1. Decontaminate all equipment.
2. Store containers of purge water produced
during development in a safe and secure area.
3. After the first round of analytical results have
been received, determine and implement the
appropriate purge water disposal method.
6.8 CALCULATIONS
There are no calculations necessary to implement
this procedure. However, if it is necessary to
calculate the volume of the well, utilize the
following equation:
Well volume = nr2h(cf) [Equation 1]
where:
n
r
h
P1
radius of monitoring well (feet)
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/ft3) = 7.48
gal/ft3 [In this equation, 7.48
gal/ft3 is the necessary conversion
factor, because 7.48 gallons of
water occupy 1 ft3]
Monitoring wells are typically 2 inches, 3 inches, 4
inches, or 6 inches in diameter. If the diameter of
the monitoring well is known, a number of standard
conversion factors can be used to simplify the
equation above.
The volume, in gallons per linear foot, for various
standard monitoring well diameters can be
calculated as follows:
v =
where:
v =
n =
r =
cf =
nr2(cf) [Equation 2)
volume in gallons per linear foot
Pi
radius of monitoring well (feet)
conversion factor (7.48 gal/ft3)
For a 2-inch diameter well, the volume per linear
foot can be calculated as follows:
v = nr^cf) [Equation 2]
3.14 (1/12 ft)2 7.48 gal/ft3
0.1632 gal/ft
Remember that if you have a 2-inch diameter well,
you must convert this to the radius in feet to be
able to use the equation.
The volume per linear foot for monitoring wells of
common size are as follows:
Well diameter
2-inch
3-inch
4-inch
6-inch
v (volume in gal/ft.)
0.1632
0.3672
0.6528
1.4688
If you utilize the factors above, Equation 1 should
be modified as follows:
Well volume = h(v) [Equation 3]
where:
h =
v =
height of water column (feet)
volume in gallons per linear foot
from Equation 2
6.9 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 standard
chain of custody forms, field data sheets or
personal/site logbooks.
All instrumentation must be operated in
accordance with operating instructions as
-------
supplied by the manufacturer, unless 6.11 HEALTH AND SAFETY
otherwise specified in the work plan.
Equipment checkout and calibration When working with potentially hazardous materials,
activities must occur prior to f0now U.S. EPA, OSHA, and specific health and
sampling/operation and they must be safety procedures.
documented.
6.10 DATA VALIDATION
This section is not applicable to this SOP.
-------
7.0 CONTROLLED PUMPING TEST: SOP #2157
7.1 SCOPE AND APPLICATION
The most reliable and 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 boundary 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. For
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 characteristics which may be learned using
pumping tests include hydraulic conductivity (K),
transmissivity (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.
This Standard Operating Procedure (SOP) outlines
the protocol for conducting controlled pumping
tests.
7.2 METHOD SUMMARY
It is desirable to monitor pre-test water levels at the
test site for about 1 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. Prior to initiating the long term pump test, a
step test is conducted to estimate the greatest flow
rate that may be sustained 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 and 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 C). The duration of the test is
determinated by project needs and aquifer
properties, but rarely goes beyond 3 days or until
water levels become constant.
7.3 SAMPLE PRESERVATION,
CONTAINERS, HANDLING, AND
STORAGE
This section is not applicable to this SOP.
7.4 INTERFERENCES AND
POTENTIAL PROBLEMS
Interferences and potential problems include:
atmospheric conditions
impact of local potable wells
compression of the aquifer due to trains,
heavy traffic, etc.
7.5 EQUIPMENT/APPARATUS
tape measure (subdivided into tenths of
feet)
submersible pump
water pressure transducer
electric water level indicator
weighted tapes
steel tape (subdivided into tenths of feet)
generator
electronic data-logger (if transducer
method is used)
watch or stopwatch with second hand
semilogarithmic graph paper (if required)
water proof ink pen and logbook
thermometer
appropriate references and calculator
a barometer or recording barograph (for
tests conducted in confined aquifers)
heat shrinks
electrical tape
flashlights and lanterns
pH meter
conductivity meter
discharge pipe
flow meter
39
-------
7.6 REAGENTS
from the pumping well.
