Environmental Investigations
Standard Operating Procedures
and
Quality Assurance Manual
May 1996
U.S. Environmental Protection Agency
Region 4
960 College Station Road
Athens, Georgia 30605-2700
(706)546-3117
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EISOPQAM
TABLE of CONTENTS
SECTION 1 - Preface 1-1
1.1 Introduction 1-1
1.2 Performance Objectives 1-1
1.3 Section Objectives 1-1
SECTION 2 - Investigations, Inspections, and Overview Activities . 2-1
2.1 Introduction . . . . 2-1
2.2 Potable Water Supply Investigations 2-2
2.3 Civil Enforcement Investigations and Studies 2-3
2 3 1 Introduction 2-3
232 Facility Entry 2-3
233 Unreasonable Search and Seizure . 2-4
234 Requesting Information 2-5
235 Photographs 2-5
236 Split Samples 2-6
2.4 Criminal Investigations and Studies 2-6
2.5 Clean Water Act Compliance Monitoring Inspections 2-7
2 5 1 Introduction 2-7
252 CWA Inspection Types . .2-7
253 Study Plans . 2-10
254 NPDES Compliance Inspection Reports . 2-10
2.6 Superfund Investigations, Technical Assistance, and Overview Activities .2-11
2 6 1 Introduction . . . 2-11
262 Superfund Investigation Types 2-11
263 Planning for Field Investigative Support . . 2-11
264 Requests for Superfund Studies 2-12
265 Investigation Study Plans . . . 2-12
266 Investigation Reports . 2-13
2.7 RCRA Inspections, Investigations, and Overview Activities 2-14
2.7 1 Introduction 2-14
2 7.2 RCRA Investigation Types 2-14
2 7.3 Planning for Field Investigative Support 2-15
274 Requests for RCRA Studies 2-15
275 Investigation Study Plans 2-15
276 Investigation Reports . . . . .2-16
2.8 Underground Storage Tank (UST) Investigations 2-17
2 8 1 Introduction 2-17
282 Investigation Reports 2-17
2.9 Underground Injection Control (UIC) Investigations 2-18
2 9 1 Introduction .2-18
292 Investigation Reports . . 2-18
2.10 Ambient Air Monitoring Evaluations and Audits 2-19
2 10.1 Introduction . 2-19
2 10 2 NAMS/SLAMS Site Evaluations . . 2 -19
Table 2.10.1 - Guidelines for PM10 and SO2 NAMS Network Size 2-20
EISOPQAM ToC -1 May 1996
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Table 2.10.2 - Population Levels for which NAMS Monitoring of Pollutants
other than PMIO and SO, is Required 2-21
Table 2 10.3 - Summary of Spacial Scales Usually Needed for SLAMS and NAMS 2 -21
2.10 3 Slate and Local QA Plan Reviews 2-22
Table 2 10.4 - Summary of Probe Siting Criteria 2-23
Table 2.10.5 - Minimum Distance between Sampling Probe and Roadways . 2 -24
2104 Performance Audits 2-25
2 10.5 National Air Monitoring Audit System 2-27
2106 National Performance Audit Program . 2-28
2.11 References 2-29
Exhibit 2.1 - Hazardous Waste Field Overview Checklist 2-30
Exhibit 2.2 - State Contractor Overview Checklist 2-45
Exhibit 2.3 - State Program Evaluation - Hazardous Waste Field Activities . 2 -48
SECTION 3 - Sample Control, Field Records, and Document Control 3-1
3.1 Introduction 3-1
3.2 Sample and Evidence Identification 3-2
3 2 1 Sample Identification 3-2
3.2 2 Photograph Identification 3-3
3.2.3 Identification of Physical Evidence ..3-3
3.3 Chain of Custody Procedures 3-4
3.3 1 Introduction 3-4
332 Sample Custody . . 3-4
333 Documentation of Cham-of-Custody 3-4
334 Transfer of Custody with Shipment 3-7
3.4 Receipt for Samples Form (CERCLA/RCRA/TSCA) 3-7
3 4 ] Introduction .3-7
342 Receipt for Samples Form . .3-7
3.5 Field Records . 3-8
3.6 Document Control . . 3-9
3.7 Disposal of Samples or Other Physical Evidence .. ... . 3-10
3.8 Field Operations Records Management System (FORMS) 3-10
Figure 3-1 - Sample Tag 3-11
Figure 3-2 - EPA Custody Seal 3-12
Figure 3-3 - Cham-of-Custody Form 3-13
Figure 3-4 - Receipt for Samples Form . . 3 -14
SECTION 4 - Branch Safety Protocols 4-1
4.1 Introduction 4-1
4.2 Hazard Communication Procedure . . 4-2
4 2 1 Introduction 4-2
422 Scope 4-2
423 Labels and Other Forms of Warnings 4-2
424 Material Safety Data Sheets (MSDSs) 4-3
425 The Hazard Chemical Inventory . . 4-3
4.3 Safety Protocols 4-4
4 3 1 Site Safety Officer Duties 4-4
4 3.2 Safety Equipment 4-5
EISOPQAM ToC - ii May 1996
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433 OSHA Confined Space Entry 4-5
4.3 4 Entry into Enclosed Areas 4-6
4.3.5 Training Status Tracking System 4-6
4 3.6 Sue Operations 4-7
Figure 4-1 - Decontamination Zone for Levels A and B . 4-19
Figure 4-2 - Decontamination Zone for Level C 4-20
Exhibit 4.1 - Site Safety Plan 4-22
SECTION 5 - Sampling Design and Quality Assurance Procedures . 5-1
5.1 Introduction .... . . . 5-1
5.2 Definitions 5-1
5.3 Sampling Design 5-5
5.3 1 Introduction 5-5
532 Representative Sampling 5-5
533 Stratification and Heterogeneous Wastes 5-5
534 Specific Sampling Designs . . 5-6
5.3.5 Determining the Number of Samples to Collect 5-6
5.3 6 Authoritative or Directed Sampling . 5-6
5.3 7 Simple Random Sampling 5-6
5.3 8 Systematic Sampling over Time or Space 5-6
5.3.9 Stratified Random Sampling 5-7
5.3.10 Systematic Grid Sampling 5-7
5.4 General Considerations for Sampling Designs . 5-8
5.5 Soil Sampling Designs 5-9
5 5 1 Historical Sampling Data, Sue Survey, and Site History . ... 5-9
552 Data Quality Objectives (DQOs) 5-9
553 Authoritative Designs for Soil Investigations 5-9
554 Systematic Grid Sampling Designs for Soil Investigations .5-10
5.6 Ground Water Sampling Designs 5-15
5 6 1 Single Source Iterative Programs . 5-15
562 Multiple-Source Area Grided Programs . . 5-16
563 Typical Ground Water Screening Devices . . . .5-16
5.7 Surface Water and Sediment Sampling Designs . . .5-18
5 7.1 Sampling Site Selection . . 5 -L8
572 Rivers, Streams, and Creeks . . 5 -19
573 Lakes, Ponds, and Impoundments 5-21
5 7.4 Estuanne Waters 5-22
575 Control Stations 5-23
5.8 Waste Sampling Designs 5-24
5 8 1 Introduction 5-24
582 Waste Investigation Objectives 5-24
583 Considerations for Waste Sampling Designs 5-25
584 Waste Sampling Equipment 5-25
5 8.5 Field Screening 5-26
Figure 5-1 - RCRA Waste Characterization Flow Chart 5-27
5.9 Wastewater Sampling Designs 5-28
5.10 UST and UIC Sampling Designs . 5-29
5.11 Air Toxics Monitoring Designs 5-30
5.12 Data Quality Objectives 5-31
EISOPQAM ToC - in May 1996
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5.13 Specific Sample Collection Quality Control Procedures . 5 -33
5131 Introduction . . . 5-33
5132 Experience Requirements 5-33
5.13.3 Traceabiltty Requirements 5-33
5134 Cham-of-Custody . . 5-33
5135 Sampling Equipment Construction Material 5-33
5136 Sample Preservation . . 5-34
5137 Special Precautions for Trace Contaminant Sampling 5-34
5 13 8 Sample Handling and Mixing 5-35
5139 Special Handling of Samples for Volatile Organic Compounds (VOCs) Analysis 5 -35
5.13 10 Estimating Variability 5-36
5 13.12 Special Quality Control Procedures for Water Samples for Extractable Organic
Compounds, Pesticides, or Herbicides Analysis (Matrix Duplicate) 5-38
51313 Special Quality Control Procedures for EPA Contract Laboratories . 5 -38
51314 Special Quality Control Procedures for Dioxins and Furans 5-39
5.14 Internal Quality Control Procedures 5-39
5 14 1 Introduction . . . 5-39
5 14.2 Traceabihty Requirements 5-39
5 14 3 Specific Quality Control Checks 5-40
5.15 Investigation Derived Waste (IDW) 5-41
5 15 1 Types of IDW 5-41
5152 Management of Non-Hazardous IDW . .5-41
5 15 3 Management of Hazardous IDW 5-42
Table 5.151- Disposal of IDW 5-43
5.16 References . . .5-44
SECTION
6.1
6.2
6.3
63 1
632
633
6.34
6.4
64 ]
642
644
645
646
647
648
6.5
6.5 1
6.5.2
6.6
6.6 1
662
663
6 • Design and Installation of Monitoring Wells
Introduction ... .
Permanent Monitoring Wells - Design Considerations . .
Drilling Methods .
Hollow-Stem Auger . ...
Solid-Stem Auger . .
Rotary Methods . . . . .
Other Methods .
Borehole Construction
Annular Space . . . .
Overdnlling the Borehole ,
Filter Pack Seal-Bentomte Pellei Seal (Plug)
Grouting the Annular Space ,
Above Ground Riser Pipe and Outer Protective Casing
Concrete Surface Pad
Surface Protection-Bumper Guards
Construction Techniques
Well Installation
Double Cased Wells
Well Construction Materials
Introduction
Well Screen and Casing Materials .... ...
Filter Pack Materials
6-1
6-1
6-1
6-2
6-2
.6-2
. . 6-3
. . . . 6-4
6-4
. . 6-4
6-4
6-5
6-5
6-6
6-6
6-6
6-7
6-7
6-8
6-10
6-10
6-10
6-11
EISOPQAM ToC - iv May 1996
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664 Filter Pack and Well Screen Design 6-11
6.7 Safety Procedures for Drilling Activities 6-12
6.8 Well Development 6-13
6.9 Well Abandonment . 6-14
6.9 1 Abandonment Procedures 6-14
6.10 Temporary Monitoring Well Installation 6-15
6 10 1 Introduction 6-15
6 10 2 Data Limitation . 6-15
6 10 3 Temporary Well Materials .6-16
6104 Temporary Monitoring Well Borehole Construction 6-16
6 10 5 Temporary Monitoring Well Types 6-16
6106 Backfilling 6-17
SECTION 7 - Ground Water Sampling 7-1
7.1 Introduction 7 . 1
7.2 Purging . 1-2
7 2.1 Purging and Purge Adequacy . . 1-2
Table 7.2.1 - Well Casing Diameter vs Volume (Gals.)/Feet of Water ... . 7-3
7.2 2 Purging Techniques (Wells Without Plumbing or In-Place Pumps) 7-4
723 Purging Techniques - Wells with In-Place Plumbing 7-6
724 Purging Techniques - Temporary Monitoring Wells 7-6
7.3 Sampling 7.7
7 3 1 Equipment Available .7-7
7 3.2 Sampling Techniques - Wells with In-Place Plumbing 7-8
733 Sampling Techniques - Wells without Plumbing 7-8
734 Sample Preservation 7.9
735 Special Sample Collection Procedures 7-9
736 Specific Sampling Equipment Quality Assurance Techniques 7-11
737 Auxiliary Data Collection 7 -11
7.4 References ... . . . 7-12
SECTION 8 - Sampling of Potable Water Supplies
8.1 Introduction ... ..... 8-1
8.2 Sampling Site Selection 8-1
8.3 Reference 3.3
SECTION 9 - Wastewater Sampling 9 . 1
9.1 Introduction 9. \
9.2 Site Selection 9.2
9 2 1 Influent ' ' \ " _ 9.2
922 Effluent ' 9.2
9.2 3 Pond and Lagoon Sampling 9-2
9.3 Sample Types 9.3
9 3 1 Grab Samples 9.3
932 Composite Samples 9.3
9.4 Use of Automatic Samplers .• 9.4
9 4 1 Introduction 9.4
EISOPQAM ToC - v May 1996
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942 Conventional Sampling (Inorganic Parameters) 9-5
943 Metals . . 9.5
944 Extractable Organic Compounds, Pesticides, and PCBs ... . . 9-5
945 Automatic Sampler Security 9-6
946 Automatic Sampler Maintenance, Calibration, and Quality Control . ... 9-6
9.5 Manual Sampling 9-6
9.6 Special Sample Collection Procedures 9-7
9.6.1 Organic Compounds and Metals 9.7
9.6 2 Bacteriological 9.7
9.6 3 Immiscible Liquids/Oil and Grease 9.7
964 Volatile Organic Compounds 9 . g
9.7 Special Process Control Samples and Tests 9-8
9.8 Supplementary Data Collection 9.9
9.9 References 9.10
SECTION 10 - Surface Water Sampling ... IQ.
10.1 Introduction 10-
10.2 Surface Water Sampling Equipment 10-
10 2 1 Dipping Using Sample Container 10-
1022 Scoops 10-
10 2 3 Peristaltic Pumps 10-
10.2 4 Discreet Depth Samplers 10-2
10.2 5 Bailers 10-2
10.2 6 Buckets 10-2
SECTION 11 - Sediment Sampling . 11_ !
11.1 Introduction l\- \
11.2 Sediment Sampling Equipment 11. 1
11.2 1 Scoops and Spoons .11-1
1122 Dredges . .... ' . 11-2
11.2.3 Coring H_2
SECTION 12 - Soil Sampling . . 12-]
12.1 Introduction . . . .12-1
12.2 Equipment 12. j
12.3 Sampling Methodology . 12-2
1231 Manual (Hand Operated) Collection Techniques and Equipment 12-2
12.3 2 Powered Sampling Devices 12-3
12.4 Special Techniques and Considerations 12-4
12.4 1 Collection of Soil Samples for Volatile Organic Compounds (VOC) Analysis 12-4
12 4.2 Dressing Soil Surfaces 12-4
1243 Sample Mixing 12_ 4
1244 Special Precautions for Trace Contaminant Soil Sampling 12-5
124.5 Specific Sampling Equipment Quality Assurance Techniques 12-5
EISOPQAM ToC - v, May 1996
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SECTION 13 - Waste Sampling 13-1
13.1 Introduction '3- '
13 1 1 Safety .... . . • 13' '
13 1 2 Quality Control Procedures . ... ... 13-1
1313 Collection of Auxiliary Information and Data 13-2
13.2 Waste Unit Types 13- 2
13.2 1 Open Units 13' 2
13.2 2 Closed Units 13' 3
13.3 Equipment • 13-4
1331 Waste Sampling Equipment 13-4
1332 Ancillary Equipment for Waste Sampling 13-4
Table 13.3.1 - Sampling Equipment for Various Waste Units 13-5
13.4 Waste Sampling Procedures 13-6
13 4 1 Waste Piles ... . 13-6
1342 Surface Impoundments 13-6
134.3 Drums 13-6
Figure 13-1 - Drum Data Form . . . . • • 13-8
134 4 Tanks . • • • • • 13-9
13.5 Miscellaneous Contaminated Materials .... . . 13-10
13.6 Waste Sample Handling Procedures 13-11
13.7 Particle Size Reduction 15-12
13.8 References 13-13
SECTION 14 - Ambient Air Monitoring - 14-1
14.1 Introduction 14-1
14 1 1 Formaldehyde Sampling Using Dinitrophenylhydrazine Cartridges Using
Method TO-11 . 14-1
1412 Volatile Organic Compounds (VOC) Sampling with SUMMA* Electropohshed
Stainless Steel Canisters Using Method TO-14 .14-3
14 1.3 Sampling for Semi-Volatile Organic Compounds (SVOC) Analysis with
High Volume PUF Samplers Using Methods TO-4 & TO-13 . . . . . 14-3
14 1 4 Collecting Samples for Metals Analysis Using the High Volume Sampler . 14- 6
1415 Sampling and Analysis of Mercury in Ambient Air Using Arizona Instrument"
Mercury Dosimeier Tubes and the Model 511 Gold Film Mercury Vapor Analyzer 14- 7
1416 Sampling for Dioxm and Dibenzofuran Analyses with High Volume
PUF Samplers Using Method TO-9 14-9
14.17 Mercury Sampling Using Gold-Coated Glass Bead Tubes 14-10
14.2 Criteria Pollutant Monitoring (Reference Monitors) for Air Pollutants
for which National Ambient Air Quality Standards have been established .... 14-12
14 2 1 Monitoring Ozone in Ambient Air 14-12
1422 Sampling of Paniculate Matter in Ambient Air as PM10 14-13
SECTION 15 - Field Physical Measurements . 15-1
15.1 Introduction 15-1
15.2 Horizontal Location Surveys 15-1
15 2 1 Introduction 15-1
15 2.2 Equipment Available 15-3
152.3 Specific Equipment Quality Control Procedures 15-3
CISOPQAM ToC - vii May 1996
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15 2 4 Procedures for Traversing 15-4
Figure 15 2.1 15-5
Figure 15.2.2 . . 15-5
Figure 15 2.3. . . . 15-6
Figure 15 2.4 .. . 15-8
15 2 5 Procedures for Differential GPS 15-8
Figure 15.2.5 15-9
15.3 Vertical Location (Elevation) Surveys 15-10
15 3 1 Introduction 15-10
15 3 2 Equipment Available 15-11
15 3 3 Specific Equipment Quality Control Procedures 15-11
1534 Procedures for Differential Leveling 15-11
Figure 15.3.1 15-12
15 3 5 Procedures for Trigonometric Leveling 15-13
Figure 153.2 ... 15-13
Figure 15.3.3 15-14
Figure 15.3 4 15-15
15.4 Bathymetry . . . 15-16
1541 Procedures .. . • 15-16
1542 Equipment Available . 15-16
154.3 Specific Equipment Quality Control Procedures . 15-16
15.5 Surface Water Stage/Tape Downs 15-17
15 5.1 Procedures .... 15-17
15.5.2 Equipment Available 15-17
15.5 3 Specific Equipment Quality Control Procedures 15-17
15.6 Time-of-Travel 15-19
15 6 1 Introduction 15-19
15 6 2 Procedures 15-19
1563 Equipment Available ... 15-21
15.7 Dilution Studies . 15-21
15 7 1 Procedures . - 15-21
15 7 2 Equipment Available 15-23
15 7.3 Specific Equipment Quality Control Procedures 15-23
15.8 Ground Water Level Measurements 15-24
15 8 1 General 15-24
1582 Specific Ground Water Level Measuring Techniques ... . 15-24
158.3 Total Well Depth Measurement Techniques . . ... 15-25
1584 Equipment Available 15-25
1585 Specific Quality Control Procedures 15-25
15.9 References 15-26
SECTION 16 - Field Measurable Physical/Chemical Characteristics 16-1
16.1 Introduction ... 16-1
16.2 Temperature 16-2
16.3 Specific Conductance (Conductivity) 16-3
16.4 Hydrogen Ion Concentration (pH) 16-4
16.5 Turbidity 16-6
16.6 Salinity 16-7
16.7 Dissolved Oxygen (DO) 16-8
EISOPQAM ToC - vin May 1996
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16.8 Total Residual Chlorine 16-10
16.9 Flash Point 16-13
16.10 Halogen Test . 16-15
16.11 References 16-16
SECTION 17 - Air Monitoring Safety Equipment Calibration Procedures 17-1
17.1 Introduction . 17. i
17.2 MSA Model 260 Combustible Gas and Oxygen Alarm 17-3
17.3 Photovac Microtip Photoionization Detector . 17-5
17.4 Toxic Vapor Analyzer (TVA 1000A) 17-11
17.5 Century Model OVA-128 Organic Vapor Analyzer 17-24
17.6 HNu Model PI 101 Photoionization Detector 17-26
17.7 Ludlum Model 3 Radiation Survey Meter 17-27
17.8 MiniRAE 17-28
SECTION 18 - Flow Measurement . 18-1
18.1 Introduction . . 18-1
18.2 Wastewater Flow Measurement 18-2
18 2 1 Introduction .18-2
18 2.2 Site Selection 18-2
18.2 3 Flow Measurement Systems 18-2
1824 Use of Existing Flow Measurement Systems 18-3
18.2 5 Specific Techniques 18-3
1826 Open Channel Flow Measurements 18-4
18.2 7 Closed Conduit Flow Measurements 18-6
18.3 Surface Water Flow Measurements .18-7
18.3 1 Introduction .18-7
1832 Techniques 18-7
18.4 General Quality Assurance Procedures 18-8
18.5 Equipment . . . . 18-8
18.6 Specific Equipment Quality Control Procedures . 18-9
18.7 References 18-11
APPENDIX A - Recommended Containers, Holding Times, & Preservation . . A - 1
APPENDIX B - Standard Field Cleaning Procedures B - 1
B.I Introduction B . j
B 1 1 Specifications for Cleaning Materials B - 1
B 1.2 Handling and Containers for Cleaning Solutions B-2
B 1.3 Disposal of Solvent Cleaning Solutions B-2
B 1 4 Equipment Contaminated with Concentrated Wastes B-2
B 1.5 Safety Procedures for Field Cleaning Operations B - 3
B 1 6 Handling of Cleaned Equipment B - 3
B.2 Field Equipment Cleaning Procedures B - 3
B.2.1 Specifications for Decontamination Pads B - 3
B 2 2 "Classic Parameter" Sampling Equipment B - 4
E1SOPQAM ToC - ix May 1996
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B2.3
B24
B25
B26
B27
B2.8
B.3
B.3 1
B3.2
B3.3
B34
B.4
Sampling Equipment used for the Collection of Trace Organic and
Inorganic Compounds
Well Sounders or Tapes
Fuliz* Pump Cleaning ...
Goulds* Pump Cleaning Procedure
Redi-Flo2* Pump . .
Automatic Sampler Tubing
Downhole Drilling Equioment
Introduction
Preliminary Cleaning and Inspection
Drill Rig Field Cleaning Procedure
Field Cleaning Procedure for Drilling Equipment
Emergency Disposal Sample Container Cleaning
APPENDIX C - Field Equipment Center Standard Cleaning Procedures
C.I
C.I.I
C.1.2
C 1 3
C 14
C 1 5
C 1 6
C.2
C2.1
C22
C2.3
C.3
C3 1
C.3. 2
C 3 3
C34
C3.5
C3.6
C37
C38
C3.9
C.4
C4.1
C4.2
C4.3
C4 4
C.5
C.5 1
C52
C5.3
C54
C5 5
C5.6
C57
Introduction
Specifications for Cleaning Materials
Handling and Containers for Cleaning Solutions
Disposal of Spent Cleaning Solutions ...
Safety Procedures for Cleaning Operations
Handling and Labeling of Cleaned Equipment . .
Initial Processing of Returned Equipment
Trace Organic and Inorganic Constituent Sampling Equipment
Teflon* and Glass
Stainless Steel or Steel
Reusable Composite Sample and Orgamc/Analyte Free Water Containers . .
Automatic Wastewater Sampling Equipment
ISCO" and other Automatic Samplers
ISCO1 1680, 2700. and 3700 Rotary Funnel, Distributor, and Metal Tube .
All Sampler Headers
Reusable Glass Composite Sample Containers
Plastic Reusable Composite Sample Containers (2700 - 5 gal., 3700 - 4 gal.)
ISCO' 1680 Glass Sequential Sample Bottles
ISCO' 1680. 2700, and 3700 Glass Sequential Bottles for GC/MS Analyses
Bottle Siphons for Composite Containers
Reusable Teflon" Composite Mixer Rods ...
Cleaning Procedures for Tubing
Silastic* Pump Tubing .
Teflon* Sample Tubing
Stainless Steel Tubing
Glass Tubing
Cleaning Procedures Tor Miscellaneous Equipment
Well Sounders and Tapes
Fuliz* Pump
Goulds* Pump
Redi-Flo2*
Little Beaver"
Drill Rig. Grout Mixer, and Associated Equipment
Miscellaneous Sampling and Flow Measuring Equipment
B-4
B-5
B-5
B-5
B-6
B-6
B-6
B-6
. B-7
B-7
B-8
B-8
C- 1
C- I
. ... C- 1
C-2
C-2
C-3
C-3
. C-4
C-4
. .C-4
. . . C-5
. . .C-5
C-5
C-5
.C-5
C-6
C-6
. . C-6
C-7
. C-7
C-7
. . C-7
. C-8
C-8
C-8
.. . . C-8
. . .C-9
. .C-9
. . . . C-9
C-9
. . . . C-10
C-10
C-ll
. . C-ll
C-12
EISOPQAM ToC - x May 1996
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C 5 8 Field Analytical Equipment C -12
C 5 9 Ice Chests and Shipping Containers C -12
C 5.10 Pressure Field Filtration Apparatus . . C -12
C 5 11 Orgamc/Analyte Free Water Storage Containers ... . . . C -13
C 5 12 Portable Solvent Rinse System . . C -14
C 5 13 Splash Suits C -14
C.5.14 SCBA Facemasks C -14
C5.15 Garden Hose C-14
C 5 16 Portable Tanks for Tap Water C -15
C517 Vehicles C-15
C.6 Preparation of Disposable Sample Containers C -15
C.6.1 Introduction .... C -15
C.6 2 Plastic Containers used for "Classical" Parameters C -15
C 6.3 Glass Bottles for Semi-Volatile GC/MS Analytes C -16
C 6 4 Glass Bottles for Volatile GC/MS and TOX Analyses C -16
C 6 5 Plastic Bottles for ICP Analytes C -17
APPENDIX D - Sample Shipping Procedures
D.I Introduction . . . D - 1
D.2 Shipment of Dangerous Goods D - 1
D.3 Shipment of Environmental Laboratory Samples D - 1
D.4 References .... . . ... D - 4
APPENDIX E - Pump Operating Procedures E - 1
E.I Peristaltic Pump .... . E - 1
E 1.1 introduction . . . . . E - 1
E 1 2 Purging with a Peristaltic Pump . . . E - 1
E 1 3 Sampling with a Peristaltic Pump ... . E - 2
E.2 Fultz* Pump E - 3
E 2 1 Introduction . E - 3
E.2 2 Operation E - 3
E 2 3 Tips and Precautions . E - 5
E 2 4 Rotor Replacement ... E - 5
E 2.5 Trouble Shooting . . . . . E - 6
E.3 Large Diameter Electric Submersible Pumps . . . E - 6
E 3 1 Introduction . E - 6
E 3.2 Safety ... . . . . . . E - 7
E 3 3 Pre-loadout Checkout Procedure . . E - 7
E.3 4 Operation . . E - 7
E 3 5 Maintenance and Precautions E - 8
E 3.6 Trouble Shooting . . . E - 8
E.4 QED" Bladder and Purge Pumps E - 9
E 4 1 Introduction E - 9
E 4 2 Operation - Bladder Pump E - 9
E 4.3 Operation - Purge Pump . E - 9
E 4 4 Trouble Shooting E -10
E.5 Small Diameter Electric Submersible Pumps . E -10
E 5 1 Introduction E -10
EISOPQAM ToC-xi May 1996
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E.5.2 Safety E-IO
E 5 3 Pre-loadout Checkout Procedures E -11
E 5 4 Operation .... . . . . . E -11
E 5 6 Maintenance and Precautions . . . . E -12
E57 Troubleshooting . . .... . E-12
APPENDIX F - Regional Technical Support for Criminal Investigations . F - 1
F.I Technical Assistance F - 1
F.2 Project Requests . . ... F - 2
F.3 Project Coordination . F - 2
F.4 Project Planning F - 2
F.5 Field Investigation . F - 3
F.6 Laboratory Support . F - 4
F.7 Final Report F - 4
F.8 Document Control .... F - 4
F.9 Sample Disposal ... F - 5
APPENDIX G - Battery Charging and Storage Operations . . G - I
G.I Receiving Batteries from the Field . G-l
G.2 Charging Batteries . . . . G - 2
G.3 Post-Charging G - 3
G .4 Maintenance ... . G - 4
Figure G.I - Battery Log G - 6
Figure G.2 - Battery Building Maintenance Report . G - 7
EISOPQAM ToC - xii May 1996
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SECTION 1
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SECTION 1
PREFACE
1.1 Introduction
This document, the Environmental Investigations Standard Operating Procedures and Quality
Assurance Manual, contains the standard operating and field quality assurance procedures used by
Region 4 field investigators The manual originated in 1980 with the title Engineering Support Branch
Standard Operating Procedures and Quality Assurance Manual and was revised in 1986 with the same
title and revised again in 1991 with the title, Environmental Compliance Branch Standard Operating
Procedures and Quality Assurance Manual The specific procedures outlined in the manual are based
on the experiences of Region 4 field investigators or are specifically referenced at the end of each
section
This manual will be provided to each Region 4 employee responsible for conducting field
investigations for activities contained in these Standard Operating Procedures (SOP). Each employee is
expected to read and be familiar with each section of the SOP. This is intended to be a dynamic
document and will be revised periodically as needed. Mention of trade names or commercial products
does not constitute endorsement or recommendation for use.
1.2 Performance Objectives
Performance objectives have been included at the beginning of sections and sub-sections where
applicable The performance objective lists the minimum requirements necessary for meeting the mtem
of the procedures that follow in the section The purpose of the performance objective is to allow
flexibility within field procedures where appropriate, however any deviations from the procedures m
the SOP should be approved by the appropriate authority and thoroughly documented.
1.3 Section Objectives
Section objectives are included at the beginning of sections where performance objectives are
not applicable. Section objectives provide a brief summary of the intention and content of the section
EISOPQAM 1-1 May 1996
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SECTION 2
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SECTION 2
INVESTIGATIONS, INSPECTIONS, AND OVERVIEW ACTIVITIES
SECTION OBJECTIVES:
• Define the standard types of investigations, inspections, and field studies conducted.
• Outline the general requirements for study plans, and reports for standard types of
investigations, inspections and field studies.
• List available agency guidance and special requirements for the standard types of
investigations, inspections, and field studies.
2.1 Introduction
The investigations, inspections, and overview activities conducted can be broadly categorized as
either enforcement or non-enforcement related activities
The enforcement related activities include Resource Conservation and Recovery Act (RCRA) case
development inspections, RCRA comprehensive ground water monitoring evaluations, water enforcement
case preparation studies. National Pollutant Discharge Elimination System (NPDES) compliance
monitoring, diagnostic evaluations of municipal wastewater treatment plants, investigations of Superfiind
hazardous waste sites, contractor overviews, investigations and monitoring of oil spills and Superfund
spills, and investigations of toxic episodes and spills.
Non-enforcement activities include investigations of potential Superfund hazardous waste sites for
National Priority Listing (NPL) purposes, technical assistance studies at municipal wastewater treatment
plants, studies involving water quality and permitting issues, studies and inspections of abandoned
hazardous waste sites, air quality studies, and a broad range of studies for national programs, as well as
technical assistance studies for state and local agencies. However, the studies and data derived from non-
enforcement type investigations could be used for enforcement purposes. Field investigations include all
environmental media, i.e . surface and ground water, air, soils, sediments, and wastes.