No chemical reagents are used for this procedure;
however, decontamination solutions may be
necessary. If decontamination of equipment is
required, refer to ERT SOP #2006, Sampling
Equipment Decontamination and the site-specific
work plan.
7.7 PROCEDURES
7.7.1 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.
7.7.2 Field Preparation
1. 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. Develop the pumping well prior to testing, per
ERT SOP #2156, Well Development.
5. Provide an orifice, weir, flow meter, container
or other type of water measuring device to
accurately measure and monitor the discharge
6. Provide sufficient pipe to transport the
discharge from the pumping well to an area
beyond the expected cone of depression.
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 determination and
sampling.
7.7.3 Pre-Test Monitoring
It is desirable to monitor pretest water levels at the
test site for about 1 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
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 atmospheric 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.
7.7.4 Step Test
Conduct a step test prior to initiating a long term
pumping test. The purpose of a step test is to
estimate the greatest flow rate that may be
sustained during a long term test. The test is
performed by progressively increasing the flow rate
at 1 hour intervals. The generated drawdown versus
time data is plotted on semilogarithmic graph paper,
and the discharge rate is determined from this
graph.
40
-------
7.7.5 Pump Test
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 Tables 4 and 5
below.
Water Level Measurements
Water levels will be measured as specified in ERT
SOP #2151, Well Level Measurement. 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 2 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 C.
During a pumping test, the following data must be
recorded accurately on the aquifer test data form.
1. Site ID -- A number assigned to identify a
specific site.
Table 4: Time Intervals for Measuring
Drawdown in the Pumped Well
Elapsed
Time From Start of Test (Minutes)
0- 10
10- 15
15-60
60-300
300- 1440
1440 - termination
Interval Between Measurements
(Minutes)
0.5-1
1
5
30
60
480
Table 5: Time Intervals for Measuring Drawdown
in an Observation Well
Elapsed
Time From Start of Test (Minutes)
0-60
60- 120
120 - 240
240-360
360- 1440
1440 - termination
Interval Between Measurements
(Minutes)
2
5
10
30
60
480
41
-------
2. Location - The location of the well in which
water level measurements are being taken.
3. Distance from Pumped Well ~ Distance
between the observation well and the pumping
well, in feet.
4. Logging Company -- The company conducting
the pumping test.
5. Test Start Date - The date when the pumping
test began.
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/min)
column divided by the total number of Pumping
Rate (gal/min) 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 have not been recorded
elsewhere, including notes on sampling.
14. Elapsed Time (min) Time of measurement
recorded continuously from start of test (time
00.00).
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/min) -- Flow rate of pump
measured from an orifice, weir, flow meter,
container or other type of water-measuring
device.
Test Duration
The duration of the test is determined by the needs
of the project and properties of the aquifer. One
simple test for determining 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 semilogarithmic graph paper. There are
several exceptions to this simple rule of thumb;
therefore, it should be considered a minimum
criterion. 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 1 to 3 days is
desirable, followed by a similar period of monitoring
the recovery of the water level. Unconfmed
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.
7.7.6 Post Operation
1. After completion of water level recovery
measurements, decontaminate and/or dispose
of equipment as per ERT SOP #2006,
Sampling Equipment Decontamination.
2. When using an electronic data-logger, use the
following procedures.
Stop logging sequence.
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.
42
-------
6. Interpret pumping/recovery test field results.
7.8 CALCULATIONS
There are several accepted methods for determining
aquifer properties such as transmissivity, storativity,
and conductivity. However, the method to use is
dependent on the characteristics of the aquifer
being tested (confined, unconfmed, leaky confining
layer, etc.). When reviewing pump test data, texts
by Fetter, or Driscoll or Freeze and Cherry may be
used to determine the method most appropriate to
your case. See the reference section on page 69.
7.9 QUALITY ASSURANCE/
QUALITY CONTROL
Calibrate all gauges, transducers, flow meters, and
other equipment used in conducting pumping tests
before use at the site.
Obtain records of the instrument calibration and file
with the test data records. The calibration records
will consist of laboratory measurements. If
necessary, perform any on-site zero adjustment
and/or calibration. Where possible, check all flow
and measurement meters on-site using a container
of measured volume and stopwatch; the accuracy of
the meters must be verified before testing proceeds.
7.10 DATA VALIDATION
This section is not applicable to this SOP.
7.11 HEALTH AND SAFETY
When working with potentially hazardous materials,
follow U.S. EPA, OSHA, and specific health and
safety procedures.
43
-------
8.0 SLUG TEST: SOP #2158
8.1 SCOPE AND APPLICATION
This procedure can determine the horizontal
hydraulic conductivity of distinct geologic horizons
under in situ conditions. The hydraulic conductivity
(K) is an important parameter for modeling the
flow of groundwater in an aquifer.
8.2 METHOD SUMMARY
A slug test involves the instantaneous injection of a
slug (a solid cylinder of known volume) or
withdrawal of a volume of water. A slug displaces
a known volume of water from a well and measures
the artificial fluctuation of the groundwater level.
There are several advantages to using slug tests to
estimate hydraulic conductivities. First, estimates
can be made in situ, thereby avoiding errors
incurred in laboratory testing of disturbed soil
samples. Second, compared with pump tests, slug
tests can be performed quickly and at relatively low
cost, because pumping and observation wells are not
required. And last, the hydraulic conductivity of
small discrete portions of an aquifer can be
estimated (e.g., sand layers in a clay).
8.3 SAMPLE PRESERVATION,
CONTAINERS, HANDLING, AND
STORAGE
This section is not applicable to this Standard
Operating Procedure (SOP).
8.5 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.
tape measure (subdivided into tenths of
feet)
water pressure transducer
electric water level indicator
weighted tapes
steel tape (subdivided into tenths of feet)
electronic data-logger (if transducer
method is used)
stainless steel slug of a known volume
watch or stopwatch with second hand
semilogarithmic graph paper (if required)
waterproof ink pen and logbook
thermometer
appropriate references and calculator
electrical tape
21X micrologger
Compaq portable computer or equivalent
with Grapher installed on the hard disk
8.6 REAGENTS
No chemical reagents are used in this procedure;
however, decontamination solvents may be
necessary. When decontaminating the slug or
equipment, refer to ERT SOP #2006, Sampling
Equipment Decontamination, and the site-specific
work plan.
8.4 INTERFERENCES AND
POTENTIAL PROBLEMS
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.
The storage coefficient, S, usually cannot
be determined by this method.
8.7 PROCEDURES
8.7.1 Field Procedures
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 information will be transferred directly to the
main computer and analyzed. Keep a computer
printout of the data in the files as documentation.
If the slug test data is collected and recorded
manually, the slug test data form (Appendix C) will
45
-------
be used to record observations. The slug test data
form should include the following information:
site ID identification number assigned to
the site
location ID - identification of location
being tested
date - the date when the test data were
collected in this order: year, month, day
(e.g., 900131 for January 31, 1990)
slug volume (ft3) manufacturer's
specification for the known volume or
displacement of the slug device
logger identifies the company or person
responsible for performing the field
measurements
test method the slug device either is
injected or lowered into the well, or is
withdrawn or pulled-out from the monitor
well. Check the method that is applicable
to the test situation being run.
comments - appropriate observations or
information for which no other blanks are
provided.
elapsed time (minutes) -- cumulative time
readings from beginning of test to end of
test, in minutes
depth to water (feet) ~ depth to water
recorded in tenths of feet
The following general procedures may be used to
collect and report slug test data. These procedures
may be modified to reflect site-specific conditions:
1. Decontaminate the transducer and cable.
2. Make initial water level measurements on
monitoring wells in an upgradient-to-
downgradicnt sequence, if possible, to minimize
the potential for cross-contamination.