E1SOPQAM 2-1 May 1996
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2.2 Potable Water Supply Investigations
Special procedures apply when a sample is collected from a private or public potable water supply
Investigators should always obtain the following information from the residents and/or owners in the eveni
contaminants are detected in the sample
• resident's and/or owner's name,
• resident's and/or owner's mailing address; and
• resident's and/or owner's home and work telephone numbers.
Immediately upon receipt, the project leader should carefully examine the resulting data. Any
exceedences of the primary or secondary drinking water standards, or the detection of any priority
pollutants, RCRA 40 CFR 261 Appendix VIII compounds, or the Comprehensive Environmental Response,
Compensation, and Liability Act (CERCLA) 40 CFR 302 list of hazardous substances shall result in the
project leader immediately providing the appropriate officials in the Water Management Division with the
following information:
• the analytical data;
• the name, address (including zip code) and telephone numbers of the residents and/or owners.
• the site name and location, and
• the EPA site identification number (if applicable).
Investigators should not release potable water supply data to anyone before providing u to the
Water Management Division.
EISOPQAM 2-2 May 1996
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2.3 Civil Enforcement Investigations and Studies
23.1 Introduction
This SOP covers the field and operational aspects of conducting field investigations, however, it
is beyond the scope of this manual to cover all aspects of enforcement activities. Each enforcement
investigation must be tailored to meet the needs of the anticipated enforcement action. The lead attorney
and compliance specialists should be consulted on a continuing basis during the planning, conduct, and
report writing phases of enforcement investigations.
Civil investigations are conducted for the Water and Waste Management Divisions and the Air,
Pesticides, and Toxics Management Division to determine if a facility, site, or project is meeting the terms
of a Consent Decree, order, water permit, etc. These investigations are conducted under a number of
environmental laws which include
• The Clean Water Act (CWA, PL 92-500)
• The Resource Conservation and Recovery Act (RCRA, PL 94-580)
• The Hazardous and Solid Waste Amendments (HSWA) of 1984
• The Comprehensive Environmental Response, Compensation, and Liability Act (Superfund)
• The Superfund Amendments and Reauthorization Act (SARA) of 1986
• The Clean Air Act (CAA 42 U. S.C. 1857 - 1857L, as amended)
• The Toxic Substances Control Act (TSCA, PL 94-469)
232 Facility Entry
Authority ~ Various federal environmental statutes grant EPA enforcement personnel authority to enter
and inspect facilities. The authority granted in each statute is similar to that stated below in Section 308
of the Clean Water Act.
• "(a)(B) the Administrator or his authorized representative, upon presentation of his credentials
(0 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 required . , and sample any effluents which the owner or operator of
such source is required to sample. . ."
For the specific requirements for conducting inspections and collecting data pursuant to a particular
Act. see Section 308 of the Clean Water Act, Section 9 of the Federal Insecticide, Fungicide, and
Rodenticide Act, Section 3007 of the Resource Conservation and Recovery Act; Section 8 of the Toxic
Substances Control Act, Section 1445 of the Safe Drinking Water Act; Section 104 of the Comprehensive
Environmental Response. Compensation, and Liability Act (Superfund); and Titles I, III, and IV of the
Clean Air Act.
EISOPQAM 2-3 May 1996
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2.3 4 Unreasonable Search and Seizure
EPA authority under the various Acts is subject to the "unreasonable search and seizure" provisions
of the Fourth Amendment to the Constitution The prohibition is not against all searches and seizures, but
only those which are unreasonable or which valid consent, if required, has not been given Consent, in
this context, means the intentional foregoing of right to privacy which is not the result of either fear,
ignorance, or trickery.
To comply with the Acts and avoid any "unreasonable search" or procedural problems, a facility
should be entered in the following manner
1. The facility premises should be entered through the main gate or through the entrance
designated by the source if in response to an inspection notification letter (a 308 letter for
example)
2 The employee shall introduce herself/himself in a dignified, courteous manner to a responsible
plant official. A responsible plant official may be the owner, operator, officer, or agent in
charge of the facility, including the plant environmental engineer. Identification credentials
shall always be presented
3 If only a guard is present at the entrance, employees shall present their credentials and suggest
that the guard call their superior on the telephone. If the field investigators know the name of
the responsible official they are to see, field investigators shall request the guard to call this
individual directly
4. If the company provides a general sign-in sheet, it is acceptable to sign it. Field investigators
shall not sign a release of liability (waiver) when entering a facility under the authority of
Federal law
5. If entry is refused, field investigators shall not contest the issue with the facility representative.
but will immediately do the following-
• Obtain the name and position of the individual denying entry to the facility, and record
the date and time
• Cue the appropriate EPA authority to conduct the inspection, ask if the individual
denying entry heard and understood the reason for your presence and record the
answer and any reasons given for denial of entry.
• Leave the premises immediately
After leaving the facility, the field investigators shall, at the earliest possible time, inform their
immediate supervisor and the Office of Regional Counsel, by telephone of the events which took place and
seek guidance on how to proceed
EISOPQAM 2-4 May 1996
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2.3 5 Requesting Information
The various laws and statutes under which EPA operates address the protection of trade secrets and
confidential information. As a general policy, field investigators should not accept confidential information
unless it is necessary for carrying out Agency functions under a particular Act. As a matter of practice,
requests for confidential information can only be signed by an Agency employee who has had the
appropriate Confidential Business Information (CBI) training and certification
In compliance with EPA regulations, an EPA request for company information, pursuant to
statutory authority, will contain a statement allowing the facility to designate all or part of the information
requested by the Agency as confidential by marking it according to: Code of Federal Regulations. Title
40. Part 2, Section 203.41; or Federal Register, 41 FR 36902. In addition to citing the appropriate
regulations, the request for confidential information will state that:
1 The company may, if it desires, assert a business confidentiality claim covering part or all of
the information in the manner described by [the applicable regulation], and that information
covered by such a claim will be disclosed by EPA only to the extent, and by means of the
procedures, set forth in [the applicable regulations]; and that
2 If no such claim accompanies the information when it is received by EPA, it may be made
available to the public by EPA without further notice to the company.
If the collection of confidential information is required to carry out the responsibility of the Branch,
personnel should consult carefully with the appropriate operating Division staff and the Office of Regional
Counsel attorneys In general, when such information is needed by Branch personnel, the request should
state that this information will be transmitted directly to the Office of Regional Counsel
In general. Branch personnel shall not accept confidential information when conducting a plant
evaluation, inspection, or reconnaissance When Branch personnel must collect or observe confidential
information, a separate logbook shall be maintained When confidential information is entered into an
inspector's logbook, the entire logbook and each page containing confidential information shall be marked
"CONFIDENTIALITY CLAIM " Upon returning to the EPA Region 4, facility, all such information shall
be maintained in a locked filing cabinet and the Office of Regional Counsel shall be notified for ultimate
disposition of the material.
All field investigators conducting investigations or inspections should be familiar with the
inspection provisions of these acts, i.e , CWA (Section 308), RCRA (Section 3007), CERCLA (Section
104). and TSCA (Section 11).
235 Photographs
At no time should field investigators be denied the opportunity to take photographs during an
investigation If photographs are denied and no other means can be arranged to get the photographs, this
is considered a denial of access on the pan of the facility. At some facilities the process operations and/or
equipment may be claimed as being proprietary In these cases, the facility may make a CBI request to
the Office of Regional Council (ORC) Generally, providing the facility with a duplicate copy of uncut
prints for their review is acceptable to both parties. If this is unacceptable to the facility, the investigator
may allow the facility to take the photographs, review them, and provide copies to EPA.
EISOPQAM 2-5 May 1996
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2 3.6 Split Samples
The inspection provisions of RCRA (Section 3007) and CERCLA (Section 104) require that. "If
the officer or employee 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." As a matter of policy, an offer will be
made to the owner, operator, or agent in charge to split all samples collected on facility property
2.4 Criminal Investigations and Studies
At the request of the Criminal Investigations Division (CID) and with the concurrence of the
Regional Administrator/Deputy Regional Administrator, technical support for criminal investigations is
provided Only experienced personnel with adequate training (such as on-site supervision by senior
investigators or the Criminal Investigations Course offered by the Federal Law Enforcement Training
Center) should be project leaders during such investigations. Technical support shall be provided at the
request of the CID Special Agent-m-Charge of the investigation in accordance with Appendix F of this
SOP
EISOPQAM 2-6 May 1996
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2.5 Clean Water Act Compliance Monitoring Inspections
2 5 1 Introduction
The term "compliance monitoring" covers all activities undertaken to ascertain a permitee's or
discharger's compliance status. This includes, but is not limited to, Clean Water Act (CWA) compliance
monitoring inspections and compliance review, e.g., the review of Discharge Monitoring Reports (DMR)
or compliance schedule reports The mam functions of CWA compliance monitoring inspections are to
verify the integrity of the self-monitoring information and to develop the basis for possible follow-up
compliance or enforcement actions. All compliance monitoring inspections shall be conducted as though
an enforcement action would result General guidance for conducting compliance monitoring inspections
is found in the US EPA, NPDES Compliance Inspection Manual (1).
A number of different types of compliance monitoring inspections have been defined including
compliance evaluation inspections (CEI), compliance sampling inspections (CSI), toxic compliance
sampling inspections (XSI), compliance biomonitoring inspections (CBI), performance audit inspections
(PAI), diagnostic evaluations (DE), reconnaissance inspections (RI), pretreatment compliance inspections
(PCI), sludge inspections (SI), legal support inspections (LSI), and Municipal Wastewater Treatment Plant
technical assistance (TA) studies
Activities associated with a visit to any facility for a compliance inspection shall not be double
counted Thus, a single visit cannot be counted as both a CSI and a CEI; it must be reported as one or the
other However, a single visit that encompasses separate activities (e.g., a PAI or legal support
investigation) will be reported and counted as two separate activities. A compliance monitoring inspection
(all types) is not considered complete until the appropriate portions of the Compliance Inspection Report
Form (EPA Form 3560-3) have been completed and the information from the coding section entered into
the permit compliance system (PCS)
Inspection Notification
Generally, CSIs and CEIs are conducted unannounced unless there is some reason to conduct the
inspection on an announced basis Routine PAI's and DE's are typically announced inspections due to the
complexity of the logistics involved in these types of investigations.
The various types of compliance monitoring inspections are defined in the next section; references
are given to available specific agency guidance for each type of inspection.
252 CWA Inspection Types
Compliance Evaluation Inspection (CEI)
The CEI is a nonsampling inspection designed to verify permittee compliance with applicable
permit self-monitoring requirements, effluent limits, and compliance schedules This inspection involves
records reviews, visual observations, and evaluations of the treatment facilities, laboratories, effluents,
receiving water, etc The CEI examines both chemical and biological self-monitoring and forms the basis
for all other inspection types except the Reconnaissance Inspection. Guidance for conducting CEIs is given
in the NPDES Compliance Evaluation Inspection Manual (2).
EISOPQAM 2-7 May 1996
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Compliance Sampling Inspections (CS11
CSI's are conducted where representative sample(s) of a permittee's influent and/or effluent are
collected and analyzed 1) to verify the accuracy of the permittee's discharge monitoring reports, 2) to
determine the quantity and quality of the effluent, 3) to develop permits, and/or 4) where appropriate, as
evidence for enforcement proceedings This activity also includes the same objectives listed for CEI's, and
where appropriate, may serve to gather detailed information for the possible institution of legal acnon
against the permittee. Guidance for conducting CSI's is given in the NPDES Compliance Sampling
Inspection Manual (3).
Toxic Sampling Inspections (XSI1
The XSI has the same objectives as a conventional CSI. However, it places increased emphasis
on toxic substances regulated by the NPDES permit. The XSI covers priority pollutants other than heavy
metals, phenols, and cyanide, which are typically included in a CSI (if regulated by the NPDES permit)
An XSI uses more resources than a CSI because highly sophisticated techniques are required to sample and
analyze toxic pollutants. An XSI may also evaluate raw materials, process operations, and treatment
facilities to identify toxic substances requiring controls.
Compliance Biomonitormg Inspection (CEI)
A CBI is an inspection utilizing a static or flow-through bioassay, in lieu of, or in addition to, the
collection of samples. The objectives of this inspection are to:
• Identify those permittees which may be meeting the minimum technology based requirements
of the CWA, but whose level of treatment is not sufficient 10 ensure the biological integrity of
the receiving waters,
• Identify those permittees which may have potential toxicants in their discharge(s) that have not
been identified or included in their NPDES permit, and
• Evaluate compliance with acute or chronic toxicity permit limit requirements.
In those instances where biomomtoring reveals the presence of toxic substances not addressed in
the issued permit, the permittee may be required through the 308 process to chemically and/or physically
characterize the composition of the discharge to identify and quantify the toxic substance or substances
(CWA Section 308) Guidance for conducting these inspections is given in the Compliance Bio-Monitoring
Inspection Manual (4).
Performance Audit Inspection (PA1>
The PAI is used to evaluate the permittee's self-monitoring program. As with a CEI, the PAI is
used to verify the permittee's reported data and compliance through a records check However, the PAI
provides a more resource-intensive review of the permittee's self-monitoring program and evaluates the
permittee's procedures for sample collection, flow measurement, chain-of-custody. laboratory analyses,
data compilation, reporting, and other areas related to the self-monitoring program During a CEI, the
inspector makes a cursory visual observation of the treatment facility, laboratory, effluents, and receiving
waters During a PAI. the inspector actually observes the permittee performing the seli-monitoring process
from sample collection and flow measurement through laboratory analyses, data workup, and reporting.
The PAI does not include the collection of samples by the inspector. However, the inspector may require
the permittee to analyze performance samples for laboratory evaluation purposes.
EISOPQAM 2-8 May 1996
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Diagnostic Evaluations (DE)
The DE is a detailed performance evaluation that focuses primarily on municipal Publicly Owned
Treatment Works (POTWs) which are not in compliance with permit requirements. The DE is designed
to evaluate the POTW's design, operations, and influent/effluent wastewater characteristics and to provide
a comprehensive evaluation of the reasons why the facility is not meeting permit limits The final product
consists of a formal report with data, data interpretation, and recommendations suitable for use in technical
assistance, negotiations, and enforcement actions.
Reconnaissance Inspection (RI)
The RI is used to obtain a preliminary overview of a permittee's compliance program The
inspector performs a brief visual inspection of the permittee's treatment facility, effluent, and receiving
waters The RI is intended to obtain a broad coverage of permittees of unknown status with a minimum
amount of resources.
Pretreatment Compliance Inspection (PCD
The PCI evaluates the POTWs implementation of its approved pretreatment program. It includes
a review of the POTWs records on monitoring, inspections, and enforcement activities for its industrial
users The PCI is usually conducted concurrently with another NPDES inspection of the POTW
Sludge Inspection (SI)
The SI is primarily conducted at POTWs Waste sludge generation and disposal practices are
evaluated under the 40 CFR 503 regulations. The SI includes a review of the sludge monitoring records.
sludge handling facilities, and sludge disposal practices.
Legal Support Inspection (LSI)
The LSI is an inspection conducted to satisfy a specific enforcement related problem An example
of this type of inspection may be an enforcement request to inspect a permittee to see if it is appropriate
to terminate a specific enforcement order or a request to gather data to support a planned action
Municipal Wastewater Treatment Plant Technical Assistance (TA) Studies
The TA program is designed to assist federal, state, and local agencies, and industries with
technical issues associated with wastewater treatment problems. The TA includes analysis of the various
technical problems, training in direct support of the program, and advice on the solutions to the problems.
EISOPQAM 2-9 May 1996
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2.5.3 Study Plans
Routine NPDES inspections (e g., PAIs, CSIs, etc.) do not require a written study plan Detailed
investigations, such as diagnostic evaluations, water quality studies, and other large scaled technical
evaluations will require a written study plan which should include the following minimal information
• Introduction - The name and location of the project, study dates, requestor, reason for request
(e.g., NPDES compliance problems), project leader, and a list of EPA and other appropriate
study contacts and telephone numbers
• Study Objectives - A detailed description of the primary objectives of the project
• Sampling Schedule - A detailed table showing all projected sampling stations, sampling
parameters, and the total number of samples to be analyzed
The study plan may include more detailed information depending on the nature and complexity of
the project Copies of the study plan should be given to the appropriate personnel.
2.5.4 NPDES Compliance Inspection Reports
The results of all compliance inspections shall be reported utilizing the NPDES Compliance
Inspection Report Form (EPA Form 3560-3) The completed form, formal narrative report, and transmittal
memorandum constitute a compliance inspection report for all routine compliance inspections conducted
by Branch personnel
The completed inspection reports are forwarded to all appropriate panics as previously agreed for
action and follow-up. The state and regional program office are kept fully informed via copies of all
correspondence. In cases where EPA is involved in litigation with a permittee, no reports will be sent to
the permittee without special permission from legal counsel
Completion of NPDES Compliance Inspection Report Form (EPA Form
General instructions for completing EPA Form 3560-3 are printed on the back of the form
The forms shall be signed by the investigator and dated on the day that the form is completed (not
the inspection date) The name of the state inspector should be included for joint inspections All routine
compliance inspections forms shall be reviewed by the supervisor, who will sign and date the 3560-3 form
in the "Reviewed By" section
EISOPQAM 2 - 10 May 1996
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2.6 Superfund Investigations, Technical Assistance, and Overview Activities
2 6 1 Introduction
Superfund field activities include remedial investigations and feasibility studies (RI/FS), field
investigations of potentially or known contaminated areas (FI), technical assistance (TA), and on-site
overviews (OV) of Superfund contractor, potentially responsible party (PRP) contractor, and state
personnel.
262 Superfund Investigation Types
Remedial Investigations/Feasibility Studies (RI/FS)
Remedial investigations are conducted to determine the nature and extent of contamination at
specific Superfund sites Investigations may include installation of temporary or permanent monitoring
wells, geophysical exploration, surface and subsurface soil sampling, off-site environmental sampling, etc
Feasibility studies may be conducted concurrently with an RI to develop and evaluate potential remedial
action alternatives The Guidance for Conducting Remedial Investigations and Feasibility Studies under
CERCLA (5) is useful for planning RI/FS investigations.
Field Investigations (FI)
These include all field investigations, other than RIs, of potentially or known contaminated areas,
and they support all phases of the Superfund program. These investigations may include sampling of
ground water, surface and subsurface soils, rivers, lakes, etc., and/or may entail geophysical studies,
global positioning system (GPS) activities, etc
Overviews (OV)
Activities include on-site overview of the field work of EPA Superfund field contractors, PRP
contractors, and State Superfund contractors Overviews are conducted to evaluate the contractors'
capabilities and to correct deficiencies in performing Superfund field investigations. The Region 4,
Hazardous Waste Field Overview Checklist (Exhibit 2.1) is completed during the overview, and a written
report presenting the overview findings is completed and transmitted to the appropriate official in the Waste
Management Division
Technical Assistance (TA>
Activities range from directing field investigations with non-Agency field support to responding
to telephone questions concerning all aspects of Superfund field investigations. In addition, field personnel
provide a vaner>' of training and technical assistance activities for Regional, State, and other Federal
agency personnel in methods of conducting field operations at hazardous waste sites.
263 Planning for Field Investigative Support
Periodic meetings are typically held between a representative(s) of the Superfund Team and the
Waste Management Division staff to discuss proposed initiatives and specific investigation needs These
meetings are usually conducted in October for yearly planning, and more frequently for quarterly planning
EISOPQAM 2-11 May 1996
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Based on the priorities agreed upon by the Superfund Team, the Superfund Coach, and the Waste
Management Division, field investigation schedules are prepared by the Superfund Team and updated as
needed
264 Requests for Superfund Studies
Superfund investigations are prioritized by (he Waste Management Division based on the need for
field investigative support Specific investigations are usually requested by project managers of the various
Superfund programs, however, they may be requested by state agencies, congressional officials, etc
Routine requests for field investigative support are coordinated with the Superfund Team leader and
Superfund Coach Requests are then brought to the Superfund Team for scheduling and project leader/staff
assignment Although the initial contact may be by telephone or electronic mail, a formal request
memorandum with a request form is required prior to commencement of the investigation
2 6.5 Investigation Study Plans
Study plans are prepared for all Superfund investigations except overviews and some emergency
investigations Study plans for typical Superfund field investigations must be issued at least one week prior
to the investigation The timing and nature of some emergency requests may preclude the issuance of a
study plan
A copy of the study plan in draft form will be provided to the requestor to insure that the plan will
meet their objectives. As a general rule, the Data Quality Objective (DQO) process should be consulted
during the study plan preparation phase. The study plan should include, as appropriate:
• Introduction - The project leader and support staff, requestor from the appropriate Superfund
Branch, and the objective(s) of the investigation
• Background - Facility compliance history, manufacturing processes, types of wastes produced,
waste treatment methods, etc
• Scope -- The study design should be discussed in this section including the number and location
of the samples to be collected, information which will be obtained, and records to be reviewed
• Logistics -- The travel and study dates.
• Methodology - Analyses to be conducted and who will conduct analyses, field and laboratory
SOP references, and when samples will be received by the laboratory.
If the study is an RI, the following additional information, where appropriate, should be included.
• Site background and physical setting
• Initial Evaluation
• Sampling DQO
• Site Management Plan
• Quality Assurance Project Plan
• Field Sampling and Analyses Plan
• Field Health & Safety Plan.
E1SOPQAM 2 - 12 May 19%
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266 Investigation Reports
Reports will be completed after each investigation and will contain the following, as appropriate
• Introduction - When the investigation was conducted; EPA, state, or other regulatory agency
participation; facility representatives and what their participation included; who requested the
investigation; and the objectives
• Background - Study area descriptions, manufacturing process and waste handling priorities,
results of previous investigations, etc A site map depicting major structures and facilities, as
well as sampling locations will be included.
• Summary -- A brief summary of the key results and conclusions of the study.
• Discussion - All aspects pertinent to the investigation, such as analytical results; deficiencies,
site hydrology, an evaluation of the monitoring well system; a site map showing monitoring
well locations, topography, and ground water flow direction; well depths, and ground water
elevations.
• Methodology - A statement indicating that this SOP was followed and/or reasons why not and
whether or not samples were split and with whom.
• Conclusions - At the discretion of the author, a conclusions section for complex investigations
• Reference and Appendices - Laboratory data sheets, checklists, etc.
If the study is an RI. the following additional information should also be included where
appropriate.
• Site information, including site description, site history, previous investigation results.
regulatory actions, demography, and surrounding land use.
• Sampling strategy
• Nature and extent of contamination
• Contaminant fate and transport
In emergencies, samples are usually collected quickly and analyzed on a fast turn-around basis.
In these cases. Team personnel may provide printed copies of sample data to the requestor as soon as
practical Where appropriate, a letter report detailing the field activities associated with the emergency
field investigation will be prepared and transmitted to the requestor.
Internal Peer Review and Report Recipients
All Superfund reports will be reviewed internally. Final copies of the report will be sent to the
requestor If facility or state personnel request a copy of the report, this will be indicated in the report
transmittal memo. The Regional Superfund program is responsible for distribution of data and reports to
site owners or operators and to the public All requests for such information should be referred to the
proper program official for action
EISOPQAM 2 - 13 May 1996
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2.7 RCRA Inspections, Investigations, and Overview Activities
2.7 1 Introduction
RCRA field activities include comprehensive ground water monitoring evaluations (CME), RCRA
facility assessments (RFAs), case development inspection/evaluations (CDIE) for both the RCRA program
and the Criminal Investigations Division (CID), and on-site field overviews (OV) of state. RCRA
contractor, and federal facility personnel
2 7.2 RCRA Investigation Types
Comprehensive Ground Water Monitoring Evaluation (CME)
The CME is an overall review of a facility's compliance with all applicable RCRA requirements
to determine adequacy of the ground water monitoring system. It includes an on-site examination of
records and other documents and an evaluation of the facility's compliance with applicable RCRA re-
quirements. Also evaluated is the effectiveness of the ground water monitoring system and the facility's
hydrogeological conditions Sampling and analysis of the ground water are usually conducted Guidance
for conducting CMEs is included in the RCRA Ground-Water Monitoring Technical Enforcement Guidance
Document (OSWER 9950.1) (6).
RCRA Facility Assessment (RFA)
The RFA is an agency lead activity which is the first step in a corrective action program The
purpose of the RFA is to identify known and/or probable releases of hazardous wastes or other constituents
at solid waste management units (SWMUs) and at previously unaddressed regulated units It includes a
"desk-top" review of information submitted by the owner/operator to EPA and State Agencies The RFA
also consists of an on-site visit, and potentially a subsequent sampling investigation to determine whether
or not releases of hazardous wastes or constituents have occurred. Guidance for conducting the RFA is
'n the Draft RCRA Preliminary Assessment/Site Investigation Guidance (7).
Case Development Investigation/Evaluation (CDIE)
These include all RCRA field investigations other than CME's and RFA's, including field sampling
investigations, closure/post closure investigations, environmental investigations, trial burns, etc The type
of investigation dictates the specific field methodology The CDIE is conducted to gather information on
the composition/characteristics of wastes and/or an area impacted by the operation of a RCRA facility
The CDIE may also include verification of a sampling and analysis plan, collection of information on
facility design and operation, verification of manifest descriptions, or other unanticipated needs or requests
necessary for case development
Overviews (OV)
Overviews of state RCRA compliance inspections or RCRA contractor inspections are conducted
to evaluate their capability to conduct RCRA field investigations The Region 4, Hazardous Waste Field
Overview Checklist (Exhibit 2.1) is completed during the overview, and a written report presenting the
overview findings is completed and transmitted to the appropriate EPA regional RCRA official
EISOPQAM 2 - 14 May 1996
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2 7.3 Planning for Field Investigative Support
Periodic meetings are typically held between a representative(s) of the RCRA Team and the RCRA
Branch staff to discuss proposed initiatives and specific investigation needs. These meetings are usually
conducted in October for yearly planning, and more frequently for quarterly planning.
Based on the priorities agreed upon by the RCRA Team, the RCRA Coach, and the RCRA Branch,
a tentative field investigations schedule is prepared by the RCRA Team and updated as needed An
updated schedule is provided to the RCRA Branch each month through the RCRA Team leader.
274 Requests for RCRA Studies
RCRA investigations are prioritized by the Region 4, RCRA program based on their need for field
investigative support. Requests for field investigative support are coordinated with the RCRA Team Coach
or their designee(s) A memorandum with a request form is required prior to commencement of the
investigation.
2 7.5 Investigation Study Plans
Study plans are prepared for all RCRA investigations and issued at least one week prior to the
investigation A copy of the draft study plan should be provided to the RCRA program requestor to insure
that the investigation will meet their enforcement or permitting objectives. As a general rule, the Data
Quality Objective (DQO) process should be consulted during the study plan preparation phase. The study
plan should include, as appropriate
• Introduction - The project leader and support staff, requestor from the RCRA program, and
the objective(s) of the investigation
• Background - Facility compliance history, manufacturing processes, types of wastes produced,
waste treatment methods, etc.
• Scope -- A discussion of the study design including the number and locations of the samples
to be collected. Information which will be obtained and records to be reviewed.
• Logistics - The travel and study dates
• Methodology - Analyses to be conducted and who will conduct analyses, field and laboratory
SOP references, and when samples will be received by the laboratory.
EISOPQAM 2 -15 May 1996
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276 Investigation Reports
Reports will be completed after each investigation and will contain the following, as appropriate
• Introduction - When the investigation was conducted; EPA, state, or other regulatory agency
participation, facility representatives and what their participation included; who requested the
investigation; and the objectives.
• Background -- Study area descriptions, manufacturing process and waste handling priorities,
results of previous investigations, etc. A site map depicting major structures and facilities, as
well as sampling locations will be included for all CMEs and CDIEs.
• Summary - A brief summary of the key results and conclusions of the study.
• Discussiqn - All aspects pertinent to the investigation e.g., analytical results, RCRA
deficiencies, etc
• Methodology - What information was obtained and from whom, what samples were collected.
whether or not photographs were taken, etc. A statement indicating that this SOP was
followed and/or reasons for deviations and whether or not samples were split and with whom
• Conclusions -- At the discretion of the investigator, a conclusions section for complex
investigations.
• Reference and Appendices -- Raw data, checklists, etc
If the study was a CME. the following information should be included where appropriate
• A discussion of site hydrology
• An evaluation of the monitoring well system
• An evaluation of the assessment plan
• A site map showing monitoring well locations, SWMU's, topography, ground water flow
direction, etc
• Well depth, ground water elevations
• CME checklist
Internal Peer Review and Report Recipients
All RCRA reports will be reviewed internally Final copies of the report will be sent to the
requestor. If facility or state personnel request a copy of the report, this will be indicated in the report
transmittal memorandum.
EISOPQAM 2 - 16 May 1996
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2.8 Underground Storage Tank (UST) Investigations
2 8 1 Introduction
Laws protecting private and public water supplies from contamination by petroleum products due
to leaking underground storage tanks were finalized on September 23, 1988 (40 CFR, Parts 280-281)
Field investigations of potentially contaminated sites are requested by the Water Management Division and
involve comprehensive ground water sampling and site inspections.
UST inspection objectives are as follows:
• Conduct sampling for metals and volatile and extractable organic compounds analyses at
potable and groundwater monitoring wells located in the investigation area
• Determine whether the potable wells are contaminated with petroleum products.
• Determine the direction of the contamination plume and the source of the contamination
282 Investigation Reports
An investigation report containing the following information will be completed:
• Introduction ~ When and where the investigation was conducted; investigation team members
and telephone numbers, potable well owners addresses and telephone numbers; and requesting
office.
• Background -- Site history, description, and results of previous studies
• Summary ~ Summary of analytical results, whether petroleum pollutants are present, direction
of plume movement if determined, and possible sources of contamination.
• Sketches/maps - Showing potable well locations.
Internal Peer Review and Report Recipients
All UST reports will be reviewed internally Final copies of the report will be sent to the
appropriate Water Management Division official. If private or public potable water supplies are sampled,
see Section 2.2 for reporting requirements
E1SOPQAM 2-17 May 1996
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2.9 Underground Injection Control (UIC) Investigations
2 9 1 Introduction
Laws protecting the ground water from contamination by the injection of wastes allow for the
sampling of injection wells as well as other nearby wells. Field investigations of potentially contaminated
sues are requested primarily by the Region 4, Underground Injection Control Unit and involve
comprehensive ground water sampling and site inspections.
UIC inspection objectives are as follows.
• Conduct sampling for specified parameters, metals, and volatile and extractable organic
compound analyses at injection, potable, and ground water monitoring wells located in the
vicinity of the investigation area
• Determine whether the potable water wells in the vicinity are being contaminated with waste
products from the injection wells
• If requested, determine the direction of the contamination plume and the source of the
contamination
292 Investigation Reports
An investigation report containing the following information will be completed.
• Introduction - When and where the investigation was conducted; investigation team members
and telephone numbers; potable water well owners addresses and telephone numbers; and
requesting office.
• Background - Site history, description, and results of previous studies.
• Summary -- Summary of analytical results, whether pollutants are present, direction of plume
movement, and possible sources of the contamination.