3. Before beginning the slug test, record
information 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.
4. Test wells from least contaminated to most
contaminated, if possible.
5. 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, (sec SOP #2151, Water Level
Measurement).
6. Cover sharp edges of the well casing with duct
tape to protect the transducer cables.
7. Install the transducer and cable in the well to
a depth below the target drawdown estimated
for the test but at least 2 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.
8. Connect the transducer cable to the electronic
data-logger.
9. Enter the initial water level and transducer
design range into the recording device
according to the manufacturer's instructions.
The transducer design range will be stamped
on the side of the transducer. Record the
initial water level on the recording device.
10. "Instantaneously" introduce or remove a 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.
11. Consider the moment of volume addition or
removal as time zero. Measure and record the
depth to water and the time at each reading.
Depths should be measured to the nearest 0.01
foot. The number of depth-time measurements
necessary to complete the test is variable. It is
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 previous aquifer tests
or evaluations.
12. 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 scmilogarithmic plot of time versus
depth.
13. Retrieve slug (if applicable).
-------
Note: 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. If the well is to be used as a monitoring
well, precautions against contaminating it should be
taken. If water is added to the monitoring well, it
should be from an uncontaminated source and
transported in a clean container. Bailers or
measuring devices should be decontaminated prior
to the test. If tests are performed on more than
one monitoring well, care must be taken to avoid
cross-contamination of the wells.
Slug tests should be conducted on relatively
undisturbed wells. If a test is conducted on a well
that has recently been pumped for water sampling
purposes, the measured water level must be within
0.1 foot of the static water level prior to sampling.
At least 1 week should elapse between the drilling
of a well and the performance of a slug test.
8.7.2 Post Operation
When using an electronic data-logger, use the
following procedure:
1. 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.
8.8 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 =
for L/R > 8
where:
K
r
L
hydraulic conductivity [feet/second]
casing radius [feet]
length of open screen (or open borehole)
[feet]
filter pack (borehole) radius [feet]
Basic Time Lag [seconds]; value of t on
semilogarithmic plot of (H-h)/(H-H0)
vs. t, when (H-h)/(H-H0) = 0.37
where:
H = initial water level prior to removal of slug
H0 = water level at t = 0
h = recorded water level at t > 0
(Hvorslev, 1951; Freeze and Cherry, 1979)
The Bower and Rice method is also commonly used
for K calculations. However, it is much more time
consuming than the Hvorslev method. Refer to
Freeze and Cherry or Fetter for a discussion of
these methods.
8.9 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 personal/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.
The following specific quality assurance activity will
apply:
Each well should be tested at least twice in
order to compare results.
2LT0
47
-------
8.10 DATA VALIDATION
This section is not applicable to this SOP.
8.11 HEALTH AND SAFETY
When working with potentially hazardous materials,
follow U.S. EPA, OSHA, and specific health and
safety procedures.
48
-------
APPENDIX A
Sampling Train Schematic
49
-------
Figure 1: Sampling Train Schematic
SOP #2149
VACUUM
BO
1/4" TEFLON TUBING
1/4" I.D. THIN WALL-
TEFLON TUBING
SAMPLING
PORT
1/4" S.S.
SAMPLE PROBE
"QUICK CONNECT
FITTING
MODELING
CLAY
SAMPLE
WELL
50
-------
APPENDIX B
HNU Field Protocol
51
-------
HNU Field Protocol
SOP #2149
Startup Procedure
1. 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 probte cord with the plug in; do
not force.
2. Turn the function switch to the battery check
position. The needle on the meter should read
within or above the green area on the scale. If
not, recharge the battery. If the red indicator
light comes on, the battery needs recharging.
3. Turn the function switch to any range setting.
For no more than 2 to 3 seconds look into the
end of the probe to see if the lamp is on. If it
is on, you will see 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.
4. 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 recheckcd and adjusted,
if necessary. Wait 15 to 20 seconds to ensure
that the zero reading is stable. If necessary,
readjust the zero.
Operational Check
1. Follow the startup procedure.
2. With the instrument set on the 0-20 range, hold
a solvent-based Magic Marker near the probe
tip. If the meter deflects upscale, the
instrument is working.
Field Calibration Procedure
1. Follow the startup procedure
operational check.
and the
2. Set the function switch to the range setting for
the concentration of the calibration gas.
3. Attach a regulator (HNU 101-351) to a
disposable cylinder of isobutylene gas. Connect
the regulator to the probe of the HNU with a
piece of clean Tygon tubing. Turn the valve on
the regulator to the 'on' position.
4. After 15 seconds, adjust the span dial until the
meter reading equals the concentration of the
calibration gas used. The calibration gas is
usually 100 ppm of isobutylene in zero air. The
cylinders are marked in benzene equivalents for
the 10.2 eV probe (approximately 55 ppm
benzene equivalent) and for the 11.7 eV probe
(approximately 65 ppm benzene equivalent).
Be careful to unlock the span dial before
adjusting it. If the span has to be set below 3.0
calibration, the lamp and ion chamber should
be inspected and cleaned as appropriate. For
cleaning of the 11.7 eV probe, only use an
electronic-grade, oil-free frcon or similar water-
free, grease-free solvent.
5. Record in the field log: the instrument ID #
(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 used; and the name of the person
who calibrated the instrument.
Operation
1. Follow the startup procedure, operational
check, and calibration check.
2. 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.
3. 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.
4. When the activity is completed or at the end of
the day, carefully clean the outside of the HNU
with a damp disposable towel to remove any
53
-------
visible dirt. Return the HNU to a secure area plastic to prevent it from becoming contaminated
and place on charge. and to prevent water from getting inside in the
event of precipitation.
5. With the exception of the probe's inlet and
exhaust, the HNU can be wrapped in clear
54
-------
APPENDIX C
Forms
------- An error occurred while trying to OCR this image.
-------
Groundwater Level Data Form
SOP #2151
PAGE OF
SITE NAME:
LOG DATE: LOGGER NAME:
MEASUREMENT REFERENCE POINT: TOP OF GROUND TOP OF CASING
LOCATION '
TIME
DEPTH TO
WATER (FT)
COMMENTS
57
-------
Pump/Recovery Test Data Sheet
SOP #2157
PAGE OF
SITE ID:
LOCATION:
TEST START
DATE:
TIME:
STATIC WATER LEVEL (FT):
AVERAGE PUMPING RATE (GAL/MIN):
DISTANCE FROM PUMPED WELL (FT):
LOGGER:
TEST END
DATE:
TIME:
STATIC WATER LEVEL (FT):
MEASUREMENT METHODS:
COMMENTS:
ELAPSED
TIME
(MIN)
0.00
PUMP TEST
DEPTH TO
WATER (FT)
PUMPING
RATE
(GAL/MIN)
RECOVERY
TEST ELAPSED
TIME (MIN)
0.00
DEPTH TO
WATER (FT)
58
-------
Pump/Recovery Test Data Sheet (Continued)
SOP #2157
PAGE OF
SITE ID: DATE:
LOCATION: LOGGER:
ELAPSED
TIME
(MIN)
PUMP TEST
DEPTH TO
WATER (FT)
PUMPING
RATE
(GAL/MIN)
RECOVERY
TEST ELAPSED
TIME (MIN)
DEPTH TO
WATER (FT)
59
-------
Slug Test Data Form
SOP #2158
PAGE OF
DATE:
SITE ID:
LOCATION ID:
SLUG VOLUME (FT3):
LOGGER:
TEST METHOD: SLUG INJECTION SLUG WITHDRAWAL
COMMENTS:
TIME (Begin Test #1):
TIME (End Test #1):
ELAPSED TIME
(MIN)
DEPTH TO WATER
(FT)
TIME (Begin Test #2):
TIME (End Test #2):
ELAPSED TIME
(MIN)
DEPTH TO WATER
(FT)
60
-------
References
Barcelona, MJ., JA. Helfrich, E.E. Garske, and J.P. Gibb. Spring 1984. A Laboratory Evaluation of
Groundwater Sampling Mechanisms. Groundwater Monitoring Review, pp. 32-41.