• Sketches/maps ~ Showing potable well locations
Internal Peer Review and Report Recipients
All UIC reports will be reviewed internally. Final copies of the report will be sent to the
appropriate Water Management Division official If private or public potable water supplies are sampled.
see Section 2 2 for reporting requirements
EISOPQAM 2 - 18 May 1996
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2.10 Ambient Air Monitoring Evaluations And Audits
2 10.1 Introduction
In 1979, the US EPA established a plan for obtaining reliable ambient air quality data The plan
includes a network of State and Local Air Monitoring Stations (SLAMS). The regulations governing the
network (40 CFR 58) cover the data collection and reporting requirements for state and local air pollution
control agencies. The purpose of this section is to provide procedures for the inspection and evaluation
of the SLAMS network Each SLAMS site must meet criteria for network design, instrument exposure,
sample inlet, etc.
2 10.2 NAMS/SLAMS Site Evaluations
State and Local Air Monitoring Stations (SLAMS)
A SLAMS network should be designed to meet a minimum of four basic monitoring objectives
Each SLAM site within a network must meet at least one of the following objectives:
• To determine the highest concentrations expected to occur in the area covered by the network
• To determine representative concentrations in areas of high population density
• To determine the impact of ambient pollution levels of significant sources or source categories.
• To determine the general background concentration levels.
National Air Monitoring Stations (NAMS)
NAMS are a selected subset of the SLAMS sites, covering urban and multi-source areas. The
emphasis is on areas of maximum concentrations and high population density. NAMS, like SLAMS, must
conform to EPA siting criteria and operate according to quality assurance procedures that meet or exceed
EPA's minimum specifications The NAMS differ from the SLAMS in that NAMS must use continuous
automated instruments for gaseous pollutants.
The NAMS fall into two categories
• Category (a) - stations in areas of expected maximum concentrations (usually middle scale)
• Category (b) - stations in areas with both poor air quality and high population density. These
areas are not necessarily those with expected maximum concentrations. They will usually be
densely populated neighborhoods, but may be areas where sensitive individuals are likely to
live or work, if such areas are common to the neighborhood.
Urban areas where NAMS are required will usually have both types of stations. It is possible that
only one monitoring station will be needed for PM,0 or SO2, in which case it must be a Category (a)
station
E1SOPQAM 2 - 19 May 1996
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Network Design
Sue selection is based on population and expected pollutant concentration. Tables 2 10 1 and
2 10 2 show the population levels for which NAMS monitoring is required The required spiuiaJ scales
for NAMS are shown in Table 2 10.3. Although SLAMS do not have specific scale requirements, the
scales that are appropriate to each pollutant are also shown in Table 2.10.3. Selection of urban areas and
actual number of stations per area is jointly determined by EPA and the state agency.
TABLE 2.10.1
GUIDELINES for PM10 and S02 NAMS NETWORK SIZE
(APPROXIMATE NUMBER of STATIONS PER AREA)
Population Area
> 1,000,000
500.000-1.000,000
250.000-500,000
100.000-250,000
High'
6-10
4-8
3^
1-2
Population Concentration
Medium"
4-8
2-4
1-2
0-1
Lowc
2-4
1-2
0-1
0
(a) PMIO: High concentration areas are those for which ambient PM]0 data show ambient
concentrations exceeding PMIO National Ambient Air Quality Standards (NAAQS) by
20% or more
SO;. Defined as high when the ambient concentration exceeds the level of the primary
NAAQS.
(b) PM,0: Ambient concentrations exceed 80% of the NAAQS.
SOv Ambient concentrations exceed 60% of the primary or 100% of the secondary
NA'AQS.
(c) PM10 Ambient concentrations are less than 80% of the NAAQS
SO, Ambient concentrations are less than 60% of the primary or 100% of the
secondary NAAQS
EISOPQAM 2 - 20 May 1996
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TABLE 2.10.2
POPULATION LEVELS for which NAMS MONITORING of POLLUTANTS other than PM10 and
S02 is REQUIRED
POLLUTANT
POPULATION
Lead
CO
Ozone
NO,
500,000'
500,000
200,000
1,000.000
(a) The minimum is also a SLAMS requirement. NAMS monitoring is also required
whenever the NAAQS has been exceeded in any of the last eight quarters.
TABLE 2.10.3
SUMMARY of SPATIAL SCALES USUALLY NEEDED for SLAMS and NAMS
Spatial Scale
Micro
Middle
Neiehborhood
Urban
Regional
Spatial Scale
Micro
Middle
Neighborhood
Urban
Regional
Scale Appropriate for SLAMS
SO,
X
X
X
CO
X
X
X
03
X
X
X
X
NO2
X
X
X
Pb
X
X
X
X
X
PM10
X
X
X
X
X
Scale Appropriate for NAMS
SO:
X
CO
X
X
03
X
X
N02
X
X
Pb
X
X
X
PM10
X
X
X
EISOPQAM
2-21
May 1996
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Monitoring Methodology
The monitoring methods that must be used in NAMS/SLAMS are specified in 40 CFR 58.
Appendix C (hereafter referred to as Appendix C) Reference methods (or their equivalent) must be used
for all regulatory purposes.
An analyzer with a nonconforming range greater than twice the upper limit may be used if it has
more than one range At least one of ihese ranges must be designated a reference or equivalent method
and it must be the one in which the pollutant concentration is likely to occur Further, the EPA
Administrator must determine that the resolution of the range is adequate. See Section 2.6, Appendix C,
for further details.
Requests for approval of a sampling method must be submitted to the Director, National Exposure
Research Laboratory (NERL), United States Environmental Protection Agency, Environmental Research
Center, Research Triangle Park, North Carolina 27711.
Probe Suing
Tables 2.10.4 and 2 10.5 display the requirements for probe siting. For clarification or
justification, refer to Appendix D of 40 CFR 58.
Only borosihcate glass and Teflon* or their equivalent are acceptable materials for intake sampling
lines The residence time in sampling probes for reactive gases must be less than 20 seconds
2 10.3 State and Local QA Plan Reviews
Introduction
40 CFR, Pan 58, Appendix A specifies the minimum quality assurance (QA) requirements
applicable to SLAMS air monitoring data submitted to EPA. The QA Plan for an air monitoring network
contains two distinct functions: control of the measurement process and assessment of the quality of
monitoring data The QA Plan must be approved by the Regional Administrator or his designee. In
Region 4, the Region's QA Officer has been delegated the authority to approve QA Plans The Air
Monitoring Team (AMT) reviews QA Plans for SLAMS in Region 4.
Review/Approval Process
The AMT reviews state and local QA Plans submitted to the Regional Administrator for approval
Ai a minimum, each QA Plan must include operational procedures for the 14 elements listed in Section 2 0
of 40 CFR Pan 58, Appendix A Based on the review results and comments received from the reviewers,
the AMT recommends approval/disapproval action to the Region 4 QA Officer. If the AMT Leader
recommends disapproval of a state or local QA Plan, he/she will hold the review process in abeyance until
he/she has requested and received additional information necessary to approve the QA Plan from the state
or local agency which submitted the QA Plan
EISOPQAM 2 - 22 May 1996
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TABLE 2.10.4
SUMMARY of PROBE SITING CRITERIA
Pollutant
CO
S02
Ozone
NO,
Lead
PM,o
Scale
Micro
Middle and Neighborhood
All
All
All
Micro
All Others
Micro
All Others
Height Above
Ground(m)
3 ± 1/2
3- 15
3-15
3-15
• 3-15
2- 7
2- 15
2- 7
2-15
Other Spacing Criteria
6, 7, 3, 5
3,8,5
1.2,3,4,5
1.2,3,5,8
1.2,4,9, 10,, 11
1.2,4,8,9.10
1.2,4,9, 10,, 12
1,2,4,9, 10. 12
6
7
8
9
10
10,
11
12
Should be greater than 20 meters from tree driplines and must be 10 meters from the
dnplme when trees act as an obstruction.
Distance from inlet probe to obstacle, such as buildings, must be at least twice the height the
obstacle protrudes above the inlet pole. Sites not meeting this criterion would be classified
as middle scale.
Must have unrestricted airflow 270 degrees around the inlet probe, or 180 degrees if the
probe is on the side of a building
No furnace or incinerator flues should be nearby. Distance is dependent on height of
furnace or incineration flues, type of fuel or waste burned, and quality of fuel (sulfur, ash,
or lead content) This is to avoid undue influences from minor pollutant sources.
The horizontal and vertical distance from supporting structures must be greater than 1
meter (When the probe is located on a rooftop, this distance is in reference to walls.
parapets, or penthouses located on the roof)
Must be greater than 10 meters from a street intersection and should be located mid-block.
Must be 2-10 meters from the edge of the nearest traffic lane.
Spacing from roads varies with traffic (Table 2.8.5).
The horizontal distance from supporting structures must be greater than 2 meters
Must have unrestricted airflow 270 degrees around the sampler.
Must have unrestricted airflow 270 degrees around the sampler, except for street canyon
sites
Must be 5-15 meters from major roadways.
Spacing from roads vanes with traffic except for CO street canyon sites, which must be 2-
10 meters from the edge of the nearest traffic lane.
EISOPQAM
2-23
May 1996
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TABLE 2.10.5
MINIMUM DISTANCE BETWEEN SAMPLING PROBE and ROADWAYS
(EDGE of NEAREST TRAFFIC LANE)
Roadway Average
Daily Traffic (ADT)
(vehicles per day)
Minimum Distance
Between Roadways and
Stations* (meters)
Neighborhood - Scale CO Stations
< 10,000
15,000
20,000
30,000
40,000
50.000
> 60,000
10
25
45
80
115
135
>150
Neighborhood and Urban-Scale Ozone and NO2 Stations
< 10,000
15,000
20,000
40.000
70.000
> 110.000
10
20
30
50
100
>250
Lead Stations
10.000
20.000
40.000
Middle
Micro Scale Neighborhood,
Urban Scale
5-15 > 15 - 50
5-15 > 15 - 75
5-15 > 15 - 100
* Distances should be interpolated based on traffic flow
Regional
Scale
>50
>75
>100
EISOPQAM
2-24
May 1996
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2104 Performance Audits
Introduction
Performance audits are conducted by the appropriate AMT staff to assess local and state agencies'
quality assurance program. The audits allow for an overall estimate of a given agencies' data quality
However, the result of an audit is not a definitive indicator of the overall quality of an agency's data base
When scheduling audits with a state or local agency, the state Quality Assurance Coordinator must
be notified in advance to allow for state agency representation during the audit Upon arrival at the audit
location, all principles involved must be briefed to explain the audit, its meaning, and the use of its results
Following the initial conference, the audits will be performed. The auditor will ask the station operator
to verify that no unscheduled zero or span adjustments have been made prior to the audit During the
audit, the auditor will request the station operator to read the instrument responses from the agency
monitor All data will be recorded on the appropriate audit form. The form shall be signed by the auditor
and an agency representative
Following the completion of the audit, an exit conference will be conducted where results of the
audit will be discussed The auditor should not give copies of the audit form to the agency personnel until
after returning to the office and after the audit data have been verified. Having verified an auditor's
results, copies of the audit form will be sent to the affected agency and state Quality Assurance
Coordinator
Multi-Component Blends And Audit Gases
A multi-component blend of CO. SO:. and NO2 (or any combination of these three gases) may be
used However, the blend shall be composed of gases, each of which is either a Standard Reference
Material (SRM) or an EPA Protocol Gas
All audit gases shall be traceable to National Institute of Standards and Technology Standard
Reference Materials (SRMs) or the gases used in the audit may be SRMs or EPA Protocol Gases
Carbon Monoxide
Carbon monoxide audit concentrations shall be introduced into the monitor prior to any filters,
dryers, or mixing chambers Audit concentration points will be in the following ranges.
Audit Point
1
2
3
4
Concentration (ppm CO)
3-8
15-20
35-45
80-90
Note. Audit point #4 will be run only on monitors operated in the 0 to 100 ppm range
EISOPQAM 2 - 25 May 1996
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Ozone audit concentrations shall be introduced into the monitor at the same point where ambient
air enters the sampling system. The audit concentration should be introduced through the probe, if
possible Audit concentration points will be in the following ranges.
Audit Point
1
2
3
4
Concentration (ppm O3)
0 03 - 0.08
0 15 - 0.20
0.35 - 0.45
0.80 - 0.90
Note- Audit point #4 will be run on monitors operating in the 0 to 1.0 ppm range.
Sulfur Dioxide
Sulfur dioxide audit concentrations shall be introduced into the monitor through the paniculate
filter The audit concentration should be introduced through the probe, if possible Audit concentration
points will be in the following ranges.
Audit Point
1
2
3
4
Concentration (ppm SO3)
0.03 - 0.08
0.15-0.20
0.35 - 0.45
0.80 - 0.90
Note Audit point #4 will only be run on monitors operating in the 0 to 1.0 ppm range.
Nnrogen Dioxide
Nitrogen dioxide audit concentrations shall be introduced into the monitor through the paniculate
filter The audit concentration should be introduced through the probe, if possible. Audit concentration
points will be in the following range
Audit Point
Concentration (ppm NO,)
1
0.03 - 0.08
0.15-0.20
0.35 - 0 45
0.80 - 0 90
Note Audit point #4 will only be run on monitors operating in the 0 to 1.0 ppm range. If the audit is
being conducted with a gas phase titrator (gpt). it will be necessary to run a zero and span point on the
monitor's NO, and NO channels. If NO and/or NO, data collected by a state/local agency are submitted
EISOPQAM
2-26
May 1996
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10 the AIRS system, the NO and/or NO, channel must be audited using either cylinder dilution or gpt
EISOPQAM 2 - 27 May 1996
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2 10.5 National Air Monitoring Audit System
Introduction
A systems audit is an on-site review and inspection of a state or local agency's ambient air
monitoring program to assess its compliance with established regulations governing the collection, analysis.
validation, and reporting of ambient air quality data. To promote uniformity in the evaluation of state and
local agencies' monitoring programs and performance, the air monitoring staff will use the "short form"
questionnaire and the reporting format described in detail in Section 2.0.11 of "The QA Handbook for Air
Pollution Measurement System," Volume II, Ambient Air Specific Methods, US EPA, Office of Research
and Development (ORD), NERL, Research Triangle Park, NC. (This Handbook is commonly referred
to and will be called the "Red Book ") The use of the "long form" questionnaire is left to the discretion
of the Regional QA Officer. The scope of the systems audit includes an appraisal of network management,
field operations, laboratory operations, data management, quality assurance, and reporting The systems
audit results should present a clear, complete, and accurate picture of the agency's collection and reporting
of ambient air monitoring data
Frequency of Systems Audits
The EPA Regional Office retains regulatory responsibility to evaluate agency performance
annually For well-established agencies, an extensive systems audit and rigorous inspections may not be
necessary every year. Agencies are presently scheduled on a three-year rotation, unless problems occur
The determination of the extent of the systems audit is left to the Regional Office's discretion
Selection of Monitoring Sites for Inspection
It is suggested that approximately five percent of a state agency's sues be inspected during a
systems audit For smaller agencies, at leasi two sues should be inspected One half of the sues to be
inspected should be selected by the agency being audited, while the other half should be selected by the
RO audit team
Data Audits
A complete systems audit must include a review of the data processing and reporting procedures
starting at the acquisition stage and terminating at the point of data entry into the AIRS computer system
The guidance for conducting a data audit is given in Section 11.3.3 of the Red Book.
Guidelines for Conducting Systems Audits of State and Local Agencies
A systems audit should consist of three separate phases'
• pre-audii activities:
• on-site activities, and
• post-audit activities
Each of these activities is discussed in detail in Sections 2.0 11.4.1; 2.0.11.4.2; and 2.0 11.3 of
the Red Book Because of the length of these sections of the Red Book, they are incorporated by reference
EISOPQAM 2 - 28 May 1996
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Audi! Reporting
The systems audit report format discussed in section 2.0.11.4.4 in the Red Book has been prepared
to be consistent with guidance offered by the State and Territorial Air Pollution Program Administrators
(STAPPA)/Association of Local Air Pollution Control Officials (ALAPCO) Ad Hoc Air Monitoring Audit
Committee The Office of Air Quality Planning and Standards considers the format acceptable for annual
systems audit reports. At a minimum, the systems audit report shall include:
• Executive Summary
• Introduction
• Audit Results
• Network Design
• Resources and Facilities
• Data and Data Management
• Quality Assurance/Quality Control
• Discussion
• Conclusions and Recommendations
• Appendix of Supporting Documentation
The Discussion section of the report should include a narrative of the process used to interpret audit
results, identify the derivation of results affecting data quality, and outline the basis for corrective action
recommendations
The report's Conclusion and Recommendations should center around the overall performance of
the agency's monitoring program This section should include the major problems, corrective action
agreements, the homogeneity of the reporting organization, and the appropriateness of pooling the precision
and accuracy (PA) data
The report's Appendix of Supporting Documentation contains copies of the completed short-form
questionnaire. Corrective Action Implementation Request (CAIR) form, and documentation contributing
significantly to the audit results.
2 10 6 National Performance Audit Program
Introduction
Appendix A, Part 2.4 of 40 CFR Part 58 requires agencies operating SLAMS networks to
participate in EPA's National Performance Audit Program (NPAP). In addition, agencies receiving Section
105 grants in Region 4 are required to participate in NPAP. The purposes of NPAP are to provide
agencies with a means of self-appraisal for the specific operation audit and to provide EPA with an index
of the data quality reported to the AIRS data bank.
Air Monitoring Team
The Air Monitoring Team's role is to coordinate the NPAP between state and local agencies and
EPA's Office of Air Quality Planning and Standards (OAQPS)
Audit Survey
The audit survey is conducted annually on high volume samplers (TSP and PM10) and semi-
EISOPQAM 2 - 29 May 1996
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annually on continuous sampler (SO,, 03. N02, and CO) and lead (Pb).
EISOPQAM 2 - 30 May 1996
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2.11 References
1 US-EPA, NPDES Compliance Inspection Manual. September 1994.
2 US-EPA, NPDES Compliance Evaluation Inspection Manual. MCD-75, United States
Environmental Protection Agency, Washington, D.C.m 1981.
3 US-EPA, NPDES Compliance Sampling Inspection Manual. MCD-51, United States
Environmental Protection Agency, Washington, D.C., 1979.
4 Compliance Biomonitonng Inspections Manual. MCD-62, United States Environmental Protection
Agency, Washington, D.C., 1981.
5 Guidance for Conducting Remedial Investigations and Feasibility Studies Under CERCLA -
Interim Final; EPA/540/G-89/004
6. RCRA Ground-Water Monitoring Technical Enforcement Guidance Document (OSWER 9950 1)
September 1986.
7 Draft RCRA Preliminary Assessment/Site Investigation Guidance — US-EPA, Permits and State
Programs Division, Office of Solid Waste, August 1985.
EISOPQAM 2-31 May 1996
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EXHIBIT 2.1
REGION 4
HAZARDOUS WASTE FIELD OVERVIEW CHECKLIST
Facility/Site Name
Address
Project No
EPA ID No.
Facility Contact
Phone No.
Overview Personnel
Date
State/Contractor Project Leader
Affiliation
Phone No.
Address
Sampling Personnel
Other Personnel & Affiliation
Type of study9
Study plan issued9
Date issued0
Study plan reviewed by the Division9
Comments'
Acceptable?
Was study plan followed9
Comments
Was a safety plan prepared for the study9
Comments
Was the safety plan adequate9
Comments
Was the safety plan followed9
Comments
Additional comments or information
Checklist sections completed
for this overview
1
3.
4.
Key 1. General Procedures
2. Ground Water Sampling
3 Soil. Sediment. Sludge Sampling
4. Surface Water Sampling
5. Waste Sampling
6. Monitoring Well Installation
EISOPQAM
2-32
May 1996
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SECTION 1 - GENERAL PROCEDURES - SAFETY. RECORDS. OA/QC. CUSTODY. ETC
1 Type samples collected?
Comments.
2 Were sampling locations properly selected7
Comments-
3 Were sampling locations adequately documented in a bound field log book using indelible
ink7
Comments-
4 Were photos taken and a photolog maintained7
Comments-
5 What field instruments were used during this study?
Comments:
6 Were field instruments properly calibrated and calibrations recorded in a bound field log
book7
Comments-
7 Was sampling equipment properly wrapped and protected from possible contamination
prior to sample collection7
Comments
8 Was sampling equipment constructed of Teflon®, glass, or stainless steel7
Comments-
9 Were samples collected in proper order7 (least suspected contamination to most
contaminated7)
Comments
10 Were clean disposable latex or vinyl gloves worn during sampling7
Comments
11. Were gloves changed for each sample station?
Comments
12 Was any equipment field cleaned7
Comments-
13 Type of equipment cleaned
Comments:
14 Were proper field cleaning procedures used7
Comments-
15 Were equipment rinse blanks collected after field cleaning?
Comments.
16 Were proper sample containers used for samples?
Comments-
E1SOPQAM 2 - 33 May 1996
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17 Were split samples offered to the facility owner or his representative?
Comments-
18 Was a Receipt for Samples form given to facility representative?
Comments-
19 Were any duplicate samples collected9
Comments-
20 Were samples properly field preserved?
Comments:
21. Were preservative blanks utilized9
Comments:
22 Were field and/or trip blanks utilized9
Comments-
23 Were samples adequately identified with labels or tags?
Comments-
24 Were samples sealed with custody seals after collection?
Comments-
25. What security measures were taken to insure custody of the samples after collection9
Comments-
26 Were chain-of-custody and receipt for samples forms properly completed9
Comments-
27 Were any samples shipped to a laboratory?
Comments-
28 If yes to No 27. were samples properly packed?
Comments
29 If shipped to a CLP lab. were Traffic Report Forms properly completed?
Comments
30. What safety monitoring equipment, protection, and procedures were used prior to and
during sampling9
Comments
31 Was safety monitoring equipment properly calibrated and calibrations recorded in a bound
field log book?
Comments
E1SOPQAM 2 - 34 May 1996
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SECTION 2 - SAMPLING - GROUND WATER
1 Type of wells sampled7 (monitoring, potable, industrial.etc.)
Comments1
2 Were wells locked and protected9
Comments. ^
3 Were identification marks and measurement points affixed to the wells?
Comments:
4 What were the sizes and construction materials of the well casings?
Comments-
5 Were the boreholes sealed with a concrete pad to prevent surface infiltration9
Comments.
6 Was there a dedicated pump in the well?
Comments-
7 Was clean plastic sheeting placed around the wells to prevent contamination of sampling
equipment and containers?
Comments-
8 Were total depths and depths to water determined before purging?
Comments ^
9 What device was used to determine depths9
Comments
10 Were measurements made to the nearest 0.01 ft9
Comments-
11 Was the measuring device properly cleaned between wells?
Comments
12 Was the standing water volume in each well determined?
Comments-
13 How was the volume determined9
Comments-
14 Was a sufficient volume purged prior to sampling?
Comments-
15 How many volumes9
Comments.
16 How was the purged volume measured9
Comments:
17 What was the method of purging9
Comments
EISOPQAM 2 - 35 May 1996
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18
19
20
21.
22
23
24
25
26
27
28
29
30
31.
32
33
34
Were pH, conductivity, temperature, and turbidity measurements taken and recorded at least
once during each well volume purged*7
Comments
Were pH, conductivity, temperature, and turbidity readings stable prior to sampling9
Comments1
How many wells were sampled9 Upgradient? Downgradient?
Comments.
How were the samples collected? Bailer Pump Other
Comments:
If a pump was used, what type?
Comments.
If a pump was used, was n properly cleaned before and/or between wells9
Comments'
Whai were the cleaning procedures?
Comments:
Did bailers have Teflon* coated wire leaders to prevent rope from coming into contact
water?
Comments
Were bailers open or closed top9
Comments
Was a clean bailer and new rope used at each well?
Comments-
Were samples properly transferred from the sampling device to the sample containers?
volatile sample first - not aerated, etc.)
Comments
Was pH of preserved samples checked to insure proper preservation?
Comments.
Were samples iced immediately after collection?
Comments
For what analyses were the samples collected?
Comments.
If samples were split, what were the sample/station numbers for these?
Comments
Are the ground water samples being filtered9
Comments:
If the ground water are being filtered, what procedure is being used?
Commems'
with
(i.e.,
E1SOPQAM 2 - 36 May 19%
-------
35 Is low flow/low volume sampling being conducted (e.g., is the intake of the pump at the
middle of the screen)?
Comments.
36 If low flow/low volume sampling is being conducted, is the water level being measured
constantly to insure minimal drawdown of the less than 3 to 4 inches?
Comments'
33 Other comments or observations
E1SOPQAM 2 - 37 May 1996
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SECTION 3 - SAMPLING - SOIL, SEDIMENT. SLUDGE. ETC. (Non-coniainenzed)
1 Type of samples collected''
Comments:
2 General description of samples?
Comments:
3 How many samples were collected9
Comments:
4 Were background and/or control samples collected?
Comments:
5 Were representative samples collected?
Comments'
6 Were grab or composite samples collected?
Comments
7 Were composite samples areal or vertical?
Comments
8 How many aliquots were taken for the composite sample?
Comments'
9. What procedures and equipment were used to collect samples?
Comments' ^
10 Were samples thoroughly mixed prior to putting them into the sample containers'7
Comments:
11 Were samples properly placed into sample containers9
Comments:
12 Were samples iced immediately after collection?
Comments'
13 For what analyses were the samples collected*3
Comments1
14 If samples were split, what were the sample/station numbers for these?
Comments
15 Was a drilling rig, back hoe. etc used to collect soil samples?
Comments'
16 Were the drilling rig(s), backhoe(s). etc., properly cleaned according to the SOP, Appendix
B, prior to arriving on sue9
Comments' ^
17 What was the condition of the drilling and sampling equipment when it arrived on site9
ents:
E1SOPQAM 2 - 38 May 19%
-------
18 Was a decontamination area located where the cleaning activities would not cross-
contaminate clean and/or drying equipment?
Comments-
19 Was clean equipment properly wrapped and stored in a clean area?
Comments:
20 Was the drilling rig(s) properly cleaned between well borings?
Comments:
21 Were the cleaning and decontamination procedures conducted in accordance with the SOP9
Comments:
22 Other comments or observations-
EISOPQAM 2 - 39 May 1996
-------
SECTION 4 - SAMPLING - SURFACE WATER fPond. Stream. River. Leachaie. Etc )
1 Type of samples collected9
Comments'
2 General description of samples9
Comments
3 How many samples were collected9
Comments:
4 Were background and/or control samples collected?
Comments:
5 Were grab or composite samples collected?
Comments.
6 How many aliquots were taken for the composite sample?
Comments:
7 What procedures and equipment were used to collect the samples?
Comments
8 Were samples collected directly into sample containers9
Comments.
9 Did the sampler wade in the stream to collect the samples?
Comments.
10 Were the samples collected upstream from the sampler?
Comments
11 Did the sampler insure that roiled sediments were not collected along with the water
samples?
Comments-
12 Were representative samples collected9
Comments
13 Was the pH of preserved samples checked to insure proper preservation9
Comments.
14 Were samples iced immediately after collection9
Comments-
15 For what analyses were the samples collected9
Comments
16 If samples were split, what were the sample/station numbers for these?
Comments-
17 Other comments or observations-
EISOPQAM 2-40 May 1996
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EISOPQAM 2-41 May 1996
-------
SECTIONS - WASTE SAMPLING-DRUMS. TANKS. BARRELS. ETC (Container.zed)
1 What was the objective of the sampling investigation?
Comments
2 Description of units or sources sampled (closed/open, etc.)9
Comments
3 General description of samples (Oil, sludge, waste)
Comments:
How many samples were collected9
Comments-
5 Were grab or composite samples collected?
Comments
6. How many ahquots were taken for the composite sample7
Comments-
7 What type of equipment was used to collect the samples?
Comments-
8. What procedures were used to collect the samples?
Comments
9 Were solid/semi-solid waste samples thoroughly mixed prior to putting them into the sample
containers9
Comments-
10 Were samples properly placed into sample containers9
Comments
11 For what analyses were the samples collected?
Comments-
12 Was equipment field cleaned9
Comments
13 Was clean equipment properly wrapped and stored in a clean area9
Comments
14 Were the cleaning and decontamination procedures conducted in accordance with the
Appendix B of the EISOPQAM0
Comments-
15 Were the study's objectives accomplished?
Comments
16 If samples were split, what were the sample/ station numbers for these?
Comments-
17. Were any special safety measures taken during collection of the samples?
Comments-
EISOPQAM 2 - 42 May 1996
-------
18 What level of safety protection was required for collection of the samples?
Comments
19 Other comments or observations
EISOPQAM 2 - 43 May 1996
-------
SECTION 6 - MONITORING WELL INSTALLATION
GENERAL
1 Were the wells installed in the proper locations in accordance with the study plan and/or
project operations plan (POP)9
Comments
2 Were the wells installed starting in the least contaminated area and proceeding to the most
contaminated area9
Comments: ^
3 Were proper safety protocols employed during the well installations?
Comments:
4 Were samples of the drilling mud, water, bentonite pellets, filter pack materials, etc.,
collected for quality control analyses?
Comments:
EQUIPMENT DECONTAMINATION
5. Were the drilling ng(s). backhoe(s), etc., properly cleaned according to the SOP, Appendix
B, prior to arriving on site?
Comments
6 What was the condition of the drilling and sampling equipment when it arrived on site7
Comments ^
7. Was a decontamination area located where the cleaning activities would not
cross-contaminate clean and/or drying equipment9
Comments-
8 Was clean equipment properly wrapped and stored in a clean area?
Comments:
9 Was the drilling ng(s) properly cleaned between well borings?
Comments:
10 Were the cleaning and decontamination procedures conducted in accordance with the SOP?
Comments-
11 What type of drilling method(s) was used to install the wells9
Comments
12 Was this drilling method(s) the same as proposed in the study plan and/or POP9
Comments
13. Were soil samples collected for logging and analyses as the wells were installed?
Comments-
14 If yes to 13, at what intervals and by what method?
Comments-
EISOPQAM 2-44 May 1996
-------
15. If air rotary was used, was an in-line organic air filter employed? Was a cyclone velocity
dissipator used?
Comments
16 What diameter borehole(s) were installed?
Comments:
17 Were surface outer casings used?
Comments:
18 If yes to 17, what size and to what depth9
Comments:
19 Were the wells double cased?
Comments:
20 If yes to 19, explain procedure
Comments1
PERMANENT WELL INSTALLATION
21 What type of well casmg(s) and screen(s) were used?
Comments:
22. What diameter were the well casmg(s) Screen(s)?
Comments-
23 Was there a minimum two inch annulus around the casing between casing and borehole was
or inside augers)9
Comments
24 What was the length of the well screen(s)?
Comments
25 What was the slot size of the well screens)9
Comments:
26 Was the well screen(s) commercially manufactured? If so, by whom?
Comments
27 Was the bottom of the well screen(s) plugged or capped?
Comments
28 Were sand and/or gravel (filter) packs installed9
Comments-
29 Specify type of materials in 28 [(play sand, Ottawa sand, etc.) and gram size (20/30, 20/40.
etc )]. if known.
Comments-
30 Was a sieve analysis conducted to determine well screen slot size and filter pack grain size9
Comments
31 Were the wells installed to the proper depths?
Comments-
EISOPQAM 2 - 45 May 1996
-------
32 Were well screens placed at the proper intervals?
Comments
33 Were the filter packs placed a minimum of two feet above the well screens7
Comments.
34 Was the tremie tube method used to place the filter packs?
Comments
35 Were seals placed above the filter packs7
Comments:
36 If yes to 35, what material was used for the seals?
Comments:
37 Was the vertical thickness of the seals a minimum of two feet?
Comments
38 If bentomte pellets were used for the seals above the filter packs, were they allowed to
hydrate a minimum of 8 hours?
Comments:
39. Did contractor/driller have documentation from manufacturer stating recommended
hydration time9
Comments
40 Was the tremie tube method used to place the bentomte pellets9
Comments
41 Was the annulus grouted from the seal to within two feet of the ground surface, or below the
frost line9
Comments
42 Was the tremie tube method used to place the grout in the annulus?
Comments
43 If no to 42, what method was used9
Comments
44. What type of grout was used to seal the annulus (neat cement, cement/bentomte,
cement/sand, etc.)9
Comments
45 What grout mix ratio was used9 (should be stated in the POP)
Comments.
46 What was the density of the grout9 (Ib/gal, etc.)
Comments
47 If bentomte grout was used, was the density at least 9 4 Ib/gal?
Comments
48 Was the density determined using a mud balance9
Comments
EISOPQAM 2-46 May 1996
-------
49 Was the grout allowed to set a minimum of 24 hours before the surface pad was installed9
Comments-
50 Was a concrete surface pad installed with an outer protective casing and locking cap9
Comments-
51 How far below the ground surface did the concrete pad extend?
Comments-
52 What were the dimensions of the concrete pads9
Comments:
53 Did the well casings extend to a minimum of 2.5 feet above the ground surface9
Comments:
54 How far above the ground surface did the outer protective casings extend?
Comments
55 Did the outer protective casings have weep holes?
Comments-
56 Were the wells properly developed9
Comments:
57 Describe method of development.
Comments:
58 Give a general evaluation of the activities observed during the installation of the wells
Comments
TEMPORARY WELL INSTALLATION
59 Describe methods and procedures
Comments
EISOPQAM 2 - 47 May 1996
-------
EXHIBIT 2.2
REGION 4
STATE/CONTRACTOR OVERVIEW CHECKLIST
*#*
NOTE *** This checklist is for overviewmg State personnel overviewing a facility or contractor or
for overviewmg a contractor overviewmg contractors.
PARTI
State/Contractor Name
Address
Facility/Site Name
Address
Facility Contact | Phone No.
Facility Activities/Operations
Project No.
EPA ID No.
Audit Personnel
Date
State/Contractor Project Leader
Title
Phone No.
Sampling Personnel
Other Personnel & Affiliation
Type of study9
Study/Work plan issued9
Date issued?
Study/Work plan reviewed by the Division9
Acceptable9
Was the Study/Work plan reviewed by the State/Contractor?
Comments
Was the study plan followed9
Comments.
Was a safety plan prepared for the study?
Did the State/Contractor review the safety plan9
Was the safety plan adequate9
Comments
Was the safety plan followed?
Comments
Did the State/Contractor have their own safety plan?
Did the State/Contractor have a copy of the SOP or have a copy of their own SOP?
Comments
Was the State/Contractor familiar with the SOP?
Additional Comments or Information
EISOPQAM 2 - 48 May 1996
-------
EISOPQAM 2 - 49 May 1996
-------
PART 2
1 Was a field overview checklist completed''
Comments:
2 Was the State/Contractor familiar with the facility and its operations?
Comments
3 Was the State/Contractor trained in equipment handling and proper sampling techniques''
Comments:
4 Did the State/Contractor observe calibration of safety monitoring and/or field measurement
equipment?
Comments:
5 Did the State/Contractor observe all phases of the field investigation such as sampling, field
measurements, record keeping, packing and shipping samples, etc.?
Comments:
6 Did the State/Contractor advise sampling personnel regarding improper procedures or
practices whenever they were observed?
Comments
7. Did the State/Contractor assist with the sampling, equipment decontamination or any other
phase of the investigation9
Comments:
8 Were there improper procedures or practices used which the State/Contractor failed to
recognize9
Comments
9 Was sampling conducted in accordance with the SOP or other EPA standard operating
procedures9
Comments
10 Was equipment decontamination conducted in accordance with standard operating
procedures specified by EPA9
Comments-
11 List any problem areas observed relative to questions #8, #9 or #10:
Comments
12 What are the qualifications of the investigative/sampling personnel (training and experience)
by name9
Comments
13 Had those personnel received training in sampling techniques and equipment handling9
Comments
14 When was the latest training received and by whom was it provided9
Comments-
15. What equipment was available and/or used during the investigation?
Comments
E1SOPQAM 2 - 50 May 1996
-------
16 Did equipment appear to have been properly cleaned and protected from possible
contamination prior to bringing it to the field?
Comments-
17 What type of samples were collected?
Comments:
18 For what analyses were the samples collected?
Comments-
19 Was sampling conducted in accordance with standard operating procedures specified by the
State or EPA7
Comments:
20 Did investigative/sampling personnel conduct a comprehensive investigation/evaluation or
only collect samples?
Comments
21 If investigative/sampling personnel only collected samples, how were their sampling efforts
coordinated with the rest of the investigation?
Comments:
22 If facility personnel collected samples, did the State/Contractor accept split samples'*
Comments-
23 Were adequate field records kept in a bound log book?
Comments
24 Were photographs taken and a photo log maintained''
Comments
25 Were QA/QC procedures adequate for the type of study being conducted and type/number
of samples being collected9
Comments-
26 Had investigative/sampling personnel received appropriate safety training9
Comments
27 Do investigative/sampling personnel undergo periodic refresher safety training?
Comments:
28 Did investigative/sampling personnel have appropriate safety equipment for the
investigation9
Comments-
29 Are investigative/sampling personnel classified as to the type of investigations they can
conduct?
Comments
30 Have investigative/sampling personnel had comprehensive physicals7
Comments
31 Do investigative/sampling personnel participate in a medical monitoring program9
Comments
EISOPQAM 2-51 May 1996
-------
32 Give a general evaluation of the activities observed during the overview and note any other
comments or observations
Comments
EISOPQAM 2 - 52 May 1996
-------
EXHIBIT 2.3
STATE PROGRAM EVALUATION
HAZARDOUS WASTE FIELD ACTIVITIES
State
Agency
Specific Activity
RCRA or CERCLA
Location
Telephone
Activity Managers
Evaluate:
Date
PART 1 -- FIELD ACTIVITY STAFFING
Description of Field Activity-
Field Activity Personnel Staffine
NAME(s)
Field Safety Proeram
and Training-
TITLE
TRAINING
Personnel categorized as to activity?
EXPERIENCE
Does a formal safety training program exist?
Does a formal safety training tracking system exist?
Does a formal medical monitoring program exist7
Safety Training
Received9
In-House
Safety Program Needs-
Outside EPA
Field Activity Adeauatelv Staffed to meet Existing RCRA or CERCLA Insnection and Investigation
Needs Adequate Inadequate
Protected Staffinc Needs
EISOPQAM
2-53
May 1996
-------
PART 2 -- FIELD OPERATING PROCEDURES
1 Does a standard operating procedures manual exist or is one being prepared9
Comments
2 Are inspection schedules and study plans prepared?
Comments'
3. Are these inspections and studies coordinated with the lab?
Comments:
4 Addressed in the SOP?
Comments.
5 Are formal inspection and investigation reports prepared9
Comments
6. Are the field activities adequately addressed in the SOP Manual?
Comments
Does the SOP address (Sample Collection)
- Ground Water
- Surface Water
Surface Soil
Subsurface Soil
- Waste - Pus. Ponds. Lagoons
Waste - Closed Container
- Tissue (Fish, etc )
- Air
- QC
Comments
YES
NO
Does the SOP address (Sample Handling Techniques)
Standard Sampling Containers
Field Equipment & Sample Container Cleaning Procedures
Sample Identification
- Sample Preservation & Holding Times
Sample Cham-of-Custody
Sample Packaging Techniques
Identification of Hazardous Samples to Lab
- QC
YES
NO
EISOPQAM
2-54
May 1996
-------
Comments.
9 Does the SOP address: (Field Documentation and Records)
Field Documentation or Bound Record Books
Comments:
Photographs
Comments:
Sue Mapping (Sketching of sues)
Comments
YES
NO
PART
1.
2
3
3 -- FIELD CONTRACTORS
Are Held contract personnel used to conduct field investigations?
Comments'
What activities do field contractors perform?
Comments
If yes, does a quality control program exist to monitor contractor
Comments-
activities?
PART 4 - FACILITIES
1 Is adequate space provided for the storage of field equipment?
Comments
Are facilities and/or space provided for the cleaning, repair, and preparation of field
equipment*7
Comments.
Specific Facility Needs.
EISOPQAM
2-55
May 1996
-------
PART 5 - FIELD EQUIPMENT AVAILABLE
1 Sampling and Investigative Equipment Available:
- Field Vehicles
• Field Analytical Instrumentation
- Surveying Equipment
- Photographic Gear
- Pumps and Automatic Samplers
- Ground Water Sampling Equipment
- Surface Water Equipment
- Sediment Sampling Equipment
- Soil Coring Equipment
- Waste Sampling Equipment
- Geophysical Equipment
- Temporary Well Installation Equipment
2 Specific Sampling and Investigation Equipment Needs:
Comments'
Safety Equipment Available
- Monitoring Equipment
- Protective Clothing
- Respiratory Protection
4 Are Safety Procedures available in written form or in a manual9
Comments
5 Specific Safety Equipment Needs
Comments
6 Does a specific field or safety equipment needs list exist?
Comments'
7 Is there an allowance for an equipment budget?
Comments-
EISOPQAM 2 - 56 May 1996
-------
SECTION 3
-------
SECTION 3
SAMPLE CONTROL, FIELD RECORDS, AND DOCUMENT CONTROL
SECTION OBJECTIVES:
• Present standard procedures for sample identification.
• Present standard procedures for sample control.
• Present standard procedures for chain-of-custody.
• Present standard procedures for maintenance of field records and document control
3.1 Introduction
All sample identification, cham-of-custody records, receipt for sample forms, and field records
should be recorded with waterproof, non-erasable ink. If errors are made in any of these documents,
corrections should be made by crossing a single line through the error and entering the correct information
All corrections should be initialed and dated If possible, all corrections should be made by the individual
making the error
If information is entered onto sample tags, logbooks, or sample containers using stick-on labels,
the labels should not be capable of being removed without leaving obvious indications of the attempt
Labels should never be placed over previously recorded information. Corrections to information recorded
on stick-on labels should be made as stated above.
Following are definitions of terms used in this section:
Project Leader- The individual with overall responsibility for conducting a specific field
investigation in accordance with this SOP
Field Sample Custodian- Individual responsible for maintaining custody of the samples and
completing the sample tags, Chain-of-Custody Record, and Receipt for
Sample form
Sample Team Leader An individual designated by the project leader to be present during and
responsible for all activities related to the collection of samples by a
specific sampling team.
Sampler The individual responsible for the actual collection of a sample
Transferee Any individual who receives custody of samples subsequent to release by
the field sample custodian.
Laboratory Sample Custodian. Individual or their designee(s) responsible for accepting custody of
samples from the field sample custodian or a transferee.
EISOPQAM 3-1 May 1996
-------
One individual may fulfill more than one of the roles described above while in the field.
EISOPQAM 3-2 May 1996
-------
3.2 Sample and Evidence Identification
PERFORMANCE OBJECTIVES:
• To accurately identify samples and evidence collected.
• To adequately insure that cham-of-custody was maintained.
3.2 1 Sample Identification
The method of sample identification used depends on the type of sample collected Samples
collected for specific field analyses or measurement data are recorded directly in bound field logbooks or
recorded directly on the Cham-of-Custody Record, with identifying information, while in the custody of
the samplers Examples include pH, temperature, and conductivity. Samples collected for laboratory
analyses are identified by using standard sample tags (Figure 3-1) which are attached to the sample
containers In some cases, pamcularly'with biological samples, the sample tags may have to be included
with or wrapped around the samples. The sample tags are sequentially numbered and are accountable
documents after they are completed and attached to a sample or other physical evidence The following
information shall be included on the sample tag using waterproof, non-erasable ink
• project number;
• field identification or sample station number;
• date and time of sample collection;
• designation of the sample as a grab or composite,
• type of sample (water, wastewater, leachate, soil, sediment, etc.) and a very brief description
of the sampling location.
• the signature of either the sampler(s) or the designated sampling team leader and the field
sample custodian (if appropriate).
• whether the sample is preserved or unpreserved;
• the general types of analyses to be performed (checked on front of tag); and
• any relevant comments (such as readily detectable or identifiable odor, color, or known toxic
properties)
Samples or other physical evidence collected during criminal investigations are to be identified by
using the "criminal sample tag " This tag is similar to the standard sample tag shown in Figure 3-1, except
that it has a red border around the front and a red background on the back of the tag. If a criminal sample
tag is noi available, the white sample tag may be used and should be marked "Criminal" in bold letters on
EISOPQAM 3-3 May 19%
-------
the tag
E1SOPQAM 3-4 May 1996
-------
If a sample is split with a facility, state regulatory agency, or other party representative, the
recipient should be provided (if enough sample is available) with an equal weight or volume of sample (see
Section 2.3.6) The split sample should be clearly marked or identified with a stick-on label.
Tags for blank or duplicate samples will be marked "blank" or "duplicate," respectively This
requirement does not apply to blind-spiked or blank samples which are to be submitted for laboratory
quality control purposes. Blind-spiked or blank samples shall not be identified as such. This identifying
information shall also be recorded in the bound field logbooks and on the Chain-Of-Custody Record as
outlined in Sections 3.3 and 3 5
322 Photograph Identification
Photographs used in investigative reports or placed in the official files shall be identified on the
back of the print with the following information
• A brief, but accurate description of what the photograph shows, including the name of the
facility or site and the location
• The date and time that the photograph was taken.
• The name of the photographer
When photographs are taken, a record of each frame exposed shall be kept in the bound field
logbook along with the information required for each photograph. The film shall be developed with the
negatives supplied uncut. The field investigator shall then enter the required information on the prints,
using the photographic record from the bound field logbook, to identify each photograph For criminal
investigations, the negatives must be maintained with the bound field logbook in the project file and stored
in a secured file cabinet.
323 Identification of Physical Evidence
Physical evidence, other than samples, shall be identified by utilizing a sample tag or recording
the necessary information on the evidence When samples are collected from vessels or containers which
can be moved (drums for example), mark the vessel or container with the field identification or sample
station number for future identification, when necessary. The vessel or container may be labeled with an
indelible marker (e.g., paint stick or spray paint) The vessel or container need not be marked if it already
has a unique marking or serial number, however, these numbers shall be recorded in the bound field log-
books In addition, it is suggested that photographs of any physical evidence (markings, etc.) be taken and
the necessary information recorded in the field logbook.
Occasionally, it is necessary to obtain recorder and/or instrument charts from facility owned
analytical equipment, flow recorders, etc.. during field investigations and inspections Mark the charts and
write the following information on these charts while they are still in the instrument or recorder •
• Starting and ending time(s) and date(s) for the chart
• Take an instantaneous measurement of the media being measured by the recorder The
instantaneous measurement shall be entered at the appropriate location on the chart along with
the date and time of the measurement
• A description of the location being monitored and any other information required to interpret
EISOPQAM 3-5 May 1996
-------
the data such as type of flow device, chart units, factors, etc
EISOPQAM 3-6 May 19%
-------
All of the above information should be initialed by the field investigator. After the chart has been
removed, the field investigator shall indicate on the chart who the chart (or copy of the chart) was received
from and enter the date and time, as well as the investigator's initials.
Documents such as technical reports, laboratory reports, etc., should be marked with the field
investigator's signature, the date, the number of pages, and from whom they were received. Confidential
documents should not be accepted, except in special circumstances such as process audits, hazardous waste
sue investigations, etc.
3.3 Chain-of-Custody Procedures
PERFORMANCE OBJECTIVE:
• To maintain and document the possession of samples or other evidence from the time of
collection until they or the data derived from the samples are introduced as evidence.
3 3 1 Introduction
Cham-of-custody procedures are comprised of the following elements; 1) maintaining sample
custody and 2) documentation of samples for evidence. To document chain-of-custody, an accurate record
must be maintained to trace the possession of each sample from the moment of collection to its introduction
into evidence.
332 Sample Custody
A sample or other physical evidence is in custody if:
• it is in the actual possession of an investigator;
• it is in the view of an investigator, after being in their physical possession;
• it was in the physical possession of an investigator and then they secured it to prevent
tampering; and/or
• it is placed in a designated secure area.
333 Documentation of Chain-of-Custody
Sample Tag
A sample tag (Figure 3-1) should be completed for each sample using waterproof, non-erasable
ink as specified in Section 3.2
E1SOPQAM 3-7 May 1996
-------
Sample Seals
Samples should be sealed as soon as possible following collection utilizing the EPA custody seal
(EPA Form 7500-2(R7-75)) shown in Figure 3-2. A similar seal is used for samples collected during
criminal investigations, however, the seal is red. Though not required, red custody seal is preferred for
sealing samples collected during criminal investigations. The sample custodian should write the date and
their signature or initials on the seal. The use of custody seals may be waived if field investigators keep
the samples in their custody as defined in Section 3.3.2 from the time of collection until the samples are
delivered to the laboratory analyzing the samples
Cham-of-Cusiodv Record
The field Chain-Of-Custody Record (Figure 3-3) is used to record the custody of all samples or
other physical evidence collected and maintained by investigators. All physical evidence or sample sets
shall be accompanied by a Chain-Of-Custody Record. This Chain-Of-Custody Record documents transfer
of custody of samples from the sample custodian to another person, to the laboratory, or other
organizational elements To simplify the Cham-of-Custody Record and eliminate potential litigation
problems, as few people as possible should have custody of the samples or physical evidence during the
investigation This form shall not be used to document the collection of split samples where there is a legal
requirement to provide a receipt for samples (see Section 3.4). The Chain-Of-Custody Record also serves
as a sample logging mechanism for the laboratory sample custodian. A Cham-of-Custody Record will be
completed for all samples or physical evidence collected. A separate Chain-of-Custody Record should be
used for each final destination or laboratory utilized during the investigation.
The following information must be supplied in the indicated spaces (Figure 3-3) to complete the
field Cham-Of-Custody Record.
• The project number.
• The project name
• All samplers and sampling team leaders (if applicable) must sign in the designated signature
block
• The sampling station number, date, and time of sample collection, grab or composite sample
designation, and a brief description of the type of sample and/or the sampling location must
be included on each line One sample should be entered on each line and a sample should not
be split among multiple lines
• If multiple sampling teams are collecting samples, the sampling team leader's name should be
indicated in the "Tag No /Remarks" column.
• If the individual serving as the field sample custodian is different from the individual serving
as the project leader, the field sample custodian's name and the title of the sample custodian
(e.g . Jane Doe, Sample Custodian) should be recorded in the "Remarks" section in the top
right corner of the Chain-of-Custody Record. The Remarks section may also be used to record
airbill numbers, registered or certified mail serial numbers, or other pertinent information
EISOPQAM 3 - 8 May 1996
-------
• The total number of sample containers must be listed in the "Total Containers" column for
each sample. The number of individual containers for each analysis must also be listed There
should not be more than one sample type per sample. Required analyses should be circled or
entered in the appropriate location as indicated on the Cham-of-Custody Record
• The tag numbers for each sample and any needed remarks are to be supplied in the "Tag
No /Remarks" column.
• The sample custodian and subsequent transferee(s) should document the transfer of the samples
listed on the Cham-of-Custody Record The person who originally relinquishes custody should
be the sample custodian. Both the person relinquishing the samples and the person receiving
them must sign the form The date and time that this occurred should be documented in the
proper space on the Cham-of-Custody Record.
Usually, the last person receiving the samples or evidence should be the laboratory sample
custodian or their designee(s).
The Cham-of-Custody Record is a serialized document. Once the Record is completed, it becomes
an accountable document and must be maintained in the project file. The suitability of any other form for
cham-of-custody should be evaluated based upon its inclusion of all of the above information in a legible
format
If cham-of-custody is required for documents received during investigations, the documents should
be placed in large envelopes, and the contents should be noted on the envelope. The envelope shall be
sealed and an EPA custody seal placed on the envelope such that it cannot be opened without breaking the
seal A Cham-Of-Custody Record shall be maintained for the envelope. Any time the EPA seal is broken,
that fact shall be noted on the Chain-Of-Custody Record and a new seal affixed. The information on the
seal should include the sample custodian's signature or initials, as well as the date.
Physical evidence such as video tapes or other small items shall be placed in Zip-Loc® type bags
or envelopes and an EPA custody seal should be affixed so that they cannot be opened without breaking
the seal A Chain-Of-Custody Record shall be maintained for these items Any time the EPA seal is
broken, that fact shall be noted on the Cham-of-Custody Record and a new seal affixed The information
on the seal should include the sample field custodian's signature or initials, as well as the date
EPA custody seals can be used to maintain custody of other items when necessary by using similar
procedures as those previously outlined in this section
Samples should not be accepted from other sources unless the sample collection procedures used
are known to be acceptable, can be documented, and the sample chain-of-custody can be established. If
such samples are accepted, a standard sample tag containing all relevant information and the Cham-Of-
Custody Record shall be completed for each set of samples.
EISOPQAM 3-9 May 1996
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334 Transfer of Custody with Shipment
• Samples shall be properly packaged for shipment in accordance with the procedures outlined
in Appendix D
• All samples shall be accompanied by the Chain-Of-Custody Record. The original and one
copy of the Record will be placed in a plastic bag inside the secured shipping container if
samples are shipped When shipping samples via common carrier, the "Relinquished By" box
should be filled in; however, the "Received By" box should be left blank. The laboratory
sample custodian is responsible for receiving custody of the samples and will fill in the
"Received By" section of the Cham-of-Custody Record. One copy of the Record will be
retained by the project leader. The original Chain-of-Custody Record will be transmitted to
the project leader after the samples are accepted by the laboratory. This copy will become a
part of the project file
• If sent by mail, the package shall be registered with return receipt requested If sent by
common carrier, a Government Bill of Lading (GBL) or Air Bill should be used. Receipts
from post offices, copies of GBL's, and Air Bills shall be retained as part of the documentation
of the cham-of-custody The Air Bill number, GBL number, or registered mail serial number
shall be recorded in the remarks section of the Chain-Of-Custody Record or in another
designated area if using a form other than that shown in Figure 3-2.
3.4 Receipt for Samples Form (CERCLA/RCRA/TSCA)
3 4 1 Introduction
Section 3007 of the Resource Conservation and Recovery Act (RCRA) of 1976 and Section 104
of the Comprehensive Environmental Response, Compensation, and Liability Act (CERCLA or Superfund)
of 1980 require that a "receipt" for all facility samples collected during inspections and investigations be
given to the owner/operator of each facility before the field investigator departs the premises The Toxic
Substances Control Act (TSCA) contains similar provisions
342 Receipt for Samples Form
The Receipt for Samples form (Figure 3-4) is to be used to satisfy the receipt for samples
provisions of RCRA. CERCLA. and TSCA The form also documents that split samples were offered and
either "Received" or "Declined" by the owner/operator of the facility or site being investigated. The
following information must be supplied and entered on the Receipt for Samples form
• The project number, project name, name of facility or site, and location of the facility or site
must be entered at the top of the form in the indicated locations.
• The sampler(s) must sign the form in the indicated location. If multiple sample teams are
collecting samples, the sample team leader's name should be indicated in the "EPA Sample
Tag No.'s/Remarks" column
EISOPQAM 3.10
May 1996
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• Each sample collected from the facility or site must be documented in the sample record
portion of the form. The sample station number, date and time of sample collection, composite
or grab sample designation, whether or not split samples were collected (yes or no should be
entered under the split sample column), the tag numbers of samples collected which will be
removed from the site, a brief description of each sampling location, and the total number of
sample containers for each sample must be entered.
• The bottom of the form is used to document the site operator's acceptance or rejection of split
samples. The project leader must sign and complete the information in the "Split Samples
Transferred By" section (date and time must be entered). If split samples were not collected.
the project leader should initial and place a single line through "Split Samples Transferred By"
in this section The operator of the site must indicate whether split samples were received or
declined and sign the form The operator must give their title, telephone number, and the date
and time they signed the form. If the operator refuses to sign the form, the sampler(s) should
note this fact in the operator's signature block and initial this entry.
The Receipt for Samples form is serialized and becomes an accountable document after it is
completed A copy of the form is to be given to the facility or site owner/operator The original copy of
the form must be maintained in the project files
3.5 Field Records
PERFORMANCE OBJECTIVE:
• To accurately and completely document all field activities.
Each project should have a dedicated logbook The project leader's name, the sample team
leader's name (if appropriate), the project name and location, and the project number should be entered
on the inside of the front cover of the logbook. It is recommended that each page in the logbook be
numbered and dated. The entries should be legible and contain accurate and inclusive documentation of
an individual's project activities At the end of all entries for each day, or at the end of a particular event
if appropriate, the investigator should draw a diagonal line and initial indicating the conclusion of the entry
Since field records are the basis for later written reports, language should be objective, factual, and free
of personal feelings or other terminology which might prove inappropriate Once completed, these field
logbooks become accountable documents and must be maintained as part of the official project files. All
aspects of sample collection and handling, as well as visual observations, shall be documented in the field
logbooks. The following is a list of information that should be included in the logbook:
• sample collection equipment (where appropriate);
• field analytical equipment, and equipment utilized to make physical measurements shall be
identified;
• calculations, results, and calibration data for field sampling, field analytical, and field physical
measurement equipment.
EISOPQAM 3-11 May 1996
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• property numbers of any sampling equipment used, if available;
• sampling station identification,
• time of sample collection,
• description of the sample location,
• description of the sample,
• who collected the sample,
• how the sample was collected;
• diagrams of processes,
• maps/sketches of sampling locations; and
• weather conditions that may affect the sample (e.g., rain, extreme heat or cold, wind, etc )
3.6 Document Control
The term document control refers to the maintenance of inspection and investigation project files
All project files shall be maintained in accordance with Divisional guidelines. All documents as outlined
below shall be kept in project files. Investigators may keep copies of reports in their personal files,
however, all official and original documents relating to inspections and investigations shall be placed in
the official project files. The following documents shall be placed in the project file, if applicable:
• request memo from the program office;
• copy of the study plan.
• original Chain-Of-Custody Records and bound field logbooks;
• copy of the Receipt for Sample forms;
• records obtained during the investigation,
• complete copy of the analytical data and memorandums transmitting analytical data,
• official correspondence received by or issued by the Branch relating to the investigation
including records of telephone calls;
• photographs and negatives associated with the project;
• one copy of the final report and transminal memorandum(s); and
• relevant documents related to the original investigation/inspection or follow-up activities
related to the investigation/inspection.
Under no circumstances are any inappropriate personal observations or irrelevant information to
EISOPQAM 3-12 May 1996
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be filed in the official project files The project leader shall review the file at the conclusion of the project
to insure that it is complete
E1SOPQAM 3 • 13 May 1996
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3.7 Disposal of Samples or Other Physical Evidence
Disposal of samples or other physical evidence obtained during investigations is conducted on a
case-by-case basis Before samples which have been analyzed are disposed, laboratory personnel shall
contact the project leader or his/her supervisor in writing, requesting permission to dispose of the samples
The samples will not be disposed of until the project leader or his/her supervisor completes the appropriate
portions of the memorandum, signs, and returns the memorandum to the laboratory, specifically giving
them permission to dispose of the samples Personnel should check with the EPA Program Office
requesting the inspection or investigation before granting permission to dispose of samples or other physical
evidence The following general guidance is offered for the disposal of samples or other physical evidence
• No samples, physical evidence, or any other document associated with a criminal investiganon
shall be disposed without written permission from EPA's Criminal Investigations Division
• Internal quality assurance samples are routinely disposed after the analytical results are
reported. The laboratory does not advise the Quality Assurance Officer of the disposal of these
samples
• Samples associated with routine inspections may be disposed following approval from the
project leader
After samples are disposed, the laboratory shall send the sample tags to the Field Equipment Center
(FEC) coordinator These sample tags are accountable and must be placed and maintained in official files
at the FEC
3.8 Field Operations Records Management System (FORMS)
FORMS is a computer program designed to streamline the documentation required by ESD and/or
the Contract Laboratory Program (CLP) for sample identification and cham-of-custody Once the
appropriate information is entered into the computer. FORMS will generate stick-on labels for the sample
tags, sample containers (CLP), and field logbooks, and will generate the sample receipt and cham-of-
custody reports for the appropriate laboratory. The advantages to this system include faster processing of
samples and increased accuracy Accuracy is increased because the information is entered only once, and
consequently, consistent from the log book to the tags, bottle labels, and cham-of-custody forms
Operating instructions are available for use with the FORMS program.
EISOPQAM 3 - 14 May 1996
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FIGURE 3-1
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Remarks:
Tag No
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Lab Sample No
EISOPQAM
3-15
May 1996
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FIGURE 3-2
EPA CUSTODY SEAL
UNITED STATES
ENVIRONMENTAL PROTECTION AGENCY
OFFICIAL SAMPLE SEAL
SAMPLE No
I DATE
SIGNATURE
PRINT NAME AND TITLE (WSPECTDR ANALYSTv TECHNICIAN)
EISOPQAM
3- 16
May 1996
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m
175
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CHAIN OF CUSTODY RECORD
PROJECT NO
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1 GROUND WATER ! SLUDGE
3 POTABLE WATER I WASTE
4 WASTEWATER 9 AIR
5 LEACHAIE 10 FISH
II OTHER
STATION NO
DATE
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SAMPLERS (SIGN)
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RECEIPT FOR SAMPLES
PROJECT NO
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•US GOVERNMENT PRINTING OFFICE 1990531617(12/89)
No. 4 4609
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SECTION 4
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SECTION 4
BRANCH SAFETY PROTOCOLS
SECTION OBJECTIVE:
• Present safety protocols to ensure that all operations are conducted in a manner which
protects worker safety and meets compliance with all OSHA regulations and EPA safety
policies
4.1 Introduction
The following parts of this section define safety protocols that are to be used by Branch
investigators while conducting field operations. This section also covers the necessary training, equipment,
and experience that is needed to conduct safe environmental investigations at hazardous waste sites.
The Division safety program is jointly coordinated by the Occupational Health and Safety Designee
(OHSD), a Division Safety, Health and Environmental Manager (SHEM) coordinator; and a Branch safety
officer The OHSD appoints the SHEM to perform the following duties: 1) classify employees into safety
categories based upon the type of work they are engaged in; 2) make requests for hazardous duty status,
3) provides and tracks safety related training; 4) notifies management of safety deficiencies; and 5) reviews
project specific safety plans The employees immediate supervisor is responsible for ensuring that their
employees meet training and medical monitoring requirements. Specific projects will include a Site Safety
Officer (SSO) whose responsibility is to ensure that the site safety plan is adhered to during the course of
work Other SSO responsibilities and duties are listed in Section 4.3.1. Responsibility for the safe conduct
of sue operations is ultimately the responsibility of each individual worker.