Barcelona, MJ., JA. Helfrich, and E.E. Garske. 1985. Sampling Tubing Effects on Groundwater Samples.
Anafy. Chem. 57: 460-463.
Boateng, K., P.C. Evens, and S.M. Testa. 1984. Groundwater Contamination of Two Production Wells: A
Case History. Groundwater Monitoring Review. 4 (2): 24-31.
Boulton, N.S. 1954. T,he 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. 3:
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. 26: 469-82.
Bower, H. 1978. Groundwater Hydrology. McGraw-Hill, New York, New York.
Bower, H. and R.C. Rice. 1976. A Slug Test for Determining Hydraulic Conductivity of Unconfined
Aquifers with Completely or Partially Penetrating Wells. Water Resources Research. 12 (3): 233-238.
Bredehoeft, J.D. and S.S. Papadopulos. 1980. A Method of Determining the Hydraulic Properties of Tight
Formations. Water Resources Research. 16 (1): 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. 13 (1).
Cooper, Jr., H.H., and C.E. Jacob. 1946. A Generalized Graphical Method for Evaluating Formation
Constants and Summarizing Well-Field History. American Geophysical Union Transactions. 27 (4):
526-534.
Driscoll, F.G. 1986. Groundwater and Wells (2nd ed.) Johnson Division, UOP Inc., St. Paul, Minnesota.
1089 pp.
Earlougher, R.C. 1977. Advances in Well Test Analysis. Society of Petroleum Engineers of AIME.
Ferris, J.G., and D.B. Knowles. 1954. The Slug Test for Estimating Transmissivity. U.S. Geological Survey.
Ground Water Note 26.
Fetter, Charles W., Jr. 1980. Applied Hydrogeology. Merrill, Columbus, Ohio.
Freeze, R. Allen and John A. Cherry. 1979. Groundwater. Prentice-Hall, Inc., Englewood Cliffs, New
Jersey.
Gibb, J.P., R.M. Schuller, and RA. Griffin. March 1980. Monitoring Well Sampling and Preservation
Techniques. EPA/600/9-80/010.
Gilian Instrument Corp. 1983. Instruction Manual for Hi Flow Sampler: HFS113, HFS 113 T, HFS 113U,
HFS 113 UT.
HNU Systems, Inc. 1975. Instruction Manual for Model PI 101 Photoionization Analyzer.
61
-------
Hvorslev. 1951. Time Lag and Soil Permeability in Ground Water Observations, Bulletin No. 36, U.S. Army
Corps of Engineers, p. 50.
Instrument Specialties Company. January 1980. Instruction Manual, Model 2100 Wastewater Sampler.
Lincoln, Nebraska.
Johnson Division, UOP, Inc. 1966. Ground Water and Wells. St. Paul, Minnesota.
Keely, J.F. and Kwasi Boateng. 1987. Monitoring Well Installation, Purging, and Sampling Techniques -
Part 1: Conceptualizations. Groundwater. 25 (3): 300-313.
Keely, J.F. and Kwasi Boateng. 1987. Monitoring Well Installation, Purging, and Sampling Techniques -
Part 2: Case Histories. Groundwater. 25 (4): 427-439.
Korte, Nic, and Dennis Ealey. 1983. Procedures for Field Chemical Analyses of Water Samples. U.S.
Department of Energy, GJ/TMC-07, Technical Measurements Center, Grand Junction Project
Office.