Field investigators will not be required to panicipate in any operation which violates OSHA and
EPA regulations/guidance. The safety protocols in this section are written in accordance with those defined
by the following regulations, guidance documents, and manuals;
29 CFR Part 1910.120. Hazardous Waste Operations and Emergency Response. These OSHA
regulations govern workers at hazardous waste sites and include requirements for training,
equipment, and practices involved in handling of hazardous materials
29 CFR Part 1910.1200. Hazard Communication. These OSHA regulations govern workers
handling hazardous materials and include requirements for training, labeling, and documentation
involved in handling hazardous materials.
Occupational Safety and Health Guidance Manual for Hazard Waste Activities: This NIOSH,
OSHA, USCG, and EPA guidance manual is for those who are responsible for occupational safety
and health programs at hazardous waste sites. It assumes a basic knowledge of science and
experience in occupational safety and health. It is the product of four Agencies (NIOSH, OSHA,
USCG. and EPA) mandated by CERCLA section 301 (0 to study the problem of protecting the
safety and health of workers at hazardous waste sites.
EISOPQAM 4-1 May 1996
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Safety and Health Manual United States Environmental Protection Agency (USEPA). Region
IV. Environmental Research Laboratory fERD. Athens. Georgia. 1990: This manual covers
safety practices and rules governing activities at EPA facilities in Athens, Georgia Included in
its contents are accident reporting procedures, procedures for natural and manmade emergencies,
safety guidelines for offices and laboratories, and special rules for storage of equipment and
wastes.
Field Health and Safety Manual USEPA. Region IV. 1990: This manual covers safety involved
in all field activities performed in Region 4. It includes regional policy regarding training
requirements, medical monitoring, and personal protection
The remaining parts of this section cover hazard communication, safety protocols, training, and equipment
thai are to be used when conducting hazardous waste investigations.
4.2 Hazard Communication Procedure
4.2 1 Introduction
The purpose of this hazard communication procedure is to ensure that the hazards of all chemicals
used by the Branch are evaluated, and that information concerning their hazards are transmitted to Branch
personnel. The transmittal of information is to be accomplished by means of a comprehensive hazard
communication program which includes container labeling and other forms of warning, material safety data
sheets (MSDS), and employee training.
4.2 2 Scope
This hazard communication procedure covers activities involving the use and storage of hazardous
chemicals
42.3 Labels and Other Forms of Warnings
Personnel responsible for receiving and storage of hazardous chemicals from manufacturers and
suppliers will ensure that the containers are marked with the following information:
• Identity of the hazardous chemical(s),
• Appropriate hazard warnings, and
• Name and address of the chemical manufacturer, importer, or other responsible party
Containers of hazardous chemicals generated during field investigations will be labeled with the
following information
• Identity of the hazardous chemical(s) contained therein; and
• Appropriate hazard warnings.
Exempt from labeling requirements are any containers into which hazardous chemicals are
transferred from labeled containers, and which are intended only for use by the person who performs the
EISOPQAM 4-2 May 1996
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transfer during the same work day which the transfer is made. Labels on containers or hazardous
chemicals will not be removed or in any way defaced. Labels for containers of hazardous chemicals will
be provided by the SHEM or a designee Information on the labels will be in English Information in
other languages may be added as long as the information presented in English is in no way obscured
4.24 Material Safety Data Sheets (MSDSs)
Personnel responsible for receiving hazardous chemicals from manufacturers or suppliers will
ensure that MSDSs are obtained for each shipment received. Receipt of hazardous chemicals will be
contingent upon both the provision of MSDSs and compliance of the MSDS with requirements set forth
in OSHA's Hazardous Communication Final Rules, part (g).
The Branch Safety Officer or a designee will ensure that copies of MSDSs are posted in the
following areas
• The Field Equipment Center,
• The Air Laboratory,
• Battery Charging Shed; and
• AH field vehicles used to transport hazardous chemicals or used as mobile laboratories where
such hazardous chemicals are utilized
4 2.S The Hazardous Chemical Inventory
The Branch Safety Officer or a designee will compile a list of hazardous chemicals used or stored
within the Branch The list will include the following'
• Name used in-house for the chemical or mixture of chemicals;
• Correct chemical name for the chemical or each component of a mixture of chemicals;
• Location(s) of the chemical, and
• Location(s) of the posting of MSDSs related to the chemical or mixture of chemicals
Employee Information and Training
The Branch safety officer or a designee will insure that personnel are provided with information
and training on hazardous chemicals in their work area at the time of their initial assignment, and whenever
a new hazard is introduced into their work area.
Information provided to personnel will consist of the following
• Requirements of this Hazard Communication Procedure;
• Operations in their work area where hazardous chemicals are present; and
• Location and availability of this Hazard Communication Procedure in this SOP, the Hazardous
EISOPQAM 4-3 May 1996
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Chemical Inventory List in the Branch safety officer's office, and the locations of MSDSs . s
stated in Section 4.2.4
Training provided to personnel will consist of:
• Methods and observations that may be used to detect the presence or release of a hazardous
chemical in the work area (e g , monitoring conducted by the Branch Safety Officer or a
designee, continuous monitoring devices, visual appearance or odor of hazardous chemicals
when being released, etc.),
• The physical and health hazards of the chemicals in the work area;
• Measures such as appropriate work practices, emergency procedures, and personal protective
equipment to be used by personnel to protect themselves from these h-::ards, and specific
procedures to be implemented to protect them from exposure to hazardo . emicals, and
• The details of this Hazard Communication Procedure, including an explanation of the labeling
system and the MSDSs, and how personnel can obtain and use the appropriate hazard
information.
4.3 Safety Protocols
4 3 1 Site Safety Officer Duties
The following is a list of duties that are required for an individual designated to be a Site safety
officer (SSO) Branch safety protocols are to be administrated by the Division's Occupational Health and
Safety Designee (OHSD) and the appointed Division Safety, Health, and Environmental Manager fSHEM)
Safety protocols are to be followed by the SSO as well as each individual that is a pan of the mvc ugation
Safety during hazardous waste site investigations begins with the individual However, .; is the
•esponsibihty of the SSO to plan and coordinate the following during an investigation.
r
1 Ensure thai each member of the investigative team is up to date on their site safety mining
(i.e Annual Safety Refresher. CPR and First Aid) or has received an over-ride by the OHSD.
2. Meet with the project leader to gam knowledge of site operations and sampling strategies
3 Prepare and enforce the sue safety plan.
4 Make sure that necessary project specific safety equipment is available and operational Th.s
includes checking out air monitoring instruments to ensure that they are fully operational
charged, and calibrated, for Level B operations - checking cool vest batteries and pumps
filling and checking self contained breathing apparatus (SCBA) air tanks and/or the airline
system.
5 The SSO is also responsible for oversight of safety during the investigation This oversight
can include the following duties - safety sweep with air monitoring instruments at the
commencement of the site investigation, directing the set-up of the command post and work
zones (decontamination, exclusion, and contaminant reduction zones), and calibrating (or
verifying such) and operating air monitoring instruments during the investigation, and conduct
EISOPQAM 4-4 May 1996
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medical monitoring for heat stress throughout the operation.
EISOPQAM 4-5 May 1996
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4.3 2 Safety Equipment
Investigators will be provided with the following safety equipment as appropriate:
• rain suit
• snow suit and ski mask
• work gloves
• safety glasses (prescription if necessary)
• goggles
• hearing protection
• hard hat
• steel toe/shank safety boots (leather and rubber)
• air purifying respirator (APR)
• first aid supplies
Field investigators will be responsible for properly operating and maintaining the safety equipment
in the field Should the safety equipment malfunction or be broken, field investigators are responsible for
reporting the condition to appropriate personnel at the Field Equipment Center (FEC) upon its return The
report will include as accurate a description or account of the problem as possible.
Field investigators will not operate any equipment for which they have not received training or have
insufficient familiarity to conduct safe operations
Activities which will require a familiarization exercise for personnel prior to the actual execution of
the work include
• Confined space entry (requires a permit, see below);
• Level A, B, or C operations.
• Drilling or power augenng,
• Drum openings.
• Brush cutting with power equipment.
• Boat operations,
• Generator operations, and
• Steam cleaning.
433 OSHA Confined Space Entry
According to 29 CFR Pan 1910.146 an individual must have a permit to enter a space that meets
the following definition for a confined space Confined space means a space that is 1) large enough and
so configured thai an investigator can bodily enter and perform assigned work; 2) has limited or restricted
means for entry or exit (e.g., tanks, vessels, silos, storage bins, hoppers, vaults, or pits are spaces that may
have limited means of entry); and 3) is not designed for continuous occupancy. Field investigators shall
not enter a space if it meets this definition
EISOPQAM 4-6 May 1996
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434 Entry into Enclosed Areas
When conducting hazardous waste site investigations in areas that do not meet the definition in
OSHA 29 CFR Pan 1910.146 or that are enclosed (areas that could potentially trap explosive vapors and/or
have depleted oxygen), field investigators should monitor the atmosphere of the area to identify
immediately dangerous to life and health (IDLH) and other dangerous conditions. Examples of dangerous
conditions that may be encountered when working around enclosed areas (other than those listed in 29 CFR
Pan 1910 146) include areas that may support flammable or explosive atmospheres, oxygen-deficient
environments, and highly toxic levels of airborne contaminants. Some examples of enclosed areas that
field investigators may enter after conducting appropriate air monitoring include, building interiors (if
possible the field mvestigator(s) should attempt to ventilate the enclosed area by opening doors and
windows), trenches (less than 3 feet deep), low lying areas in tank farms, tractor trailers, sumps, and
behind barriers such as tall buildings or tanks. At a minimum, field investigators should use direct reading
instruments such as the combustible gas indicator (CGI), oxygen meter, and an organic vapor analyzer
(OVA) to monitor the atmosphere in areas that may unexpectedly trap harmful vapors or have a depleted
oxygen supply
4 3.5 Training Status Tracking System
A computer system is used for tracking the status of required safety training for all personnel
involved in hazardous waste field operations within the Division. The system tracks the following safety
training'
• Medical monitoring physical (annual renewal);
• 40-hour hazardous waste training (no required renewal),
• 8-hour refresher training (annual renewal);
• Cardio-pulmonary resuscitation (CPR) certification (annual renewal),
• First aid certification (tn-annual renewal);
• Fit testing (annual renewal):
• Fire extinguisher operation (annual renewal);
• International Air Transport Association (bi-annual renewal); and
• Hazard Communication (no required renewal).
It is the responsibility of the Branch safety officer or their designee to notify field investigators or
their supervisor when renewals of required training are due. Notification will be at least 60 days prior to
the actual renewal date. Scheduling training will be the responsibility of each individual unless otherwise
stipulated in the notification. Upon scheduling of the training, the individual will notify the Branch safety
officer of the date Upon successful completion of training, a copy of the certificate received will be sent
by the individual to the Branch safety officer for inclusion in the safety training file.
In the event that a field investigator's OSHA required training has lapsed by more than 90 days,
the individual will not be allowed to enter onto a hazardous waste site. When lapses in training required
by EPA policy occur, the individual will be allowed to enter hazardous waste sites at the discretion of the
Occupational Health and Safety Designee (OHSD). The individual and their supervisor will be notified
of the change in status. Upon successful completion of the required training, the individual and their
supervisor will be notified of their return to prior status.
EISOPQAM 4-7 May 1996
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436 Site Operations
Upon initial entry at a hazardous waste site, a site survey will be conducted In a facility that has
active working employees, the site survey may be conducted in Level D accompanied by air monitoring
At sites that do not have active working employees, the SSO must use discretion when choosing the level
of protection that will be used while conducting an initial site survey. All initial site surveys should be
conducted using appropriate air monitoring instruments that detect explosive vapors (CGI), oxygen content.
and organic vapors (OVA). The purpose of an initial site survey is to accomplish one or both of the
following objectives:
• Determine the hazards that may exist which could affect site personnel
• Verify existing information or obtain new information about the site
To accomplish the first objective, an assessment of real or potential dangers from fire, explosion.
airborne contaminants, radiation, and oxygen deficient atmospheres must be made This assessment will
be made as follows:
• Combustible Gases - The atmosphere in any location capable of containing or generating a
combustible concentration of gases will be monitored with a combustible gas meter Response
of the meter in excess of 25% of the lower explosive limit (LEL) will cause an immediate
evacuation of the site
• Oxygen Deficiency -- A location capable of containing or generating an oxygen deficiency
either by depletion or displacement will be monitored with an oxygen meter. Any reading less
than 19.5% oxygen will result in the use of self contained breathing apparatus (SCBA)
• Organic Vapors and Gases -- The atmosphere will be monitored with both a photoionization
detector (PID) and a flame icmization detector (FID). When appropriate, cyanide gas and
halogenated vapors will also be monitored Any response above background concentrations
will cause an upgrade to Level C respiratory protection. Any response above 5 ppm when
contaminants are not known, will cause an upgrade to Level B respiratory protection A
response above 200 ppm when contaminants are not known will cause an upgrade to Level A
protection.
• Inorganic Vapors and Gases -- There are only a few direct reading instruments with the
capability to detect and quantify non-specific inorganic vapors and gases PIDs have a very
limned capability in this area If specific inorganics are known or suspected of being present,
an attempt should be made to provide appropriate monitoring if possible. In the absence of
a monitoring capability always assume a worse case scenario and upgrade the level of
protection (see below) to a level that gives respiratory and skin protection that is appropriate
to a worse case assumption.
• Radiation - A radiation survey will be conducted of the site. The primary survey instrument
will be a Geiger-Mueller detector for beta/gamma radiation (see Appendix G for a discussion
of limitations). Any response above background will result in evacuation of the area
Following the initial survey, monitoring will be repeated when new areas of the site are entered,
or when operations likely to cause a release are being conducted
EISOPQAM 4-8 May 1996
-------
EISOPQAM 4-9 May 1996
-------
Levels of Personal Protection
Personal protective equipment is divided into four categories based on the degree of protection
afforded The following table compares the relative protection for each level.
Respiratory
Skin
Eye
Level A
Maximum
Maximum
Maximum
Level B
Maximum
High
High
LEVEL C
Moderate
Moderate
Moderate
LEVEL D
Minimum
Minimum
Minimum
The relationship between air monitoring results and levels of protection (LOP) is shown in the following
table
Instrument
PID/FID
PID/FID
PID/FID
PID/FID
Oxygen
CN
CN
Response
Background
Less than 5 PPM above background
5 PPM to 200 PPM
Greater than 200 PPM
Less than 19.5%
Greater than 0 PPM and less than 10 PPM
10 PPM or greater
LOP
D
C
B
A
B
B
A
NOTE Measurements from direct-reading air monitors are only one consideration for LOP decisions
If contaminants are known, protection can be achieved at a lesser LOP
EISOPQAM
4- 10
May 1996
-------
The four levels of protection (ranked from least protective Level D to most protective Level A) and a
description of the situations for which each is appropriate is as follows.
LEVEL D
REQUIRED
OPTIONAL
LEVEL D
is used when.
Long sleeved shirt, long pants or coveralls
Boots with steel toes and shank
Gloves
Rubber boots with steel toe and shank
Boot covers (disposable)
Safety glasses, goggles, or face shield (not for chemical splash protection)
Hard hat
Emergency Life Support Apparatus (ELSA)
Thermal/weather protection (coat, overalls, sweater, hat, ram gear,
vests, and heat stress monitors)
cool
The atmosphere contains no known or anticipated hazard.
Work conditions preclude splashes, immersion, or the potential for
unexpected inhalation of or contact with hazardous levels of any chemicals
EISOPQAM
4- II
May 1996
-------
LEVEL C
REQUIRED
OPTIONAL
LEVEL C
is used when.
LEVEL D (modified to require chemical resistant boots with steel toe
shank)
&
Full-face Air Purifying Respirator (APR) (NIOSH approved)
Disposable chemical-resistant overalls
Chemical resistant gloves (inner and outer)
Emergency Life Support Apparatus (ELSA) (for confined space initial
entry)
Boot covers (disposable)
Hard hat
Face shield
ELSA (for other than initial operations)
Thermal/weather protection (coat, overalls, sweater, hat, ram gear, cool
vests and heat stress monitors)
The atmospheric contaminants, liquid splashes, or other direct contact
not adversely affect or be absorbed through any exposed skin
The types of air contaminants have been identified, concentrations
measured, and an air-purifying respirator is available that can remove
contaminants
will
the
All criteria for the use of air-purifying respirators are met
NOTE Level C operations require decontamination of personnel and equipment Also, zones of
protection are required
Level C is not considered hazardous duty because adequate safety precautions have been taken
to reduce the degree of risk
EISOPQAM
4- 12
May 1996
-------
MODIFIED LEVEL C
REQUIRED
OPTIONAL
Modified
Level C
is used when-
LEVEL C (modified to include chemically resistant splash suit and triple
glove system)
Cool vests and heat stress monitors (if ambient temperature exceeds 80° F) -
see below
Splash shield
ELSA (for confined space initial entry)
Boot covers (disposable)
Hard hat
ELSA (for other than initial operations)
Cool vests and heat stress monitors are optional if ambient temperature is
80° F or less)
All requirements for atmospheric contaminants and APR use related to
normal Level C have been met.
Materials being handled require a high degree of splash or contact
protection
NOTE 1 Modified Level C operations require decontamination of personnel and equipment Also,
zones of protection are required.
Modified Level C is not normally considered hazardous because adequate safety precautions
have been taken to reduce the degree of risk to a negligible level. Modified Level C could be
considered hazardous in a situation where atmospheric contamination was not the determining
factor
NOTE 2- When wearing a chemically resistant splash suit (Level B):
• Cool vests are required when wearing an chemically resistant suit for more than 30
minutes and the temperature is 80°F to 90°F
• Cool vests are required when wearing an chemically resistant suit for more than 15
minutes and the temperature is above 90°F.
• At the discretion of the SSO, a lack of shade may result in the need for cool vests
regardless of the temperature
• Heat stress monitors are optional unless mandated by SSO.
E1SOPQAM
4-13
May 1996
-------
LEVEL B
REQUIRED
OPTIONAL
Level B
is used when
MODIFIED LEVEL C (without the requirement for splash shield, ELS A.
and APR)
Positive pressure, full-face piece self-contained breathing apparatus
(SCBA)/airime system
Boot covers (disposable)
Hard hat
ELSA
Cool vests and heat stress monitors (if ambient temperature is
80°F or less)
Splash shield
The type and concentration of atmospheric contaminants have been
identified and require the maximum level of respiratory protection, bui only
a high level of skin protection.
The atmosphere contains less than 19.5 percent oxygen.
The presence of incompletely identified vapors or gases is indicated by
direct-reading detecting equipment, but the concentrations of contaminants
are not suspected of posing a hazard through skin contact.
The work involves opening containers suspected of containing concentrated
wastes where a likelihood of an air release is possible. In this situation,
Level B is the initial protection and can be upgraded or downgraded as
more information on the nature of the wastes is gathered
NOTE 1 Level B operations require decontamination of personnel and equipment. Also, zones of
protection are required
Level B operations normally qualify as hazardous duty because the exact nature of
atmospheric/skin contact risk is not known
NOTE 2 When wearing a chemically resistant suit (Level B)
• Cool vests are required when wearing an chemically resistant suit for more than 30
minutes and the temperature is 80°F to 90°F.
• Cool vests are required when wearing an chemically resistant suit for more than 15
minutes and the temperature is above 90°F.
• At the discretion of the SSO, a lack of shade may result in the need for cool vests
regardless of the temperature
• Heat stress monitors are optional unless mandated by SSO.
EISOPQAM
4- 14
May 1996
-------
LEVEL A
REQUIRED
OPTIONAL
LEVEL A
is used when
LEVEL D (with chemical resistant rubber boots with steel toe and shank)
Totally-encapsulating chemical-protective suit
Positive pressure, full face-piece self-contained breathing apparatus
(SCBA)/airlme system
Boot covers (disposable)
Hard hat
Cool vests and heat stress monitors (if ambient temperature is 80° F or less)
The hazardous substance has been identified and requires the highest level
of protection for skin, eyes, and the respiratory system.
Measurements by direct-reading detecting equipment show concentrations
high enough to pose a hazard through skin contact
Operations are being conducted in confined, poorly ventilated areas not
normally intended for human occupation, and conditions requiring a lower
level of protection have not been determined (i.e.. Levels B. C. or D)
NOTE 1- Level A operations require decontamination of personnel and equipment Also, zones of
protection are required
Confined space operations require special training and compliance with OSHA permit-required
confined space entry procedures
Level A operations are hazardous duty due to the nature of the equipment worn, and the
inability to reduce the risks to a negligible level.
NOTE 2- When wearing a totally-encapsulated, chemical-protective suit (Level A):
• Cool vests are required when wearing a totally-encapsulated, chemical-protective suit for
more than 30 minutes and the temperature is 80° F to 90°F.
• Cool vests are required when wearing a totally-encapsulated, chemical-protective suit for
more than 15 minutes and the temperature is above 90°F.
• At the discretion of the SSO. a lack of shade may result in the need for cool vests
regardless of the temperature
• Heat stress monitors are optional unless mandated by SSO.
EISOPQAM
4- 15
May 1996
-------
Stress
Field personnel on hazardous waste sites are exposed to both psychological and physiological
stress Psychological stress is countered with adequate training and job proficiency Physiological stress
is primarily due to exposure of the worker to extremes of heat and cold.
Heat Stress
Heat stress can be the result of working during hot weather or wearing protective clothing that
inhibits natural ventilation It can occur even under moderate temperature conditions. Whenever possible,
work should be scheduled during cooler parts of the day or night. The following protocols are to be used
to counter heat stress:
Allow workers to replace lost body fluids, water will be available at the site. Liquids for
electrolyte replenishment will be available at the discretion of the SSO.
• Cool vests will be made available. Their use will be designated during modified Level C or
higher protective level operations when ambient temperatures exceed 80°F or at the discretion
of the SSO (see preceding policy)
• At the discretion of the SSO, workers' vital signs will be monitored (i e., body temperature,
blood pressure and heart rate) If deemed necessary by the site safety officer, workers will
be fitted with heat stress monitors Monitoring of vital signs will be mandatory during
modified Level C or higher level operations when ambient temperatures exceed 80°F
Adequate shade will be provided to shelter workers from direct exposure to the sun during rest
periods
• Work teams will be rotated so that an individuals time on stressful jobs is minimized
• Field personnel are encouraged to maintain their physical fitness.
• Intake of diuretics (coffee or alcohol) should be minimized prior to field work.
Cold Stress
Exposure to extreme cold can result in hypothermia. Field work during periods of low
temperatures and high winds should be conducted to minimize the possibility of hypothermia The
following protocols are to be followed
• Workers will dress as warmly as possible using the principle of layering their clothing to
maximize protection
• Gloves should be worn when handling metal equipment
• At the discretion of the SSO. work tours will be limited to minimize exposure to the cold
• Warm shelter will be made available for workers during breaks. Use of vehicles for warm
shelter is discouraged due to the possibility of carbon monoxide exposure.
The SSO will carefully observe workers for signs of hypothermia/frostbite.
EISOPQAM 4 - 16 May 1996
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E1SOPQAM 4 - 17 May 1996
-------
Sue Control
Site control serves to minimize exposure to contaminants and is accomplished by. 1) providing
site security 10 exclude unnecessary personnel; 2) limiting the number of workers and equipment on-site
to the minimum required for effective operations; 3) conducting operations to reduce personal exposure
and minimize the potential for airborne dispersion; and 4) implementing decontamination procedures
Work Zones
To control access of personnel and equipment to possible contaminants, the site will be divided into
work zones Three categories of zones and one command post are utilized. For all operations except
Level D, work zones will be designated as follows.
1 Support Zone -- Along with the command post, this is the outermost boundary of the site
Contamination of personnel and equipment in this area is unlikely.
2 Contamination Reduction Zone -- This area serves as a corridor between the exclusion zone
and the support zone All personnel and equipment passing through this corridor from the
exclusion zone to the support zone must undergo appropriate decontamination
3 Exclusion Zone - This is an area within the support zone, where actual operations are being
conducted Access to this area is limited to personnel and equipment being utilized at that
particular time. The risk of contamination in this area is high.
Decontamination
Prior to exiting a hazardous waste site, all personnel and equipment (as needed) must undergo a
thorough decontamination The purpose of this decontamination is twofold. First, it minimizes the
transportation of hazardous wastes from a site Second, it protects workers from exposure which may
occur while they are removing their protective equipment
Decontamination must be conducted in an organized, stepwise manner. If certain pieces of the
protective equipment are removed prior to the elimination of potential problems by decontamination, the
worker may suffer damage due to inhalation or skin contact with contaminants. It is therefore important
that persons doing the decontamination work know the proper procedures and the order in which to
perform them to insure that such potential personal injuries do not occur. It is also important that site
workers avoid contaminating themselves until after they have been cleared to exit the contamination
reduction zone
Decontamination procedures will generate a quantity of hazardous waste (e.g., contaminated
solvents, disposable equipment, etc.) called investigation derived waste - IDW. This material must be
handled and disposed of in accordance with Section 5.15.
EISOPQAM 4-18 May 1996
-------
Level A Decontamination Procedures
Level A operations pose a possibility of hazardous exposure to decontamination workers Due to
the nature of Level A work, personnel in the exclusion zone are likely to have contacted high
concentrations of hazardous materials which remain on their protective equipment Therefore,
decontamination workers are required to perform their duties in Level B protection Following are the
Level A decontamination procedures.
1 Immediately upon leaving the exclusion zone, site workers will place all sampling equipment at
a designated area provided at the first station. The area will be covered with disposable plastic
Sue workers will then proceed to the first decontamination wash tub where their sun, boots, and
outer gloves will be thoroughly scrubbed with the appropriate cleaning solution (usually alkaline
soap and water) Long handle brushes will be provided for use by the decontamination workers
Decontamination workers should avoid touching the site workers until after they have cleared the
rinse station.
2 Site workers' boots and outer gloves will usually be the most contaminated items. Therefore, this
step of the decontamination procedure will be accomplished by using soap and water from the
washtub/bucket and a brush which is stored in the tub/bucket. In this step, only the boots and
gloves of the site worker will be scrubbed The site workers' suits will be scrubbed using a
cleaning solution from a pump sprayer and a brush which is not allowed to contact the more
contaminated contents of the washtub/bucket.
3 After clearance from the decontamination personnel, the site worker will proceed to the rinse water
washtub/bucket At this location, the decontamination personnel will scrub the site workers' boots
and outer gloves with water from the washtub/bucket using a long handle brush. The site workers'
suits will be rinsed with water from a pump sprayer, scrubbed with a brush which has not been
allowed to contact the contaminated water in the washtub/bucket, and finally rinsed a second time
with water from a pump sprayer
4 Once cleared by the decontamination personnel, the site worker will exit the rinse tub/bucket area
and proceed to a location where the outer gloves and boot covers (if used) will be removed and
discarded. Having been decontaminated, the site worker will exit the contamination reduction
corridor and enter the support zone The support zone will be located a distance of at least 25 feet
upwind of the last station in the contamination reduction corridor.
5 Once in the support zone, the site workers may receive a fresh cylinder of air, new outer gloves,
and new boot covers and return through the contamination reduction corridor to the exclusion
zone If there is to be no immediate return to the exclusion zone, site workers will proceed to the
last station At this location, site workers will remove their boots first, and then remove the suit
Following this. SCBAs and cool vests (if used) will be removed. Each site worker will then clean
their SCBA masks with a soap and water rinse, followed by cleaning the inside of the mask with
an alcohol wipe. Finally, the site workers will remove their inner glove systems which will be
discarded.
6 Decontamination personnel for Level A operations will themselves require decontamination prior
to entering the support zone. Decontamination personnel will perform decontamination on each
other A decontamination line separate from the Level A decontamination line will be set up for
this purpose. Procedures used on this decontamination line will be those given for Level B
decontamination. Under no circumstances will decontamination personnel attempt to perform
personal decontamination in the Level A decontamination line.
E1SOPQAM 4 - 19 May 1996
-------
Level B Decontamination Procedures
Level B operations pose a limited risk of exposure to decontamination personnel Level B sue
workers often exit the exclusion zone with moderate levels of contamination on their outer gloves and
boots To a lesser extent, contamination may be present on their splash suits. To protect against exposure
to this contamination, decontamination workers will perform their functions in Level C protection
1 Upon exiting the exclusion zone, site workers will place all equipment in a designated area
provided at the first station The area will be covered with disposable plastic. Following the
equipment drop, site workers will proceed to the first decontamination washtub/bucket area where
their boots and outer gloves will be thoroughly scrubbed with the appropriate cleaning solution
(usually alkaline soap and water). Long handle brushes will be provided for use by the
decontamination workers While at the first decontamination washtub/bucket area.
decontamination workers will not attempt to scrub the site workers' suits above chest height This
procedure is to prevent the cleaning solution carrying contaminants from splashing into the open
facial area of the impermeable suit When scrubbing the impermeable suit and SCBA equipment
below chest level, decontamination workers will apply water from a pump sprayer and use long
handle brushes which have not come into contact with the water in the washtub/bucket. Following
this step, decontamination workers will clean areas of the impermeable suit and SCBA above chest
level as necessary with paper towels wetted with the cleaning solution from the pump sprayers
Immediately following this step, the decontamination workers will discard their outer gloves and
don clean ones Areas above chest level of the site workers will then be rinsed with clean water
from a pump sprayer.
2 Once cleared from the first decontamination washtub/bucket area, site workers will then step into
the rinse water washtub/bucket. At this location, decontamination workers will thoroughly scrub
the site workers' boots and gloves with water from the washtub/bucket using a long handle brush
The site worker will then be rinsed with water from a pump sprayer Following this, the
decontamination workers will thoroughly scrub site workers (below chest level only) with a long
handle brush which is not allowed to contact the contaminated water in the washtub/bucket Site
workers will be rinsed a second time with water from a pump sprayer
3 Once cleared by decontamination personnel, site workers will exit the rinse tub/bucket and proceed
to a location where the outer gloves and boot covers (if used) will be removed and discarded
Having been decontaminated, site workers will exit the contamination reduction corridor and enter
the suppon zone The support zone will be located a distance of at least 25 feet upwind of (he last
station in the contamination reduction corridor.
4 Once in the suppon zone, site workers may receive a fresh cylinder of air, new outer gloves and
boot covers then return through the contamination reduction corridor to the exclusion zone If
there is to be no immediate return to the exclusion zone, the site workers will proceed to the last
station At this location, site workers will remove their boots first, then remove their SCBA.
Following this, the impermeable sun and cool vest (if worn) will be removed Each site worker
will then clean their SCBA mask with a soap solution and water rinse, followed by cleaning the
inside of the mask with an alcohol wipe. Finally, the site workers will remove their inner gloves
and discard them
E1SOPQAM 4 - 20 May 1996
-------
Decontamination personnel for Level B operations will require a minimal amount of
decontamination before exiting the contamination reduction zone. This decontamination will
consist of a boot rinse in the rinse water washtub/bucket (not the decontamination cleaning solution
washtub/bucket), followed by removing the outer gloves and discarding them If boot covers are
worn by decontamination personnel, the boot rinse can be eliminated and the covers can simply
be removed and discarded. Decontamination workers can then enter the support zone where new
respirator cartridges, outer gloves, and boot covers can be obtained for return to the contamination
reduction corridor. If no immediate return to the corridor is anticipated, decontamination workers
can remove their respirators and clean them in a soap wash and water rinse, followed by cleaning
the inside of the mask with an alcohol wipe. Their inner gloves will then be removed and
discarded.
Level C Decontamination Procedures
Level C operations do not pose a significant risk of exposure to decontamination workers
Therefore, Level D protection is all that is required to be worn when performing decontamination
functions
1 Upon exiting the exclusion zone, site workers will place their equipment in a designated area
provided at the first decontamination station. The area will be covered with disposable plastic.
Following this, they will proceed to a decontamination cleaning solution washtub/bucket area
where decontamination personnel will scrub their boots with a long handle brush Once cleared
from the cleaning solution washtub/bucket area, the site worker will step into a water rinse
washtub/bucket. Upon leaving the water rinse tub/bucket, site workers will remove their outer
gloves and boot covers (if used) and discard them.
2 Site workers are then clear to enter the support zone where they may obtain new respirator
cartridges, outer gloves, and boot covers for return to the exclusion zone. If an immediate return
is not anticipated, site workers may remove their respirators Respirators will be washed in soap
solution and rinsed in water Following this, the inside of the respirators will be cleaned with an
alcohol wipe Finally, site workers will remove and discard their inner gloves
3 Decontamination personnel may exit the contamination reduction corridor without having to
conduct any decontamination upon themselves other than to remove and discard their gloves.
EISOPQAM 4-21 May 1996
-------
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Sue Safety Plans
Site safety plans will be developed for every hazardous waste site project conducted The plan will
use the form included in this section MSDSs will be attached for contaminants anticipated at the sue The
plan will be submitted to the Branch safety officer and the OHSD for approval.
Prior to commencing site activities, investigators will be briefed on the contents of the safety plan
The plan's emergency instructions and directions to the closest hospital will be posted in a conspicuous
location at the site command post and in each field vehicle. When there is more than one organization
involved at the site, the development of the safety plan should be coordinated among the various groups
EISOPQAM 4 - 24 May 1996
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SECTION 5
-------
SECTION 5
SAMPLING DESIGN AND QUALITY ASSURANCE PROCEDURES
SECTION OBJECTIVES:
• Define planning and quality assurance elements that must be incorporated in all sampling
operations.
• Define sampling site selections and collection procedures for individual media
• Define sampling quality assurance procedures
5.1 Introduction
This section discusses the standard practices and procedures used by Branch personnel during field
operations to ensure the collection of representative samples. Sampling activities conducted by field
investigators are conducted with the expectation that information obtained may be used for enforcement
purposes, unless specifically stated to the contrary in advance of the field investigation Therefore, correct
use of proper sampling procedures is essential Collection of representative samples depends upon
• Ensuring that the sample is representative of the material being sampled.
• The use of proper sampling, sample handling, preservation, and quality control techniques
5.2 Definitions
Sample -- part of a larger lot. usually an area, a volume, or a period of time
Representative Sample -- a sample that reflects one or more characteristics of a population
Sample Representativeness -- the degree to which a set of samples defines the characteristics of a
population, where each sample has an equal probability of yielding the same result.
Variability -- the range or "distribution" of results around the mean value obtained from samples
within a population. There are three types of variability which must be measured or otherwise
accounted for in field sampling
1 Temporal Variability
Temporal variability is the range of results due to changes in contaminant concentrations over
time An example would be the range of concentrations obtained for a given parameter in
wastewater samples collected at different times from an outfall where contaminant
concentrations vary over time
EISOPQAM 5-1 May 1996
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2 Spacial Variability
Spacial variability is the range of results due to changes in contaminant concentrations as a
function of their location. An example would be the range of concentrations obtained for a
given parameter in surface soil from a site where discreet "hot spots" are present due to localized
releases of contaminants on otherwise uncontammated soil.
3 Sample Handling Variability
Sample handling variability is the range of results due to the sample collection and handling by
the sampler This variability manifests itself as a positive bias due to errors such as unclean
sampling equipment, cross contamination, etc., or a negative bias due to improper containers
or sample preservation
Accuracy -- a measure of agreement between the true value and the measured value of a parameter
Precision ~ measure of the agreement among individual measurements of identical samples
Bias - consistent under or over-estimation of the true value due to sampling errors, sample handling
errors, or analytical errors.
Grab Sample « an individual sample collected from a single location at a specific time or period of
time. Grab samples are generally authoritative in nature.
Composite Samples -- a sample collected over a temporal or spacial range that typically consists of
a series of discrete, equal samples (or "aliquots") which are combined or "composited" Four types
of composite samples are listed below
1 Time Composite (TC) - a sample comprised of a varying number of discrete samples (aliquots)
collected at equal time intervals during the compositing period The TC sample is typically used
to sample wastewater or streams
2 Flow Proportioned Composite (FPC) - a sample collected proportional to the flow during the
compositing period by either a time-varying/constant volume (TVCV) or time-constant/varymg
volume (TCW) method The TVCV method is typically used with automatic samplers that are
paced by a (low meter The TCVV method is a manual method that individually proportions
a series of discretely collected aliquots The FPC is typically used when sampling wastewater
3 Areal Composite - sample composited from individual, equal aliquots collected on an areal or
horizontal cross-sectional basis Each aliquot is collected in an identical manner Examples
include sediment composites from quarter-point sampling of streams and soil samples from
within grids
4 Vertical Composite - a sample composited from individual, equal aliquots collected from a
vertical cross section. Each aliquot is collected in an identical manner. Examples include
vertical profiles of soil/sediment columns, lakes, and estuanes.
EISOPQAM 5-2 May 1996
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Quality Control Samples
Quality control samples are collected during field studies for vanous purposes which include the
isolation of site effects (control samples), define background conditions (background sample), evaluate
field/laboratory variability (spikes and blanks, tnp blanks, duplicate, split samples).
The definitions for specific quality control samples are listed below:
Control Sample - typically a discrete grab sample collected to isolate a source of contamination
Isolation of a source could require the collection of both an upstream sample at a location where the
medium being studied is unaffected by the site being studied, as well as a downstream control which
could be affected by contaminants contributed from the site under study.
Background Sample - a sample (usually a grab sample) collected from an area, water body, or site
similar to the one being studied, but located in an area known or thought to be free from pollutants
ofconcern
Split Sample ~ a sample which has been portioned into two or more containers from a single sample
container or sample mixing container The primary purpose of a split sample is to measure sample
handling variability.
Duplicate Sample ~ two or more samples collected from a common source. The purpose of a
duplicate sample is to estimate the variability of a given characteristic or contaminant associated
with a population
Tnp Blanks -- a sample which is prepared prior to the sampling event in the actual container and is
stored with the investigative samples throughout the sampling event. They are then packaged for
shipment with the other samples and submitted for analysis. At no time after their preparation are
trip blanks to be opened before the> reach the laboratory. Tnp blanks are used to determine if
samples were contaminated during storage and/or transportation back to the laboratory (a measure
of sample handling variability resulting in positive bias in contaminant concentration) If samples
are to be shipped, trip blanks are to be provided with each shipment but not for each cooler
Spikes - a sample with known concentrations of contaminants. Spike samples are often packaged
for shipment with other samples and sent for analysis At no time after their preparation are the
sample containers to be opened before they reach the laboratory. Spiked samples are normally sent
v* ith each shipment to contract laboratories only. Spiked samples are used to measure negative bias
due to sample handling or analytical procedures, or to assess the performance of a laboratory.
Equipment Field Blanks - a sample collected using organic-free water which has been run
over/through sample collection eouipment. These samples are used to determine if contaminants
have been introduced by contact of the sample medium with sampling equipment. Equipment field
blanks are often associated with collecting nnse blanks of equipment that has been field cleaned
E1SOPQAM 5-3 May 1996
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Pre- and Post-Preservative Blanks - a sample that is prepared in the field and used to determine if
the preservative used during field operat.ons was contaminated, thereby causing a positive bias in
the contaminant concentration On small studies, usually only a post-preservative blank is prepared
at the end of all sampling activities. On studies extending beyond one week, a pre-preservativc
blank should also be prepared prior to beginning sampling activities At the discretion of the project
leader, additional preservative blanks can be prepared at intervals throughout the field investigation
These blanks are prepared by putting orgamc/analyte-free water in the container and then preserving
the sample with the appropriate preservative.
Field Blanks ~ a sample that is prepared in the field to evaluate the potential for contamination of
a sample by site contaminants from a source not associated with the sample collected (for example
air-bome dust or organic vapors which could contaminate a soil sample). Organic-free water is
taken to the field in sealed containers or generated on-site. The water is poured into the appropriate
sample containers at pre-designated locations at the site. Field blanks should be collected in dusn
environments and/or from areas where volatile organic contamination is oresent in the atmosphere
and originating from a source other than the source being sampled
Material Blanks -- samples of sampling materials (e.g., material used to collect wipe samples, etc ).
construction materials (e g., well construction materials), or reagents (e.g., orgamc/analyte free water
generated in the field, water from local water supplies used to mix well grout, etc.) collected to
measure any positive bias from sample handling variability. Commonly collected material blanks
are listed below:
Wipe Sample Blanks -- a sample of the material used for collecting wipe samples The material
i > handled, packaged, and transported in the same manner as all other w ipe samples with the
exception that it is not exposed to actual contact with the sample medium
Grout Blanks - a sample of the material used to make seals around the annular space in
monitoring wells
Filler Pack Blanks « a sample of the material useo to create an interface around the screened
interval of a monuonng well
Construction Water Blanks -- a sample of the uater used to mix or hydrate construction
materials such as monitoring well grout.
Orpamc/Analvte Free Water Blanks - a sample collected from a field orgamc/analyte free water
generating system. The sample is normally collectec at the end of sampling activities since the
orgamc/analyte free water system is recharged prior u. use on a study. On large studies, samples
can be collected at intervals at the discretion of the project leader. The purpose of the
orgamc/analyte free water blank is to measure posifve bias from sample handling variability
due to possible localized contamination of the organ, -analyte free water generating system or
contamination introduced to the sample containers o .nng storage at the site Orgamc/analyte
free water blanks differ from field blanks in that the ample should be collected in as clean an
area as possible (a usual location for the orgamc/an.ilyte free water system) so that only the
water generating system/containers are measured.
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5.3 Sampling Design
5 3 1 Introduction
Development of a sampling design may follow the seven steps outlined in the EPA publication,
"Guidance for the Data Quality Objectives Process" (1). The Data Quality Objectives (DQOs) process is
a logical step-by-step method of identifying the study objective, defining the appropnate type of data to
collect, clarifying the decisions that will be based on the data collected, and considenng the potential
limitations with alternate sampling designs Investigations may be executed without completing the DQO
process step-by-step; however, the basic elements of the DQO process should be considered by the project
leader for each investigation.
Sampling designs are typically either non-probabilistic (directed sampling designs) or probabilistic
(random sampling designs) in nature. The sampling design ultimately must meet specific study objectives
The location and frequency of sampling (number of samples) should be clearly outlined in the sampling
design, as well as provisions for access to all areas of the site, the use of special sampling equipment, etc
Development of the sampling design in the context of DQOs and sampling optimization are discussed in the
ASTM documents "Standard Practice for Generation of Environmental Data Related to Waste Management
Activities Development of Data Quality Objectives" (2), and "Standard Guide for the Generation of
Environmental Data Related to Waste Management Activities" (3).
5 3.2 Representative Sampling
A "representative sample" is often defined as a sample that reflects one or more characteristics of
the population being sampled. For example, the characteristic which is desired to be reflected by the sample
may be the average, minimum, or maximum concentration of a constituent of concern. Ultimately a
representative sample is defined by the study objectives For instance, the objective of the study may be to
determine the maximum concentration of lead in the sludge from a surface impoundment. One sample
collected near the inlet to the impoundment may provide that information. The collection of a representative
sample may be influenced by factors such as equipment design, sampling techniques, and sample handling
533 Stratification and Heterogeneous Wastes
Environmental media, as well as waste matrices, may be stratified, i.e., different portions of the
population, which may be separated temporally or spatially, may have similar characteristics or properties
which are different from adjacent portions of the population An example would be a landfill that contains
a trench which received an industrial waste contaminated with chromium. The trench would be considered
a strata within the landfill if chromium was the contaminant of concern. A special case, "stratification by
component", is often observed with waste matrices when the constituent of interest is associated with one
component of the matrix An example would be slag contaminated with lead that is mixed with otherwise
uncontammated fire bnck Thus the lead is stratified by component, that being the slag. Stratified sampling
designs are discussed later which incorporate independent sampling of each strata, thereby reducing the
number of samples required
Some environmental and waste matrices may be, for purposes of the field investigation,
homogeneous (for instance the surface water in a limited segment of a small stream). If the composition of
the matrix and the distribution of contaminants are known, or can be estimated, less sampling may be
necessary to define the properties of interest. An estimate of the variability in contaminant distribution may
be based on knowledge, or determined by preliminary sampling. The more heterogeneous the matrix, the
greater the planning and sampling requirements.
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A population could also have very localized strata or areas of contamination that are referred to as
"hot spots" Specific procedures for hot spot identification and characterization are available in Statistical
Methods for Environmental Pollution Monitoring (4).
534 Specific Sampling Designs
Sampling strategies used by the Branch typically fall into two general groups: directed or
probabilistic Directed or "authontati ve" approaches typically rely on the judgement and experience of the
investigators, as well as available information on the matrix of concern. Probabilistic, or "statistical"
approaches may be appropriate when estimates on uncertainty and specific confidence levels in the results
are required The probabilistic approaches include: simple random sampling, stratified random sampling.
and systematic grid sampling The main feature of a probabilistic approach is that each location at the site
has an equal probability of being sampled, therefore statistical bias is minimized.
53.5 Determining the Number of Samples to Collect
The number of samples to collect as part of a sampling design will typically be based on several
factors, e.g . the study objectives, properties of the matrix, degree of confidence required, access to sampling
points, and resource constraints Practical guidance for determining the number of samples is included in
several documents including the ASTM document Standard Guide for General Planning of Waste Sampling
(5). the US-EPA document Characterization of Hazardous Waste Sites - A Methods Manual. Volume 1 - Site
Investigations (6), and Statistical Methods for Environmental Pollution Monitoring by Richard O Gilbert
(4)
5.3 6 Authoritative or Directed Sampling
Directed sampling is based on the judgement of the investigator, and does not necessarily result in
a sample thai reflects the average characteristics of the entire matrix. Directed sampling is also called
authoritative or judgmental sampling, and is considered non-probabilistic The experience of the investigator
is often the basis for sample collection, and bias (depending on the study objectives) should be recognized
as a potential problem However, preliminary or screening investigations, and certain regulatory
investigations, may correctly employ directed sampling. Directed sampling may focus on "worst case"
conditions in a matrix, for example, the most visually contaminated area or the most recently generated
waste. In the presence of high temporal or spacial variability, directed samples have a very limited degree
of representativeness.
537 Simple Random Sampling
Simple random sampling insures that each element in the population has an equal chance of being
included in the sample. This is often be the method of choice when, for purposes of the investigation, the
matrix is considered homogeneous or when the population is randomly heterogeneous. If the population
contains trends or patterns of contamination, a stratified random sampling or systematic grid sampling
strategy would be more appropriate.
538 Systematic Sampling over Time or Space
Systematic sampling over time at the point of generation is useful if the material was sampled from
a wastewater sewer, a materials conveyor belt, or being delivered via truck or pipeline. The sampling
interval would be determined on a time basis, for example every hour from a conveyor belt or pipeline
discharge, or from every third truck load. Systematic sampling over space might involve the collection of
EISOPQAM 5-6 May 1996
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samples at defined intervals from a ditch, stream, or other matrix that is spatially unique
5.3 9 Stratified Random Sampling
Stratified random sampling may be useful when distinct strata or "homogeneous sub-groups" are
identified within the population. The strata could be located in different areas of the population, or the strata
may be comprised of different layers This approach is useful when the individual strata may be considered
internally homogeneous, or at least have less internal variation, in what would otherwise be considered a
heterogeneous population. Information on the site is usually required to establish the location of individual
strata A grid may be utilized for sampling several horizontal layers if the strata are horizontally oriented
A simple random sampling approach is typically utilized for sample collection within each strata The use
of a stratified random sampling strategy may result in the collection of fewer samples.
5 3.10 Systematic Grid Sampling
Systematic grid sampling involves the collection of samples at fixed intervals when the
contamination is assumed to be randomly distributed. This method is commonly used with populations when
estimating trends or patterns of contamination. This approach may not be acceptable if the entire population
is not accessible, or if the systematic plan becomes "phased" with variations in the distribution of
contaminants within the matrix This approach may also be useful for identifying the presence of strata
within the population. The gnd and starting points should be randomly laid out over the site, yet the method
allows for rather easy location of exact sample locations within each gnd. Also, the gnd size would typically
be adjusted according to the number of samples that are required.
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5.4 General Considerations for Sampling Designs
Prior to commencing work on any project, the objective of the study in terms of the purpose the data
generated is to serve should be known Some examples of uses for which data are generated include
• RCRA waste identification investigations;
• RCRA or Superfund screening investigations (presence or absence of contaminants).
• Superfund Remedial Investigations, Removal Actions, or Feasibility Studies;
• Surface water and sediment studies.
• Wastewater treatment plant evaluations,
• Monitoring investigations,
• USTAJIC investigations; and
• Special environmental characterization investigations.
The purpose of data collection is to meet the objectives of the investigation. The process of
designing an investigation typically follows a logical series of steps. Proper evaluation of these steps will
greatly enhance the project leader's ability to choose a design which adequately serves the purpose of the
study The DQO approach may not be strictly followed, but the elements of the approach are always
considered during study planning These elements include-
• Identification of objectives, and investigation boundaries,
• Collection of information concerning historical data, site survey, and site history.
• Sampling design selection and design optimization,
• Sample types and number,
• Analytical requirements and limitations, and
• Data interpretation and assessment
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5.5 Soil Sampling Designs
The objectives of a soil sampling investigation must be clearly defined in terms of the purpose of
the data generated A discussion of study planning elements that include considerations specific to soil
investigations follows.
5 5 1 Historical Sampling Data, Site Survey, and Site History
Investigations that are used for initial site screening purposes are one of the few cases where
historical sampling data is usually not available. In this case, the purpose of the sampling effort is to
determine the presence/absence of contaminants and if present, to determine their nature. Such a purpose
can be served with a minimum of samples whose locations can be determined from a site survey and a
review of the site history. When designing a soil sampling study for purposes other than site screening, a
record of previous sampling efforts is usually available from which a relatively sound foundation of
historical sampling data can be derived
The site survey is invaluable for soil sample design. Information which should be obtained during
a sue survey includes1
• General site layout,
• Site access:
• Soil types and depths.
• Surface water drainage pathways,
• Existing site conditions,
• Visible staining of surface soil,
• Vegetation stress; and
• Possible offsite or non-site related sources
The site history should include factors such as previous land use both on and nearby the site, types
of industrial operations conducted both on the site and on adjoining property, types of contaminants to which
the site has been exposed, and locations of possible dumping/burial areas The site history can be derived
from property plats, tax records, aerial photos, and interviews with people familiar with the site
552 Data Quality Objectives (DQOs)
Consideration of the purpose which the data generated from the soil sampling effort is to serve dnves
the selection of DQOs DQO selection will then be the main factor which determines the types of samples
to be collected, the types of equipment to be used, and the analytical requirements for the samples. See
Section 5 12 for a discussion of DQOs.
553 Authoritative Designs for Soil Investigations
When the purpose of the investigation is to determine the presence of contaminants, a simple
strategy can be used. Such a purpose is normally encountered during screening inspections, criminal
investigations, and any other project where the scope is limited to gathering evidence of contamination
These cases are normally characterized by a lack of previous sampling data, thereby requiring that sample
types and locations be determined by site history and a site survey In these instances, an authoritative
design is normally used
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Authoritative sampling usually involves a limited number of locations (10 to 15) from which grab
samples are collected Locations are selected where there is a good probability of finding high levels of
contamination. Examples may include areas where significant releases or spillage occurred according to the
site history or areas of visible staining, stressed vegetation, or surface drainage are noted in the site survey
An authoritative design usually involves the selection of two or three control sampling locations to measure
possible contaminants migrating onto the site from adjacent sources not involved in the study The selection
of control locations is similar to the selection of other sampling locations, except that upstream or upgradient
control samples are expected to be unaffected by site contaminants.
Because of the biased nature of an authoritative design, the degree of representativeness is difficult
to estimate Authoritative samples are not intended to reflect the average characteristics of the site Since
determining representativeness is not an issue with this type of design, duplicate samples designed to
estimate variability are not normally collected. However, split samples should be collected to measure
sample handling variability
An interactive approach may be used in an authoritative design to determine the extent of
contamination on a site when the source can be identified Samples are typically collected using a pattern
that radiates outward from the source The direction of contaminant migration may not be known which will
result in the collection of more samples, and in this case field screening would be desirable to help in
determining appropriate sampling locations.
554 Systematic Grid Sampling Designs for Soil Investigations
In cases where both the presence of contaminants and the extent of contamination needs to be
determined, an authoritative design is inappropriate as site variability cannot be estimated without collecting
an inordinate number of samples A systematic design is normally used during investigations when
determining the extent of contamination, such as remedial investigations and removal actions
Once a site has reached the stage where the extent of contamination becomes an issue, access to data
from previous sampling efforts (screening investigations) which used an authoritative design is normally
available The preliminary data can be used to estimate the variability of contaminant concentrations as a
function of area and/or depth for purposes of planning the more extensive systematic design In the absence
of previous sampling data a variability study should be conducted. An alternative would be to estimate the
\anabiliry. with confirmation of the estimate being made during the more extensive systematic study If a
\ariability study is to be conducted, it will be limited in scope and will use certain default values or
assumpuons to determine the number of samples to collect for determining site variability The methods
used for variability studies are included in the following discussion of systematic sampling strategies
Determination of the Number of Samples to Collect
When designing a systematic grid sampling investigation, the number of samples to be collected
must be determined first. This can be calculated based on variability information derived from previous
sampling data Upon review of the historical data, a contaminant or contaminants of concern (COCs) can
be selected COCs are parameters which are closest to or in excess of an action level Their presence is
normally the driving force behind the need to determine the extent of contamination.
EISOPQAM 5 - 10 May 1996
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The following steps are to be followed to determine the number of samples to collect (6)
1 Select a margin of error (p) acceptable for the subsequent use of the data. For soil studies, a margin
of error of 0.20 is not unusual The margin of error may be obtained by dividing the precision
wanted (in units of concentration; e.g. ±10 ppm, etc.) by the known or anticipated mean
concentration of the COCs Note that changes in the precision or mean concentration for the COC
relative to those anticipated during the planning process may require a re-evaluation of the assumed
margin of error
2 A coefficient of variation (CV), which is defined as the standard deviation of a COC divided by the
mean of the COC, is either obtained using previous sampling data, or estimated based on anticipated
variability If a CV above 0.65 is obtained, a large number of samples will usually result
The number of samples required may be minimized by using a stratified design if areas with known
high variability can be identified and addressed separately from areas of lower variability. Areas
of high variability will require more samples while areas of low variability will require fewer using
the approach outlined in this section. The overall effect will normally be a substantially lower
number of samples for the entire site
3 A confidence level (ta) needs to be established. For work involving hazardous wastes, a confidence
level of 95% should be used For a 95% confidence level, a factor of 1.96 (from standard statistical
tables) is used to calculate the number of samples required.
4 The required number of samples is calculated using the following formula
n= Ja:(CV):
P2
Where.
n = number of samples to collect
tB = statistical factor for a 95% confidence level
CV = coefficient of variation
p = margin or error
In a case where no previous sampling data is available, the default values given in the previous
discussion can be used
n= M.96W0.6SV'
(0.20):
n = 40 samples
Upon completion of the soil sampling effort, the data obtained for the COCs is reviewed It can then
be determined if an adequate number of samples were collected with respect to the margin of error and
confidence selected during the planning process This determination is completed by calculating the CV
using the data obtained during the study The standard deviation of the concentration for a COC is divided
by the mean concentration and the CV is calculated This CV may be higher or lower than the CV selected
during the planning process Using this CV value, the same equation is used to determine the required
number of samples based on the actual CV for the study If this second value for "n" is less than or equal
to the number of samples collected during the study, then the site has been characterized for the extent of
EISOPQAM 5-11 May 1996
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COCs within the limits of confidence and error stated. If the second value for "n" is significantly greater
then additional sampling is necessary, or an adjustment to the margin of error or confidence level should be
considered. If the collection of additional samples is deemed necessary by the investigation team, the data
that has been generated may be used to plan for a more efficient and cost-effective re-sampling of the site
Areas of the site where higher than anticipated variabilities were obtained may be segregated from areas of
lower variability (stratified design) A recalculation of the number of samples required to characterize each
strata should then be completed and resampling may proceed.
The following table illustrates the number of samples required at a 95% confidence level with
varying margins of error (p) and coefficients of variation (CV):
Margin of Error (p)
0 1
0.2
0.3
0.5
1 0
20
Coefficient of Variation (CV)
0.1
4
1
-
-
-
-
0.5
96
24
10
4
1
-
0.65
162
40
18
6
2
-
1.0
384
96
42
15
4
1
20
1537
384
170
61
15
4
Number of Samples (n)
Note that as the CV increases at a set margin of error, the number of samples required increases
When the variability is low (as measured by the standard deviation or the square root of the variance) relative
to the mean of the data, then the CV is low However, as the variability in the population begins to increase
relative to the mean of the data, then the CV increases and the number of samples required increases if
characterization of the sue at a 95% confidence level and a set margin of error is desired.
A similar relationship is observed for the margin of error. When the precision required (say + 10
ppm lead) is high relative to the mean of the data (say 100 ppm lead), then the margin of error is low (in this
case 0 1) In this case 162 samples would be required with a CV of 0.65. If the investigators could accept
a higher margin of error (e.g.. ± 20%). and the mean concentration of the data is still 100 ppm lead, then the
resulting margin of error (0.2) would result m a lower number of required samples. Note that 40 samples
would be required at the same CV of 0 65.
If the investigators change the confidence level, then the numbers in the table provided would change
accordingly If the confidence level is decreased to 80%, then the required number of samples reflected in
this table would be lower for each margin of error and CV combination
EISOPQAM
5- 12
May 1996
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Establishment of the Grid
Having determined the number of samples to collect, the project leader should then determine ho\\
to disperse the samples within the site. Commonly, a grid system is used. The number of grids is equal to
the number of samples required for a systematic gnd design. Grids may also be used to determine sampling
locations when using a random design, however, with this type of design every gnd is not sampled.
The size of the grids is calculated by dividing the area of the site by the number of samples required
The product of this calculation is the area of each gnd. By taking the square root of the gnd area, the length
of a grid side is determined.
G = (a/n)1'3
Where-
G = length per side of each individual grid
a = area
n = number of samples required
The length of a gnd size should be "rounded" down to some number convenient for the method used
in laying out the gnd (e.g., plane survey, geographical positioning system (GPS), etc.). Rounding down the
grid size will increase the number of samples slightly. It is important to remember that the number of
samples calculated is the minimum, and that site conditions may not allow for collection of all samples
Therefore, additional samples would be appropnate.
Grab vs Composite Samples
When designing a systematic gnd sampling investigation, a determination of whether to collect grab
or composite samples must be made Grab samples may not adequately describe variability, even within
individual gnd cells, and therefore, limit the representativeness of the data set. If the study involves a small
area with gnd cells of 25 feet or less in length, then grab samples could be collected in each gnd cell without
sijrmficantly affecting the representativeness of the data However, most studies have much larger gnds (100
10 500 feet per side) In these cases, composite samples collected within each grid cell result in more
representative data It should be remembered that a composite sample under the best of conditions will yield
an average value of contaminants within the gnd Composite samples are most appropriate where a
reasonable degree of vanabihty is anticipated, and where soil types are amenable to adequate mixing This
is normally the case when contaminants have been distributed by airborne deposition (relatively
homogeneous distribution across the site) Where localized "hot spots" are present due to releases from
process units, indiscriminate dumping, or the burying of wastes, a more specialized approach that takes these
r>pes of distribution into account is required Situations where the distnbution of contaminants is strongly
non-random (heterogeneous distnbutions) are the most difficult to plan for and charactenze.
Composite samples should consist of five to nine aliquots per sample located on compass points
within the gnd cell. Greater than nine aliquots per sample can result in dilution of fairly high concentrations
down to a value below the analytical detection limits. Less than 5 aliquots may limit the representativeness
of the sample with no added value over a single grab sample within the gnd cell. A certain number of
samples are collected (10 percent of the grid cells is often selected) dunng the investigation for variability
determinations based on rotating the aliquot distnbution pattern on the points of the compass within the grid
cell
Surface vs Sub-Surface Samples
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The two mam considerations for sub-surface soil samples are contaminant mobility and type of
deposition A contaminant that is relatively immobile in soil will naturally be found in the same area in
which it was deposited. Mobile contaminants require specialized consideration of the likely extent of their
migration in order to determine sub-surface soil sampling locations and depths. Airborne deposition of
mobile contaminants normally require a considerable amount of sub-surface soil sampling to determine their
extent in a systematic design.
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5.6 Ground Water Sampling Designs
Sampling design, as it pertains to ground water, often involves the use of some form of temporar>
well point or direct push technology (DPT) for rapid in-field screening and plume delineation These
techniques are discussed in Section 6 Samples obtained using these techniques are usually analyzed
immediately, using an on-site field laboratory, or are sent to an off-site laboratory for quick turnaround
analyses. In this manner, delineations of both a horizontal (areal) and vertical nature can be rapidly achieved
in the field These delineations can then be used as the basis for locating and installing permanent ground
water monitoring wells.
The degree of complexity for these delineations varies, depending on a number of factors which
include
• The known or anticipated size of the suspected source area.
• Site stratigraphy
• The amount of information regarding hydrogeological conditions (thickness of aquifers or
water-bearing units, depth to confining units, ground water flow direction, etc )
• The type of contamination (aqueous phase, light non-aqueous phase liquid (LNAPL), or dense
non-aqueous phase liquid (DNAPL))
In addition to the design considerations imposed by the preceding factors, screening program designs
may be either simple iterative or grid-based Grid-based may even transform, at some point, to a more or
less iterative program
5 6 1 Single Source Iterative Programs
The simplest case is one in which there is a small source area of an aqueous phase contaminant or
component, such as benzene, toluene, ethyl benzene, and xylene (BTEX) contamination without associated
product, and there is a high degree of confidence with respect to ground water flow direction In this
situation, a sample location would be placed in the middle of the source area, for source area
characterization, and several locations would be established downgradient. It is not possible to specify the
numbers and locations for these sampling points Three points would typically be the minimum number, one
located immediately downgradient of the source area and two located to either side of the center line If
contaminants were detected in any of the downpraaient locations, additional locations would need to be
established downgradient and/or side-gradient of those locations to complete boundary delineation This
process would continue until both the downgradient and lateral extent of the contamination were established
As indicated, the numbers and locations of these sampling locations are subject to site scale and
other factors and can only be determined in the field using best judgement. At this point, some attention
should be given to vertical characterization of the contaminants Additional samples should be collected at
locations below the depths at which the contaminants were identified until the vertical extent is determined
If this is not accomplished during screening acmities, it must be done during subsequent investigations with
permanent monitoring wells
Single-source light non-aqueous phase liquids (LNAPL) problems are generally no more
complicated than the non-aqueous phase delineation problems If there are no senous vertical profiling
problems, however, the sampling device should be capable of identifying the presence of and determining
the thicknesses of the floating LNAPL layers
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A more complex situation would be a single source area in which there is a dense non-aqueous pha>e
liquid (DNAPL) product layer with associated aqueous phase contamination The initial pan of the
investigation would be conducted m a manner similar to the simplest case. After delineation of the aqueou^
phase plume, additional characterization would be required for the DNAPL component. If a confining layer
is present and the depth to the surface of this layer is known, sample* should be collected from the boundar>
between the water-bearing formation and the confining unit to determine if DNAPL products are present
Wherever DNAPLs are found, additional samples must be collected. The rationale for sample location
selection depends on both sub-surface structure and ground water flov direction. DNAPL constituents may
flow down-dip on the surface of confining units, in directions that are totally contrary to ground water flow
directions No attempt at DNAPL characterization should be made until the site geology (stratigraphy.
structure and ground water flow patterns) are known.