Korte, Nic, and Peter Kearl. 1985. Procedures for the Collection and Preservation of Groundwater and
Surface Water Samples and for the Installation of Monitoring Wells: Second Edition, U.S.
Department of Energy: GJ/TMC-08, Technical Measurements Center, Grand Junction Projects
Office.
Lohman, S.W. 1982. Ground Water Hydraulics. U.S. Geological Survey. Paper 708, p. 70.
National Council of the Paper Industry for Air and Stream Improvement, Inc. January 1982. A Guide to
Groundwater Sampling. Technical Bulletin No. 362. Madison, New York.
National Institute for Occupational Safety and Health. October 1985. Occupational Safety and Health
Guidance Manual for Hazardous Waste Site Activities.
Neuman, S.P. 1972. Theory of Flow in Unconfined Aquifers Considering Delayed Response of the Water
Table. Water Resources Research. 8 (4): 1031.
New Jersey Department of Environmental Protection. February 1988. Field Sampling Procedures Manual.
Nielsen, David M. and Yeates, Gillian L. Spring 1985. A Comparison of Sampling Mechanisms Available
for Small-Diameter Groundwater Monitoring Wells. Groundwater Monitoring Review, pp. 83-99.
Papadopulos, S.S., J.D. Bredehoeft, H.H. Cooper, Jr. 1973. On the Analysis of Slug Test Data. Water
Resources Research. 9 (4): 1087-1089.
Roy F. Weston, Inc. 1987. Weston Instrumentation Manual. Volume I.
Scalf M. J., et al. 1980. Manual for Groundwater Sampling Procedures. R.S. Kerr Environmental Research
Laboratory, Office of Research and Development. Ada, Oklahoma.
Sisk, S.W. 1981. NEIC Manual for Ground/Surface Investigations at Hazardous Waste Sites.
EPA/330/9-81/002.
Todd, David K. 1980. Ground Water Hydrology (2nd ed.) John Wiley & Sons, New York, New York.
U.S. Department of the Interior. National Handbook of Recommended Methods for Water-Data Acquisition.
Reston, Virginia.
62
-------
U.S. Department of the Interior. 1977. Ground Water Manual, Bureau of Reclamation. U.S. Government
Printing Office, New York, New York.
U.S. Environmental Protection Agency. August 1977. Procedures Manual for Groundwater Monitoring at
Solid Waste Disposal Facilities. EPA/530/SW/611.
U.S. Environmental Protection Agency. 1981. Manual of Groundwater Quality Sampling Procedures.
EPA/600/2-81/160. Washington, D.C.
U.S. Environmental Protection Agency. 1982. Handbook for Chemical and Sample Preservation of Water
and Wastewater. EPA/600/4-82/029. Washington, D.C.
U.S. Environmental Protection Agency. 1983. Methods for Chemical Analysis of Water and Waste.
EPA/600/4-79/020. Washington, D.C.
U.S. Environmental Protection Agency. December, 1984. Characterization of Hazardous Waste Sites - A
Methods Manual: Volume II, Available Sampling Methods, 2nd Edition. EPA/600/4-84/076.
U.S. Environmental Protection Agency. 1984. Test Methods for Evaluation of Solid Waste. EPA-SW-846.
Second Edition. Washington, D.C.
U.S. Environmental Protection Agency. September 1985. Practical Guide for Groundwater Sampling.
EPA/600/2-85/104.
US. Environmental Protection Agency. April 1, 1986. Engineering Support Branch Standard Operating
Procedures and Quality Assurance Manual. U.S. EPA Region IV.
U.S. Environmental Protection Agency. September 1986. RCRA Groundwater Monitoring Technical
Enforcement Guidance Document. OSWER-9950-1.
U.S. Environmental Protection Agency. 1987. A Compendium of Superfund Field Operations Methods.
EPA/540/P-87/001. Office of Emergency and Remedial Response. Washington, D.C. 20460.
63
U S. GOVERNMENT PRINTING OFFICE: 1993-341-932/92611
------- |