562 Multiple-Source Area Gnded Programs
Some ground water screening nvestigations involve identifying multiple source areas and
determining the size and shape (delineation) of the associated plumes over relatively large areas In these
cases, it may be appropriate to pre-determme and establish a gnd pattern to direct the collection of ground
water samples As the apparent contaminant pattern begins to develop, it may be appropriate to disregard
established but unsampled sampling location-, and concentrate on other areas within the gnd pattern It ma\
even be appropriate to expand the area of investigation by establishing additional sampling locations These
locations may be determined by using a gnd c- may be located using best judgement, in an iterative manner
Considerations regarding non-aqueous phases must be observed here as well. If aqueous phase
sample analysis indicates that DNAPL constiuents may be present, sampling should be conducted at the
surface of the confining unit to determine if pn duct layers are present
563 Typical Ground Water Screening Devices
Listed below are numerous tools, device.- and techniques available to field investigators that can
be used to effectively collect ground water samples for rapid field screening and plume delineation
• Temporary wells -- Well casing can be nstalled temporanlj either inside hollow-stem augers
or in an open hole after removal of holli-w- or solid-stem augers. Because of the potential for
cross-communication between vertical in ervals, this technique is appropnate only for screening
the upper portion of the saturated zone Camples are pumped or bailed directly from the well
casing Because turbidity is likely to be . problem using this technique, care should be taken
\\hen using the samples for metals screening Depth of the investigation is limited only by the
capability of the drill rig and cross-con.animation considerations See section 6 10 for
temporary well installation procedures
• Geoprobe® -- Slotted steel pipe is hydrau.'cally pushed • hammer dnven to the desired
sampling depth. Samples are usually acquired with a pensu. tic pump. The device is subject
to cross-communication at threaded rod jomr. It requires -ome knowledge of the saturated
interval The Geoprobe® is most useful at deptns less than 30 to 40 feet below ground surface
EISOPQAM 5-16
May 1996
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Hydropunch® ~ A larger, more versatile device, similar to the Geoprobe®. which is pushed to
sampling depths with a drill rig It requires some knowledge of saturated intervals to use
successfully. Depths of investigation with this technology are roughly correlated to the
capability of the drill rig used to push the sampling device.
Hydrocone® - This is a pressure-sealed sampling device that is hydraulically pushed to the
desired sampling depth It is capable of collecting a discrete sample from any depth at which
it can be pushed. A limited volume of about 700 ml is collected and is generally turbid This
technique is mainly applicable for the screening for volatile organic compounds. A temporary
well point can be driven by the same drill ng to collect samples with greater volume
requirements Samples from depths exceeding 100 feet have been obtained with this device
Routine depths obtained without special anchoring are generally within the 50-foot range, but
are dependent on the geological materials being encountered.
EISOPQAM 5 - 17 May 1996
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5.7 Surface Water and Sediment Sampling Designs
5 7 1 Sampling Site Selection
The following factors should be considered in the selection of surface water and sedimeni sampling
locations1
• Study objectives,
• Water use,
• Point source discharges,
• Nonpomt source discharges,
• Tributary locations,
• Changes in stream characteristics;
• Type of stream bed,
• Depth of stream,
• Turbulence;
• Presence of structures (weirs, dams, etc.);
• Accessibility; and
• Tidal effect (estuanne)
If the study objective is to investigate a specific water use such as a source of water supply,
recreation, or other discrete use, then considerations such as accessibility, flow, velocity, physical
characteristics, etc.. are not critical from a water quality investigation standpoint
If the objective of a water quality study is to determine patterns of pollution, provide data for
mathematical modeling purposes, conduct assimilative capacity studies, etc., where more than a small area
or short stream reach is to be investigated, then several factors become interrelated and need to be considered
in sampling location selection An excellent guide to conducting surface water stream studies is F W
Kittrells. "A Practical Guide to Water Quality Studies" (7).
Before any sampling is conducted, an initial reconnaissance should be made to locate suitable
sampling locations Bridges and piers are normally good choices as sites since they provide ready access
and permit water sampling at any point across the width of the water body. However, these structures may
alter the nature of water flow and thus influence sediment deposition or scouring. Additionally, bridges and
piers are noi always located in desirable locations with reference to waste sources, tributaries, etc. Wading
for water samples in lakes, ponds, and slow-moving rivers and streams must be done with caution since
bottom deposits are easily disturbed, thereby resulting in increased sediments in the overlying water column
On the other hand, wadeable areas may be best for sediment sampling In slow-moving or deep water, a boat
is usually required for sampling Sampling station locations can be chosen without regard to other means
of access if the stream is navigable by boat, especially in estuanne systems where boats frequently provide
the only access to critical sampling locations
Fresh water environments are commonly separated into two types:
• Flowing water, including rivers, creeks, and small to intermittent streams; and
• Water that is contained, with restricted flow including lakes, ponds, and manmade
impoundments
Since these waterways differ considerably in general characteristics, site selection must be adapted
to each Estuanne environments are a special case and are discussed separately.
EISOPQAM 5 - 18 May 1996
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E1SOPQAM 5 - 19 May 1996
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572 Rivers, Streams, and Creeks
In the selection of a surface water sampling site in nvers, streams, or creeks, areas thai exhibit ihe
greatest degree of cross-sectional homogeneity should be located When available, previously collected daia
may indicate if potential sampling locations are well mixed or vertically or horizontally stratified Smci-
mixing is principally governed by turbulence and water velocity, the selection of a site immediate 1>
downstream of a riffle area will insure good vertical mixing These locations are also likely areas for
deposition of sediments since the greatest deposition occurs where stream velocities decrease provided that
the distance is far enough downstream from the riffle area for the water to become quiescent Horizontal
(cross-channel) mixing occurs in constrictions in the channel, but because of velocity increases, the stream
bottom may be scoured, and therefore, a constriction is a poor location to collect sediment
Typical sediment depositional areas are located1
• Inside of river bends.
• Downstream of islands;
• Downstream of obstructions, and
• Areas of flow reversals
Sites that are located immediately upstream or downstream from the confluence of two streams or
rivers should generally be avoided since flows from two tributaries may not immediately mix. and at times
due to possible backflow can upset the depositional flow patterns.
When several locations along a stream reach are to be sampled, they should be strategically located
• At intervals based on time-of-water-travel, not distance, e.g., sampling stations may be located
about one-half day ume-of-waier-travel for the first three days downstream of a waste source
(the first six stations) and then approximately one day through the remaining distance
• At the same locations if possible, when the data collected is to be compared to a previous study
• Whenever a marked physical change occurs in the stream channel Example A stream reach
between two adjacent stations should not include both a long rapids section of swift shallow
water with a rocky bottom, and a long section of deep, slow-moving water with a muddy
bottom Stations at each end of the combined reach would yield data on certain rates of change.
such as reaeration. that would be an unrealistic average of two widely different rates. The actual
natural characteristics of the stream would be better defined by inserting a third sampling station
within the reach, between the rapids and the quiet water sections
• To isolate major discharges as well as major tributaries. Dams and weirs cause changes in
the physical characteristics of a stream They usually create quiet, deep pools in river reaches
that previously were swift and shallow Such impoundments should be bracketed with
sampling stations. When time-of-water-travel through the pools are long, stations should be
established within the impoundments
EISOPQAM 5 • 20 May 1996
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Some structures, such as dams, permit overflow and cause swirls in streams that accomplishes
significant reaeration of oxygen deficient water. In such cases, stations should be located short distances
upstream and downstream from the structures to measure the rapid, artificial increase in dissolved oxygen.
which is not representative of natural reaeration.
When major changes occur in a stream reach, an upstream station, a downstream station, and an
intermediate station should be selected Major changes may consist of
• A wastewater discharge,
• A tributary inflow,
• Non-point source discharge (farms or industrial sites); and
• A significant difference in channel characteristics.
The use of three stations is especially important when rates of change of unstable constituents are
being determined If results from one of only two stations in a subreach are in error for some unforeseen
reason, it may not be possible to judge which of the two sets of results indicate the actual rate of change
Results from at least two of three stations, on the other hand, may support each other and indicate the true
pattern of water quality in the subreach.
To determine the effects of certain discharges or tributary streams on ambient water quality, stations
should be located both upstream and downstream from the discharges. In addition to the upstream and
downstream stations bracketing a tributary, a station should be established on the tributary at a location
upstream and out of the influence of the receiving stream
Unless a stream is extremely turbulent, it is nearly impossible to measure the effect of a waste
discharge or tributary immediately downstream from the source. Inflow frequently "hugs" the stream bank
due to differences in density, temperature, and specific gravity, and consequently lateral (cross-channel)
mixing does not occur for some distance
Tributaries should be sampled as near the mouth as feasible. Frequently, the mouths of tributaries
are accessible by boat Care should be exercised to avoid collecting water samples from stratified locations
which are due to differences in density resulting from temperature, dissolved solids, or turbidity
Actual sampling locations will vary with the size of the water body and the mixing characteristics
of the stream or nver Generally, for small streams less than 20 feet wide, a sampling site should be selected
where the water is well mixed In such cases, a single grab sample taken at mid-depth at the center of the
channel is adequate to represent the entire cross-section A sediment sample could also be collected in the
same vicinity if available
For slightly larger streams, ai least one vertical composite should be collected from mid-stream
Samples should be collected just below the surface, at mid-depth, and just above the bottom. For larger
streams and rivers, at least quarter point (1/4. 1/2. and 3/4 width) composite samples should be collected.
Dissolved oxygen, pH, temperature, and conductivity should be measured from each aliquot of the vertical
composite
EISOPQAM 5-2! May 1996
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For large nvers, several locations across the channel width should be sampled Vertical composites
across the channel width should be located in a manner that is roughly proportional to flow, i.e . they should
be closer together toward mid-channel, where most of the flow is, than toward the banks, where the
proportion of total flow is less The number of vertical composites required and the number of depihs
sampled for each are usually determined in the field by the investigators This determination is based on a
reasonable balance between the following two considerations:
• The larger the number of subsamples, the more closely the composite sample will represent the
water body, and
• Subsample collection is time-consuming and expensive, and increases the chance of cross-
contamination.
In most circumstances, a number of sediment samples should be collected along a cross-section of
a nver or stream in order to adequately characterize the bed material. A common procedure is to sample at
quarter points along the cross-section. When the sampling technique or equipment requires that the samples
be extruded or transferred on site, they may be combined into a single composite sample However, samples
of dissimilar composition should not be combined but should be stored for separate analysis in the labora-
tory To insure representative samples, the preferred method is diver deployed coring tubes
573 Lakes, Ponds, and Impoundments
Lakes, ponds, and impoundments have a much greater tendency to stratify than rivers and streams
The relative lack of mixing generally requires that more samples be obtained Occasionally, an extreme
turbidity difference may occur where a highly turbid nver enters a lake. For these situations, each layer of
the vertically stratified water column needs to be considered. Since the stratification is caused by water
temperature differences, the cooler, more dense nver water is beneath the warmer lake water. A temperature
profile of the water column as well as visual observation of lake samples can often detect the different layers
which can be sampled separately
The number of water sampling stations on a lake, pond, or impoundment will vary with the objective
of the investigation as well as the size and shape of the basin In ponds and small impoundments, a single
vertical composite at the deepest point may be sufficient Dissolved oxygen, pH, and temperature are
generally measured for each vertical composite aliquot. In naturally-formed ponds, the deepest point is
usually near the center; in impoundments, the deepest point is usually near the dam
In lakes and larger impoundments, several vertical subsamples should be composited to form a single
sample These vertical sampling locations are often collected along a transect or gnd The number of
vertical subsamples and the depths at which subsamples are taken are usually at the discretion of the field
investigators In some cases, it may be of interest to collect separate composites of epilimnetic and hypo-
limnetic zones (above and below the thermoclme or depth of greatest temperature change)
In lakes with irregular shapes and with several bays and coves that are protected from the wind,
additional separate composite samples may be needed to adequately determine water quality Similarly,
additional samples should be collected where discharges, mbutanes, land use charactenstics, etc., are
suspected of influencing water quality
EISOPQAM 5 - 22 May 1996
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When collecting sediment samples in lakes, ponds, and reservoirs, the sampling sue should be
approximately at the center of the water mass This is particularly true for reservoirs that are formed by the
impoundment of rivers or streams Generally, the coarser grained sediments are deposited near the
headwaters of the reservoir, and the bed sediments near the center of the water mass will be composed of
fme-gramed materials. The shape, inflow pattern, bathymetry, and circulation must be considered when
selecting sediment sampling sites in lakes or reservoirs.
574 Estuanne Waters
Estuanne areas are zones where inland freshwaters (both surface and ground) mix with oceanic
saline waters Estuaries are generally categorized into three types, dependent upon freshwater inflow and
mixing properties
• Mixed estuary -- Characterized by an absence of vertical haloclme (gradual or no marked
increase in salinity in the water column) and a gradual increase in salinity seaward Typically
this type of estuary is found in major freshwater sheetflow areas, featuring shallow depths
• Salt wedge estuary -- Characterized by a sharp vertical increase in salinity and channelized
freshwater inflow into a deep estuary. In these estuaries, the vertical mixing forces cannot
override the density differential between fresh and saline waters. In effect, a salt wedge tapenng
inland moves horizontally, back and forth, with the tidal phase.
• Oceanic estuary -- Characterized by salinities approaching full strength oceanic waters
Seasonally, freshwater inflow is small with the preponderance of the fresh and saline water
mixing occurring near, or at. the shore line.
A reconnaissance investigation should be conducted for each estuanne study unless pnor knowledge
of the estuanne type is available The reconnaissance should focus upon the freshwater and oceanic water
dynamics with respect to the study objective. National Oceanic Atmospheric Administration (NOAA) tide
tables and United States Geological Survey (USGS) freshwater surface water flow records provide valuable
insights into the estuary hydrodynamics The basic in-situ measurement tools for reconnaissance are
• Boat.
• Recording fathometer.
• Salmometer,
• Dissolved oxygen meter, and
• Global Positioning System (GPS) equipment and charts.
These instruments coupled with the study objective or pollution source location, whether it is a point
or nonpomt source problem, provide the focus for selecting sampling locations More often than not,
preplanned sampling locations in estuanne areas are changed dunng the actual study penod Because of the
dynamics of estuanes. the initial sampling results often reveal that the study objective could be better served
by relocating, adding, or deleting sampling locations.
Water sampling in estuanne areas is normally based upon the tidal phases, with samples collected
on successive slack tides. All estuanne sampling should include vertical salinity measurements at one to
five-foot increments coupled with vertical dissolved oxygen and temperature profiles. A variety of water
sampling devices are used, but in general, the Van Dom (or similar type) horizontal sampler or peristaltic
pump are suitable.
EISOPQAM 5 - 23 May 1996
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Samples are normally collected at mid-depth in areas where the depths are less than 10 feet, unless
the salinity profile indicates the presence of a haloclme (salinity stratification). In that case, samples art-
collected from each stratum. Depending upon the study objective, when depths are greater than 10 feet.
water samples may be collected at the one-foot depth from the surface, mid-depth, and one-foot from the
bottom
Generally, estuanne investigations are two phased, with study investigations conducted during wet
and dry periods Depending upon the freshwater inflow sources, estuanne water quality dynamics cannot
normally be determined by a single season study
575 Control Stations
In order to have a basis of comparison of water quality, the collection of samples from control
stations is always necessary. A control station upstream from the waste source is as important as are stations
downgradient, and should be chosen with equal care to ensure representative results. In some situations it
is desirable to have background stations located in similar, nearby estuaries which are not impacted by the
phenomena or pollutants being investigated At times it may be desirable to locate two or three stations
downstream from the waste inflow to establish the rate at which the unstable material is changing The time-
of-water-travel between the stations should be sufficient to permit accurate measurement of the change in
the constituent under consideration
EISOPQAM 5-24 May 1996
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5.8 Waste Sampling Designs
5 8 1 Introduction
Waste sampling involves the collection of materials that are typically generated from industrial
processes, and therefore may contain elevated concentrations of hazardous constituents Waste sampling
in its broadest term is conventionally considered to be sampling of processed wastes or man-made waste
materials Because of the regulatory, safety, and analytical considerations, wastewater sampling should
be separate from waste sampling Environmental sampling is also different from waste sampling as it
involves the collection of samples from natural matrices such as soil, sediment, groundwater, surface water
and air
It is convenient to distinguish waste management units into two types due to Branch safety
protocols The first, "open units", are units where wastes are generated, stored, or disposed, and would
be open to the environment and environmental influences. Examples of open waste units are surface
impoundments and waste piles "Closed units" are waste containers/drums, tanks, or sumps where the
potential for the accumulation of toxic vapors or explosive/ignitable gases exists. While both open and
closed waste units are considered dangerous because of the potential exposure to concentrated wastes.
closed units are regarded as high hazards due to their potential to accumulate gases and vapors
582 Waste Investigation Objectives
The first step in an investigation is the identification of study objectives. Thorough planning and
researching of the waste generation/management practices is then required for the samples and associated
data to reflect the waste population characiensuc(s) of interest Prior to sampling wastes, it is extremely
important to obtain and assess all of the available information, e.g , waste generation process(es), waste
handling and storage practices, previous field screening results, existing sampling and analytical data, any
pertinent regulations, and permitting or compliance issues.
Common objectives in waste sampling investigations include:
• Determine if a material is a hazardous waste;
• Characterize a wastestream,
• Determine if a waste material has been released into the environment; or
• Characterize environmental media contaminated with hazardous waste
The most frequently used objective during RCRA Case Development/Investigation Evaluations and
Criminal Investigations involve hazardous waste determinations. For studies that are designed to determine
if a release has occurred, it is recommended that samples be collected from the source as well as both the
affected and the unaffected media
Waste matrices are frequently heterogenous in nature due to the physical characteristics of the
material (panicle size, viscosity, etc.), the distribution of hazardous constituents within the matrix, or the
manner in which the material has been managed or disposed When waste is comprised of strata that can
be separated by the sampling equipment (e.g., liquid-liquid or liquid-solid phases), it is not necessary to
collect a sample that is representative of the entire unit to make a waste determination An acceptable
objective would be to make a waste determination on a specific strata. For example, in drums containing
an oil and water mixture, a glass thief or a composite liquid waste sampler (COLFWASA) could be used
to sample only the oil or only the water phase to determine if the phase of interest contains hazardous
constituents or characteristics.
EISOPQAM 5 - 25 May 1996
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5.8.3 Considerations for Waste Sampling Designs
Waste sampling designs should consider the variability of the sample population in terms of the
characteristic of concern, the physical size and state of items present m the population, and the ability to
access all portions of the population for purposes of sampling Elements of the sampling design ma\
include the determination of the actual sampling locations and the number of samples to be collected.
decisions on the type of samples (grab or composite) to collect, and selection of the appropriate sampling
equipment While sampling locations are usually restricted to accessible portions of a sample population.
the number of samples is usually determined by preliminary information, the size of the sample population.
field screening results, and the variability of the waste. Composite samples are used to obtain average
concentrations of waste units while grab samples are utilized to delineate hot spots or to acquire data for
sample variability.
A small wastestream that has a hazardous constituent or characteristic randomly distributed
(relatively homogeneous matrix) requires fewer samples than a large wastestream that has a constituent or
characteristic of concern which is non-randomly distributed (heterogeneous matrix) For a waste that is
randomly distributed, a directed or systematic grid sampling design would be appropriate depending on
the objectives, whereas a stratified sampling or very specialize design should be employed for wastes that
are non-randomly distributed
Reviewing the available preliminary information should improve the effectiveness of any sampling
investigation If waste variability cannot be estimated after review of available information, then a
preliminary sampling and analytical effort may be necessary. A preliminary sampling investigation would
be important when the study's objective is to fully characterize a waste stream using a probabilistic or
"statistical" design.
Probabilistic sampling designs similar to the ones used to characterize a site with soil contamination
can be used to characterize large units such as waste piles or surface impoundments with random
contammani distributions Note that an authoritative design is often appropriate to demonstrate the
maximum degree of contamination in certain waste management units. Examples include the collection
of a sludge sample for inorganic analyses at the inlet to a surface impoundment, or a sample for volatile
organic compound analysis from the most recently generated material placed in a waste pile
A comprehensive probabilistic design may be required to fully characterize unusually complex
wastestreams that have a high degree of heterogeneity For some highly complex, heterogeneous wastes
where an average concentration would not be reflected by a design of reasonable scope, an authoritative
sampling design based on the sampler's experience may be the only feasible approach
No background or control samples are required when collecting highly concentrated waste samples
584 Waste Sampling Equipment
An extremely important factor in the sampling strategy will be determined by the physical
characteristics of the waste material Selecting appropriate sampling equipment can be one of the most
challenging tasks in developing a sampling design. By selecting sampling equipment that will not
discriminate against certain physical characteristics (e.g., phase, particle size, etc.), sampling bias can be
minimized during waste sampling Because wastes often stratifies due to different densities of phases.
settling of solids, or varying wastes constituents generated at different times, it also may be important to
obtain a vertical cross section of the entire unit.
EISOPQAM 5 - 26 May 1996
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Other desired features of sampling equipment that should be considered during sample design are.
the ability to access the desired sampling locations, the ability to maintain sample integrity, the reactivity
of equipment with the waste, and the ability to properly decontaminate the sampling apparatus In addition.
analytical requirements such as the sample handling and preparation to correctly analyze physical samples
need to be considered For solidified wastes, samples will often be required to undergo panicle size
reduction (PSR) prior to chemical analyses.
Sampling equipment should be selected to accommodate all of the known physical characteristics
of concern or chosen such that the effect of any sampling bias is understood. Often because of a lack of
preliminary information, varying field conditions, or waste heterogeneity, a piece of equipment selected
during the sampling design may be unsuccessful for collecting a particular waste sample and another piece
of equipment will be required as a substitute Any sampling bias or deficiencies resulting from the use of
substituted equipment should be documented and reviewed with the data.
585 Field Screening
Field screening can be very effective in waste characterization and extremely valuable in selecting
appropriate sampling locations and chemical analyses when little preliminary data exists Field
investigators routinely use observations of the physical characteristics of drum contents, air monitoring
equipment. pH meters/paper, and field flash point analyzers to confirm preliminary data or to decide on
sampling locations during waste investigations. Figure 5-1 (RCRA Waste Characterization) is a flow
diagram that depicts the process that field investigators may use to decide which waste containers to sample
and what analyses to perform on particular samples
EISOPQAM 5 - 27 May 1996
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FIGURE 5-1
RCRA WASTE CHARACTERIZATION FL~)W CHART
EISOPQAM 5 - 28 May 1996
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STOP
STOP
STOP
OL
Q
O
CM
O
CD
»TE CHARACTERJZATIOM
r
SAWIINGSTRATCGY
I low
'lOTtxcaiiHM )——& NO SAMPLE
OR NO
I >24% K3NITABLE
0001
1 BASED ON FIELD OBSERVATION
2 BASED ON KNOWLEDGE OR VOC SCAN RESULTS
TCRULE
CONSTITUENTS
I ~ >20XREG
1C SCREENING I
TC RULE CONSTITUENTS
« 20 X REG LEVEL
I VOC SCAN '
<>, VOC TCLP '
VOC SCAN
HWS DECISION
' AS8 ANALYSIS
ASD DECISION
I FIELD ANA1YSIS
TC RULE 261 2«
(INORGANICS)
(EXT & PEST)
TCRULE
CONSTITUENTS
r ; 20 X REG LEVEL
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5.9 Wastewater Sampling Designs
Introduction
Wastewater sampling studies focus primarily on collecting wastewater samples of the influent or
effluent at domestic and non-domestic facilities The sampling activities are usually conducted for National
Pollutant Discharge Elimination System (NPDES) compliance, compliance assistance, civil and criminal
investigations, and water quality studies The collection of wastewater samples is necessary in order to
obtain reliable data that can support compliance or enforcement activities. Specific sampling criteria for
the collection of wastewater samples is given in Section 9 of this SOP
The mam considerations in developing a wastewater sampling strategy are as follows
• Type of study (Compliance Sampling Inspection, Diagnostic Evaluation, etc.).
• Regulated or target pollutants in the wastewater stream to be sampled
• Selection of the projected sampling locations to satisfy the study objectives.
• Quality control criteria of the parameters to be sampled (oil and grease samples need to be
collected as grab samples, trip blanks are taken into the field for the collection of samples for
volatile organic compound analyses, etc.).
Complexity of the sampling program will vary with a number of factors Some primary factors
are as follows
• The number of sampling stations to be monitored This will be dependent on NPDES permit
requirements and the type of study (typically Toxic CSIs and DEs require a greater amount of
sampling stations than a routine CSI)
• Special handling requirements of the target pollutants (sampling equipment for trace organic
compounds require special cleaning procedures, etc.).
Laboratory conducting the analyses (use of a contract laboratory may require shipping from
the field, etc.)
• Accessibility to sampling stations
Process and operation criteria of the source generator (e.g., batch operation versus continuous
discharge)
• Coordination of participating organizations in the study (e.g., state assistance with the sample
collection).
• The length of sampling activities will dictate logistical considerations (e.g , shipment of
samples, additional supplies, etc.)
E1SOPQAM 5 . 30 May 1996
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5.10 LIST and U1C Sampling Designs
LIST and LTIC studies focus on determining the quality of the ground water in a target area
Sampling of the ground water in the target area provides the needed scientific data for regional decisions
on impacted areas. The main considerations in developing a UST or UIC sampling strategy are as
follows
• Identification of the pollutants in the ground water
• Identification of the source generator.
• Delineation of the contamination plume
Complexity of the sampling program will vary based on a number of factors Some primary
factors are as follows
• Size of the target area
• Hydrogeological conditions of the target area.
• Accessibility to potable and ground water monitoring wells.
• Process mode of the source generator responsible for the ground water contamination
Whenever possible, at least one background location (possibly more) should be selected to sample
ground water quality representative of an area that is not impacted by any source generator Background
samples should be collected prior to collection of potentially contaminated samples. Enough sampling sites
should be utilized to assure a representative sampling of ground water in the target area to adequately
characterize the extent of ground water contamination
Primary impact sampling locations, should be located downgradient of the source generator and
ai a distance near to the source generator to isolate the contributing process mode responsible for the
ground water contamination
EISOPQAM 5-31 May 1996
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5.11 Air Toxics Monitoring Designs
Ambient air monitoring strategies vary depending upon the monitoring objective However, some
elements are important for any air monitoring objective. Meteorology measurements should be taken
concurrent with any major air monitoring effort At a minimum, these measurements should include wind
speed and wind direction
At least on background sampling location (possibly more) should be selected to sample an air mass
that is representative of the area before it is impacted by any emission from the site being monitored
Background samples should be collected concurrent with the site samples. An adequate number of
sampling locations should be selected to assure representative sampling of the air mass, and provide enough
data to adequately characterize the contaminant concentrations being emitted from the site Generally, at
a site with soil contamination, sampling should be conducted at the areas of high contaminant
concentration, near the downwind fencelmes, and/or at the fencelines near any residences
Whenever possible, the sampling sites should be located in an open space and well away from any
tall buildings Attention should be given to avoiding potential local interference such as earth moving
equipment, haul roads, etc.
Sampling methods for various ambient air pollutants are given in Section 14 of this SOP
E1SOPQAM 5 - 32 May 1996
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5.12 Data Quality Objectives
PERFORMANCE OBJECTIVE:
• To ensure that a proper level of QA/QC is performed to match the analytical effort of
the study.
• To determine what practical limits are to be placed on the subsequent use of the
analytical and field data
As defined in EPA's "Data Quality Objectives Process for Superfund, Interim Final Guidance" (8),
Data Quality Objectives (DQO) are qualitative and quantitative statements derived from the outputs of each
siep of the DQO process. The DQO process offers a way to plan field investigations so that the quality
of data collected can be evaluated with respect to the data's intended use. (For a detailed discussion of the
complete DQO process, refer to the referenced guidance document.)
Depending on the study objective and DQOs, different field procedures and analytical methods may
be acceptable Data collected in the field include samples and site information. The methods by which
samples are collected may limit the uses of the subsequent analytical data. The methods by which site
information, such as physical measurements, photographs, field notes, etc., are collected, may reduce their
accuracy The manner in which sampling equipment is cleaned will also affect the DQO level of the data
Higher quality methods may be substituted for lower level work.
Field methodologies described in this SOP support the highest level of data gathering, unless stated
otherwise These are the standard methods to be used for all studies. Any deviations from these methods
must be documented in the field logbook or the approved study plan Investigators must be aware that such
deviations in the field work may reduce the DQO level of the data, with a subsequent reduction in the data
uses
Occasionally, special analytical procedures may require specialized field procedures and
equipment The lead investigator must be aware that these procedures should be specified in the approved
study plan prior to beginning the study
There are four data categories The first two are defined by Region 4; the latter two are in the "Interim
Final Guidance"
• Field Screening -- This level is characterized by the use of portable instruments which can
provide real-time data to assist in the optimization of sampling locations and health and safety
support Data can be generated regarding the presence or absence of certain contaminants at
sampling locations
• Field Analyses - This level is characterized by the use of portable analytical instruments which
can be used on site, or in a mobile laboratory stationed near a site. Depending upon the types
of contaminants, sample matrix, and personnel skills, qualitative and quantitative data can be
obtained.
E1SOPQAM 5 - 33 May 1996
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EISOPQAM 5 - 34 May 1996
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• Screening Data with Definitive Confirmation - These data are generated by rapid, less precise
methods of analysis with less rigorous sample preparation. Sample preparation steps may be
restricted to simple procedures such as dilution with a solvent, instead of elaborate
extraction/digestion and cleanup Screening data provides analyte identification and
quantification, although the quantification may be relatively imprecise. At least 10% of the
screening data should be confirmed using appropriate analytical methods and QA/QC
procedures and criteria associated with definitive data. Screening data without associated
confirmation data is not considered to be data of known quality.
Definitive Data -- These data are generated using rigorous analytical methods, such as
approved EPA reference methods Data are analyte-specific, with confirmation of analyte
identity and concentration These methods produce tangible raw data (e g., chromatograms.
spectra or digital values) in the form of paper printouts or computer-generated electronic files
Data may be generated at the site or at an off-site location, as long as the QA/QC requirements
are satisfied To be definitive, either the analytical or total measurement error must be
determined.
DQO information in field study plans should include:
• Sampling locations ~ including background and/or control samples.
• Sampling procedures -- reference to this SOP or other guidance documents.
• Sample type — surface water, ground water, soil, waste, GPS coordinates, etc
• Use of data - characterize nature and extent of contamination, accurate sample locations, etc
• Data types ~ field measurements and field analytical data level and laboratory analyses and
laboratory analytical data levels
Field QA/QC - percentage of spin and duplicate samples, trip blanks, rinse blanks, etc
EISOPQAM 5 - 35 May 1996
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5.13 Specific Sample Collection Quality Control Procedures
5 13.1 Introduction
This subsection provides guidelines for establishing quality control procedures for sampling
activities. Strict adherence to all of the standard operating procedures outlined in this subsection form the
basis for an acceptable sampling quality assurance program.
5132 Experience Requirements
There is no substitute for field experience. Therefore, all professional and paraprofessional
investigators shall have the equivalent of six months field experience before they are permitted to select
sampling sites on their own initiative This field experience shall be gained by on-the-job training using
the "buddy" system. Each new investigator should accompany an experienced employee on as many
different types of field studies as possible During this training period, the new employee will be permitted
to perform all facets of field investigations, including sampling, under the direction and supervision ol
senior investigators.
5 13.3 Traceability Requirements
All sample collection activities shall be traceable through field records to the person collecting the
sample and to the specific piece of sampling equipment (where appropriate) used to collect that sample
All maintenance and calibration records for sampling equipment (where appropriate) shall be kept so that
they are similarly traceable See Sections 3.1 through 3.6 for specific procedures to be utilized that insure
traceability
5 13 4 Cham-of-Custody
Specific cham-of-custody procedures are included in Sections 3 1 through 3 6 of this SOP These
procedures will insure that evidence collected during an investigation will withstand scrutiny during
litigation To assure that procedures are being followed, it is recommended that field investigators or their
designees audit cham-of-custody entries, tags, field notes, and any other recorded information for accuracy
5.13 5 Sampling Equipment Construction Material
Sampling equipment construction materials can affect sample analytical results Materials used
must not contaminate the sample being collected and must be easily decontaminated so that samples are not
cross-contaminated
EISOPQAM 5 - 36 May 1996
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5 13.6 Sample Preservation
Samples for some analyses must be preserved in order to maintain their integrity. Preservatives
required for routine analyses of samples collected are given in Appendix A of this SOP. All chemical
preservatives used will be supplied by the Region 4 laboratory. All samples requiring preservation should
be preserved immediately upon collection in the field. Samples that should not be preserved in the field
are
• Those collected within a hazardous waste site that are known or thought to be highly
contaminated with toxic materials which may be highly reactive. Barrel, drum, closed
container, spillage, or other source samples from hazardous waste sites are not to be preserved
with any chemical These samples may be preserved by placing the sample container on ice.
if necessary.
• Those that have extremely low or high pH or samples that may generate potentially dangerous
gases if they were preserved using the procedures given in Appendix A.
• Those for metals analyses which are shipped by air shall not be preserved with nitric acid in
excess of the amount specified in Appendix A.
All samples preserved with chemicals shall be clearly identified by indication on the sample tag
that the sample is preserved If samples normally requiring preservation were not preserved, field records
should clearly specify the reason
5137 Special Precautions for Trace Contaminant Sampling
Some contaminants can be detected in the pans per billion and/or pans per trillion range. Extreme
care must be taken to prevent cross-contamination of these samples The following precautions shall be
taken when trace contaminants are of concern
• A clean pair of new, non-powdered, disposable latex gloves will be worn each time a different
location is sampled and the gloves should be donned immediately prior to sampling The
gloves should not come into contact with the media being sampled
• Sample containers for source samples or samples suspected of containing high concentrations
of contaminants shall be placed in separate plastic bags immediately after collecting, tagging,
etc
• If possible, ambient samples and source samples should be collected by different field teams
If different field teams cannot be used, all ambient samples shall be collected first and placed
in separate ice chests or shipping containers Samples of waste or highly contaminated samples
shall never be placed in the same ice chest as environmental samples. Ice chests or shipping
containers for source samples or samples suspected to contain high concentrations of
contaminants shall be lined with new, clean, plastic bags.
• If possible, one member of the field sampling team should take all the notes, fill out tags, etc ,
while the other members collect the samples
• When sampling surface waters, the water sample should always be collected before the
sediment sample is collected.
EISOPQAM 5 - 37 May 1996
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• Sample collection activities should proceed progressively from the least suspected contaminated
area to the most suspected contaminated area.
• Investigators should use equipment constructed of Teflon*, stainless steel, or glass that has
been properly precleaned (Appendix B) for collection of samples for trace metals or organic
compounds analyses. Teflon* or glass is preferred for collecting samples where trace metals
are of concern Equipment constructed of plastic or PVC shall not be used to collect samples
for trace organic compounds analyses.
5138 Sample Handling and Mixing
After collection, all sample handling should be minimized. Investigators should use extreme care
to ensure that samples are not contaminated If samples are placed in an ice chest, investigators should
ensure thai melted ice cannot cause the sample containers to become submerged, as this may result in
sample cross-contamination Plastic bags, such as Zip-Lock* bags or similar plastic bags sealed with tape.
should be used when small sample containers (e g., VOC vials or bacterial samples) are placed in ice chests
to prevent cross-contamination
Once a sample has been collected, it may have to be transferred into separate containers for
different analyses The best way to transfer liquid samples is to continually stir the sample contents with
a clean pipette or precleaned Teflon* rod and allow the contents to be alternately siphoned into respective
sample containers using Teflon* or PVC (Tygon* type) tubing (and a siphon bulb to start the flow)
Teflon® must be used when analyses for organic compounds or trace metals are to be conducted Any
device used for stirring, or tubing used for siphoning, must be cleaned in the same manner as other
equipment (Appendix B). However, samples collected for volatile organic compound, oil and grease.
bacteria, su I fides, and phenols analyses may not be transferred using this procedure
li is extremely important that waste (when appropriate), soil and sediment samples be mixed
ihoroughly 10 ensure that the sample is as representative as possible of the sample media The most
common method of mixing is referred to as quartering The quartering procedure should be performed
as follows
1 The material in the sample pan should be divided into quarters and each quarter should be
mixed individually.
2 Two quarters should then be mixed to form halves.
3 The two halves should be mixed to form a homogenous matrix .
This procedure should be repeated several times until the sample is adequately mixed. If round bowls are
used for sample mixing, adequate mixing is achieved by stirring the material in a circular fashion,
reversing direction, and occasionally turning the material over
5139 Special Handling of Samples for Volatile Organic Compounds (VOCs) Analysis
Water samples to be analyzed for volatile organic compounds should be stored in 40-ml septum
vials with screw cap and Teflon*-silicone disk in the cap to prevent contamination of the sample by the cap
The disks should be placed in the caps (Teflon* side to be in contact with the sample) in the laboratory
prior to the beginning of the sampling program
E1SOPQAM 5 - 38 May 1996
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The vials should be completely filled to prevent volatilization, and extreme caution should be
exercised when filling a vial to avoid any turbulence which could also produce volatilization. The sample
should be carefully poured down the side of the vial to minimize turbulence. As a rule, it is best to gently
pour the lasi few drops into the vial so that surface tension holds the water in a convex meniscus The cap
is then applied and some overflow is lost, but the air space in the bottle is eliminated. After capping, turn
the bottle over and tap it to check for bubbles. If any bubbles are present, repeat the procedure with
another clean 40-ml vial. Since the VOC vials are pre-preserved, caution should be-exercised when the
vials are used as the collection device for surface water samples in order to prevent the loss of the
preservative When collecting water samples for VOCs. Three 40-ml vials containing preservative should
be filled the with sample
One 2-oz glass container with screw caps and Teflon*-silicon disks in the cap are used for the
storage of soil and sediment samples for VOC analyses. Soil and sediment samples collected for VOC
analyses should not be mixed The sample container should be filled completely so that no head space
remains in the sample containers
5 13 10 Estimating Variability
Spacial Variability
The following spacial duplicate sampling procedures should be used during the collection of
samples as a measure of variability within the area represented by the sample. Spacial duplicate grab
and/or composite samples should be collected during all major investigations and studies conducted by the
Branch A "major study" would include all investigations where more than twenty (20) samples were
collected, or those studies where the study objectives dictate that additional quality control samples be
collected No more than ten percent of all samples should be collected as spacial duplicates These
samples should be collected at the same time, using the same procedures, the same type of equipment, and
in the same types of containers as the original samples, but collected from a different location within the
area represented by the original They should also be preserved in the same manner and submitted for the
same analyses as the required samples The collection of spacial duplicate composite samples requires that
the sample aliquots be arrayed m a manner different from the original sample and spaced within the same
area of representativeness Data from spacial duplicates will be examined by the lead investigator to
determine if the samples represent the areas intended in the project work plan.
Temporal Variability
When required, temporal variability at a given sampling location will be measured by collecting
temporal duplicate samples. These samples will be collected from the same sampling location, using the
same techniques and the same type of equipment, but at a time different from the original sample The
time selected for the temporal duplicate sample will be within the same span of time for which the original
sample is designed to be representative in the project work plan. Data from temporal duplicates will be
examined by the project leader to determine if samples represent the time span intended in the project work
plan
E1SOPQAM 5 - 39 May 1996
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Sample Handling Variability
The effectiveness of sample handling techniques will be measured by collecting split and blank
samples
Split Samples
Split samples will be collected by initially collected twice as much material as normally collected
for a sample After mixing, the material will be apportioned into two sets of containers Both sets
of containers will be submitted for analyses with one set designated as an 'original sample", the
other designated as a "split sample" Data from split samples will be examined by the Quality
Assurance Officer to determine sample handling variability. On large studies (more than 20
samples), no more than 10 percent of all samples will be collected as split samples
Blank Samples
The following blank samples will be prepared by the laboratory and obtained by the project leader
prior to traveling to a sample site
1 Water Sample VOC Trip Blank -- A water sample VOC trip blank is required for every study
where water samples are collected for VOC analysis. Two sealed preserved (or unpreserved
if appropriate) 40-ml VOC vials will be transported to the field. For routine studies these
samples will be prepared by lab personnel Investigators shall request that these samples be
provided at least one week in advance of scheduled field investigations and inspections and
never (except in emergency situations) less than two days in advance of scheduled field
investigations and inspections These samples should not be picked up earlier than the morning
of departure for the scheduled inspection/investigation. These field blanks will be handled and
treated in the same manner as the water samples collected for volatile organic compounds
analysis on that particular study These samples will be clearly identified OP sample lags and
Cham-of-Custody Records as trip blanks
2 Soil Sample VOC Trip Blank -- A soil sample VOC trip blank is required for every study
where soil samples are collected for VOC analysis The preparation and pick up of this sample
will be the same as for the water sample VOC trip blank One 2-oz. soil VOC vial will be
transported to the field This field blank will be handled and treated by Branch personnel in
the same manner as the soil samples collected for volatile organic compounds analysis on that
particular study. These samples will be clearly .demified on sample tags and Cham-Of-
Custody Records as trip blanks
The following blanks are prepared in the field
1 Inorganic Sample Preservative Blanks - Metals and general inorganic sample containers filled
with analyte-free water will be transported to the fielc and preserved and submitted for the
same analyses as the other inorganic samples col lee ed These samples will be clearly
identified as preservatives blanks on sample tags and t:ie Chain-Of-Custody Record(s) At
least one preservative blank for each type of preserved sample should be collected at the end
of routine field investigations A minimum of one prese-vative blank should be prepared in
the field at the beginning and end of all major field investigations that last more than one week
EISOPQAM 5-40 May 1996
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2 Equipment Field Blanks -- When field cleaning equipment is required during a sampling
investigation, a piece of the field-cleaned equipment will be selected for collection of a rinse
blank. At least one rinse blank will be collected during each week of sampling operations
After the piece of equipment has been field cleaned and prior to its being used for sample
operations, it will be rinsed with orgamc/analyte free water. The rinse water will be collected
and submitted for analyses of all constituents for which normal samples collected with thai
piece of equipment are being analyzed
3 Orgamc/Analyte Free Water System Blanks - When using a portable organic-free water
generating system in the field, a sample of the water generated will be collected at least once
during each week of operations. The collected water sample will be submitted for analyses
of all constituents for which normal samples are being analyzed.
4 Material Blanks - When construction materials are being used on a site in such a way as to
have a potential impact on constituent concentrations in the sample, a sample of the materials
will be submitted for analyses. An example of a situation where construction blanks are
required is monitoring well construction. In this situation all materials used in well
construction should be submitted for analyses (e.g., grout, sand, tap water, etc.)
5 Automatic Sampler Blanks ~ In general, cleaning procedures outlined in Appendix B of this
SOP should be adequate to insure sample integrity. However, it is the standard practice of the
Branch to submit automatic sampler blanks for analyses when automatic samplers are used to
collect samples for organic compounds and metals analyses. Automatic sampler blanks for
other standard analyses shall be submitted at least once per quarter.
The Quality Assurance Officer will inform the project leaders and management when blank samples
are found to be unacceptably contaminated The Quality Assurance Officer will immediately initiate an
investigation to determine the cause of the problem The results of this investigation will be promptly
reported to appropriate personnel so that corrective action and/or qualifications to the data can be initiated
51312 Special Quality Control Procedures for Water Samples for Extractable Organic Compounds,
Pesticides, or Herbicides Analyses (Matrix Duplicate)
Duplicate water samples shall be submitted to the laboratory for extractable organic compounds.
pesticides, and/or herbicides analyses from at least one sampling location per project and laboratory used
These samples should be collected from a location expected to be relatively free from contamination, since
the samples will be used for laboratory quality control purposes The duplicate samples should be clearly
identified as "Duplicate Sample for Matrix Spike" on the sample tag, Chain-Of-Custody Record, in the
field logbook, and on the Contract Laboratory Program (CLP) Traffic Report Form (if appropriate). This
procedure shall be followed for all projects where water samples are collected for the indicated analyses.
51313 Special Quality Control Procedures for EPA Contract Laboratories
On a case-by-case basis, field investigators may be required to collect split samples (or duplicate
samples if appropriate) for analyses by both the Region 4 laboratory and contract laboratories The split
samples are to be submitted to the Region 4 laboratory using established procedures The contract
laboratory involved shall not be notified that samples were split, i.e., there should be no indication on
Chain-Of-Custody Records or CLP Traffic Report Forms submitted to the contract laboratories that these
samples were split with the Region 4 laboratory
EISOPQAM 5 - 41 May 1996
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5 13 14 Special Quality Control Procedures for Dioxms and Furans
All samples collected for dioxms and furans analyses are analyzed by other EPA laboratories or
through contract laboratories. The Region 4 laboratory does not conduct in-house analyses for dioxms and
furans The Region 4 laboratory should be consulted for the current quality control procedures for dioxm
and furan samples prior to the sampling event.
5.14 Internal Quality Control Procedures
5.14 1 Introduction
The focus of this subsection is on Field Equipment Center (FEC) operations involving preparation
of sampling and support equipment for field operations as well as for field data generated under the
Specific Sample Collection Quality Control Procedures discussed in Section 5.13. Quality control checks
of these operations insure that field sampling teams are provided with equipment that is suitable for
sampling use, and that field sampling is conducted using proper procedures.
5 14 2 Traceability Requirements
Records, in the form of bound notebooks, will be kept by FEC personnel documenting the dates
of operations and the person performing operations for the following:
• Orgamc/Analyte Free Water System Maintenance (Field and FEC Systems) -- Maintenance
on field systems will be performed immediately following every major study, or at least once
per calendar quarter. FEC system maintenance will be performed at least once per calendar
quarter.
• Air Monitoring Instrumentation Checkouts -- Pre-loadout checks on air monitoring
instrumentation will be recorded each time they are performed Discrepancies will be
immediately reported to the Branch Safety Officer.
• Self Contained Breathing Apparatus (SCBA) Checkouts - Pre-loadout checks on SCBAs will
be recorded when they are performed SCBA checkouts will be performed at least once per
calendar quarter in the absence of loadout requests Any discrepancies will be reported
immediately to the Branch Safety Officer
Other Equipment Maintenance -- Maintenance performed on equipment other than that listed
above will be recorded in a logbook for miscellaneous field equipment. All required repairs
will be reported to the FEC coordinator.
• Sampling Containers and Latex Gloves - A record will be kept of shipments received of
sampling containers and latex gloves. Containers and gloves will be recorded by lot numbers.
Upon receipt, the Quality Assurance (QA) Officer will be notified. Containers and gloves
within a received lot will not be used until they have been checked by the QA Officer.
All equipment cleaned and wrapped for field use will be marked with the date on which preparation
was completed Equipment will be stored in the FEC in specified areas to minimize the risk of
contamination while awaiting use.
EISOPQAM 5 - 42 May 1996
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EISOPQAM 5 - 43 May 1996
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5 14 3 Specific Quality Control Checks
At least once per calendar quarter, the QA Officer will conduct the following checks and issue a
written report on the results
1 Collect and submit for analyses samples of each lot of containers received during that quarter
Bottles from each lot will be tagged and sealed, then submitted for the following analyses
One-Gallon Amber -- metals, cyanide, extractable organics, and pesticides
8-oz. Glass -- metals, cyanide, extractable organics, and pesticides
1-Liter Polyethylene -- metals and cyanide.
Latex glove samples will be collected as rinse blanks using organic/analyte free water The
rmsate will be submitted for analyses of VOCs, metals, cyanide, extractable organics. and
pesticides A new glove will be rinsed for each parameter (e.g., one glove for VOC sample.
another glove for metals, etc ) to avoid dilution of potential contaminants on the gloves
2 Collect and submit for analyses a sample of water from the FEC organic/analyte free water
system The sample will be submitted for analyses of VOCs, metals, cyanide, extractable
organics, and pesticides
3 Collect and submit for analyses a sample of analyte-free water stored in one-gallon containers
at the FEC. The sample will be submitted for analyses of metals and cyanide
4 Collect and submit for analyses a rmsate blank of at least one piece of sampling or sample
related equipment stored at the FEC The sample will submitted for analyses of VOCs. metals.
cyanide, extractable organics. and pesticides
5 Collect the results of field quality control samples from the project leaders for the quarter
Normally, field quality control samples consist of the following
• Field split samples (not to include inter-lab splits),
• Water VOC trip blank samples.
• Soil VOC trip blank samples.
• Inorganic sample preservative blanks,
• Equipment field rinse blanks.
• Field organic/analyte free water system blanks, and
• Material blanks
The QA Officer will evaluate all data received and immediately attempt to resolve any problems
found A written report will be issued on the quality control checks during each calendar quarter. The
report will be submitted to appropriate personnel
EISOPQAM 5-44 May 1996
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5.15 Investigation Derived Waste (IDW)
5 15 1 Types of IDW
Materials which may become IDW are
• Personnel protective equipment (PPE) - This includes disposable coveralls, gloves, booties,
respirator canisters, splash suits, etc
• Disposable equipment -- This includes plastic ground and equipment covers, aluminum foil.
conduit pipe, composite liquid waste samplers (COLIWASAs), Teflon* tubing, broken or
unused sample containers, sample container boxes, tape, etc.
• Soil cuttings from drilling or hand augering.
• Drilling mud or water used for water rotary drilling.
• Ground water obtained through well development or well purging
• Cleaning fluids such as spent solvents and wash water.
• Packing and shipping materials
Table 5151 lists the rypes of IDW commonly generated during investigations, and current disposal
practices
5 15 2 Management of Non-Hazardous IDW
Disposal of non-hazardous IDW from hazardous waste sites should be addressed in the study plan.
To reduce the volume for transportation back to the FEC, it may be necessary to compact the waste into
a reusable container, such as a 55-gallon drum
If the waste is from an active facility, permission should be sought from the operator of the facility
to place the non-hazardous PPE. disposable equipment, and/or paper/cardboard wastes into the facilities'
dumpsters If necessary, these materials may be placed into municipal dumpsters, with the permission of
the owner These materials may also be taken to a nearby permitted landfill On larger studies, waste
hauling services may be obtained and a dumpster located at the study site. Non-hazardous IDW may also
be buried on site near the contamination source, with the burial location noted in the field logbook
Disposal of non-hazardous IDW such as drill cuttings, purge or development water, decon-
tamination washwater. drilling muds. etc.. should be specified in the approved study plan It is
recommended that these materials be placed into a unit with an environmental permit such as a landfill or
sanitary sewer These materials must not be placed into dumpsters. If the facility at which the study is
being conducted is active, permission should be sought to place these types of IDW into the facilities
treatment system It may be feasible to spread drill cuttings around the borehole, or if the well is
temporary, to place the cuttings back into the borehole. Cuttings, purge water, or development water may
also be placed in a pit in or near the source area Monitoring well purge or development water may also
be poured onto the ground downgradient of the monitoring well Purge water from private potable wells
which are in service may be discharged directly onto the ground surface.
EISOPQAM 5 - 45 May 1996
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The minimum requirements of this subsection are
• Liquid and soil/sediment IDW must be containerized and analyzed before disposal
• The collection, handling, and proposed disposal method must be specified in the approved
study plan
5 15 3 Management of Hazardous IDW
Disposal of hazardous or suspected hazardous IDW must be specified in the approved study plan
Hazardous IDW must be disposed as specified in US-EPA regulations. If appropriate, these wastes may
be placed back in an active facility waste treatment system. These wastes may also be disposed of in the
source area from which they originated, if doing so does not endanger human health and the environment
If on-site disposal is not feasible, and if the wastes are suspected to be hazardous, appropriate tests
must be conducted to make that determination If they are determined to be hazardous wastes, they must
be properly contained and labeled They may be stored on the site for a maximum of 90 days before they
must be manifested and shipped to a permitted treatment or disposal facility. Generation of hazardous IDW
must be anticipated, if possible, to permit arrangements for proper contamerization, labeling.
transportation, and disposal/treatment in accordance with US-EPA regulations.
The generation of hazardous IDW should be minimized to conserve Branch resources Most
routine studies should not produce any hazardous IDW, with the exception of spent solvents and possibly
purged ground water Care should be taken to keep non-hazardous materials segregated from hazardous
waste contaminated materials The volume of spent solvents produced during equipment decontamination
should be controlled by applying only the minimum amount of solvent necessary, and capturing it
separately from the washwater
At a minimum the requirements of the management of hazardous IDW are as follows
• Spent solvents must be returned to the FEC for proper disposal or recycling.
• All hazardous IDW must be containerized Proper handling and disposal should be arranged
prior to commencement of field activities.
E1SOPQAM 5 - 46 May 1996
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TABLE 5.15.1
DISPOSAL of IDW
TYPE
HAZARDOUS
NON-HAZARDOUS
PPE-Disposable
Containerize in plastic 5-gallon bucket with
tight-fitting lid Identify and leave on-site
with permission of sue operator, otherwise
return to FEC for proper disposal.
Double bag waste. Place in dumpster
with permission of site operator,
otherwise return to FEC for disposal
in dumpster
PPE-Reusable
Decontaminate as per Appendix B, if
possible If the equipment cannot be
decontaminated, containerize in plastic 5-
gallon bucket with tight-fitting lid Identify
and leave on-site with permission of site
operator, otherwise return to FEC for
proper disposal
Decontaminate as per Appendix B
Spent Solvents
Containerize in original containers. Clearly
identify contents Leave on-site with
permission of sue operator, otherwise return
to FEC for proper disposal
N/A
Soil Cuttings
Containerize m 55-gallon drum with tight-
fitting lid Identify and leave on-site with
permission of sue operator, otherwise
arrange with WMD sue manager for testing
and disposal.
Containerize in 55-gallon drum with
tight-fitting lid Identify and leave on-
sue with permission of site operator,
otherwise arrange with site manager
for testing and disposal
Groundwater
Containerize in 55-gallon drum with tight-
fitting lid Identify and leave on-site with
permission of sue operator, otherwise
arrange with WMD sue manager for testing
and disposal.
Containerize in 55-gallon drum with
tight-fitting lid. Identify and leave on-
site with permission of sue operator,
otherwise arrange with sue manager
for testing and disposal
Decontamination
Water
Containerize in 55-gallon drum with tight-
fitting lid Identify and leave on-site with
permission of sue operator, otherwise
arrange with WMD sue manager for testing
and disposal
Containerize in 55-gallon drum with
tight-fitting lid Identify and leave on-
site with permission of sue operator,
otherwise arrange with sue manager
for testing and disposal
Disposable
Equipment
Containerize in 55-gallon drum or 5-gallon
plastic bucket with tight-fitting lid Identify
and leave on-site with permission of sue
operator, otherwise arrange with WMD site
manager for testing and disposal.
Containerize in 55-gallon drum or 5-
gallon plastic bucket with tight-fitting
lid. Identify and leave on-siie with
permission of site operator, otherwise
arrange with sue manager for testing
and disposal.
Trash
N/A
Double bag waste. Place in dumpster
with permission of site operator,
otherwise return to FEC for disposal
in dumpster.
EISOPQAM
5-47
May 1996
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5.16 References
1 US-EPA, Guidance for the Data Quality Objectives Process (EPA QA/G-4, 1994)
2 ASTM, Standard Practice for Generation of Environmental Data Related to Waste Management
Activities- Development of Data Quality Objectives (D-34.02.10-Draft)
3 ASTM. Standard Guide for the Generation of Environmental Data Related to Waste Management
Activities (D-34.01.11-Draft)
4 Gilbert. Richard O., Statistical Methods for Environmental Pollution Monitoring. Van Nostrand
Remhold Co., New York, NY, 1987.
5 ASTM, Standard Guide for General Planning of Waste Sampling.
6 US-EPA, Characterization of Hazardous Waste Sites - A Methods Manual. Volume 1 - Site
Investigations (EPA 600/4-84/075)
7 Kittrell. F W., A Practical Guide to Water Quality Studies.
8 US-EPA, Data Quality Objectives Process for Superfund. Interim Final Guidance. (EPA540-R-93-
071). September 1993
E1SOPQAM 5 - 48 May 1996
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SECTION 6
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SECTION 6
DESIGN AND INSTALLATION OF MONITORING WELLS
PERFORMANCE OBJECTIVES:
• Ensure that the monitoring well will provide high quality samples.
• Ensure that the monitoring well is constructed properly and will last the duration of the
project.
• Ensure that the monitoring well will not serve as a conduit for contaminants 10 migrate
between aquifers
6.1 Introduction
Methods and procedures for the design and installation of monitoring wells to be employed in
Region 4 are contained in this section They are to be used for all permanent and temporary monitoring
wells installed for collecting ground water samples for analysis.
6.2 Permanent Monitoring Wells - Design Considerations
The design and installation of permanent monitoring wells involves drilling into various types of
geologic formations that exhibit varying subsurface conditions. Designing and installing permanent
monitoring wells in these geologic environments may require several different drilling methods and
installation procedures. The selection of drilling methods and installation procedures should be based on
field data collected during a hydrogeologic site investigation and/or a search of existing data Each
permanent monitoring well should be designed and installed to function properly throughout the duration
of the monitoring program. When designing monitoring wells, the following should be considered-
• short-and long-term objectives.
• purpose(s) of the well(s),
• probable duration of the monitoring program;
• contaminants likely to be monitored.
• types of well construction materials to be used;
• surface and subsurface geologic conditions,
• properties of the aquifer(s) to be monitored,
• well screen placement,
• general site conditions; and
• potential site health and safety hazards.
Each of the above considerations can be expanded into many subtopics depending on the complexity of the
project. In designing permanent monitoring wells, the most reliable, obtainable data should be utilized
Once the data have been assembled and the well design(s) completed, a drilling method(s) has to be
selected The preferred drilling procedure for installing permanent monitoring wells is the hollow-stem
EISOPQAM 6-1 May 1996
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auger method However, site conditions may not always be amenable to using the hollow-stem auger
method When this occurs, alternate methods should be selected that will perform the job equally as well
The following discussion of methods and procedures for designing and installing monitoring wells will
cover the different aspects of selecting materials, drilling boreholes, and installing monitoring devices
6.3 Drilling Methods
The following drilling methods are listed in order of preference; however, final selection should be based
on actual site conditions
6 3 1 Hollow-Stem Auger
This type of auger consists of a hollow, steel stem or shaft with a continuous, spiralled steel flight.
welded onto the exterior side of the stem, connected to an auger bit and when rotated transports
cuttings to the surface This method is best suited in soils that have a tendency to collapse when
disturbed. A monitoring well can be installed inside of hollow-stem augers with little or no
concern for the caving potential of the soils and/or water table. However, retracting augers in
caving sand conditions while installing monitoring wells can be extremely difficult or impossible,
especially since the augers have to be extracted without being rotated. If caving sands exist during
monitoring well installations, a drilling rig must be used that has enough power to extract the
augers from the borehole without having to rotate them. A bottom plug, trap door, or pilot bit
assembly can be fastened onto the bottom of the augers to keep out most of the soils and/or water
that have a tendency to clog the bottom of the augers during drilling. Potable water (analyzed for
contaminants of concern) may be poured into the augers (where applicable) to equalize pressure
so that the inflow of formation materials and water will be held to a minimum when the bottom
plug is released Water-tight center plugs are not acceptable because they create suction when
extracted from the augers. This suction forces or pulls cuttings and formation materials into the
augers, defeating the purpose of the centerplug. Augenng without a center plug or pilot bit
assembly is permitted, provided that the soil plug, formed in the bottom of the augers, is removed
before sampling or installing well casings Removing the soil plug from the augers can be
accomplished by washing out the plug using a side discharge rotary bit, or augermg out the plug
with a solid-stem auger bit sized to fit inside the hollow-stem auger. The type of bottom plug, trap
door, or pilot bit assembly proposed for the drilling activity should be approved by a senior field
geologist prior to drilling operations Boreholes can be augered to depths of 150 feet or more
(depending on the auger size), but generally boreholes are augered to depths less than 100 feet
6 3.2 Solid-Stem Auger
This type of auger consists of a solid stem or shaft with a continuous spiralled steel flight, welded
on the outer side of the stem, connected to an auger bit and when rotated transports cuttings to the
surface This auger method is used in cohesive and semi-cohesive soils that do not have a tendency
to collapse when disturbed. Boreholes can be augered to depths of 200 feet or more (depending
on the auger size), but generally boreholes are augered to depths less than 150 feet.
Both of the previously discussed auger methods can be used in unconsolidated soils and semi-
consolidated (weathered rock) soils, but not in competent rock Each method can be employed without
introducing foreign materials into the borehole such as water and drilling fluids, minimizing the potential
for cross contamination. Minimizing the risk of cross contamination is one of the most important factors
to consider when selecting the appropriate drilling method(s) for a project.
EISOPQAM 6-2 May 1996
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633 Rotary Methods
This method consists of a drill pipe or drill stem coupled to a drilling bit that rotates and cuts
through the soils. The cuttings produced from the rotation of the drilling bit are transported to the
surface by drilling fluids which generally consist of water, drilling mud, or air. The water, drilling
mud, or air are forced down through the drill pipe, and out through the bottom of the drilling bit
The cuttings are then lifted to the surface between the borehole wall and the drill pipe The drilling
fluids not only force the cuttings to the surface but also keeps the drilling bit cool When
considering this method, it is important to evaluate the potential for contamination when fluids
and/or air are introduced into the borehole. If the rotary method is selected as one of the drilling
methods, water rotary is the preferred method, followed by air rotary and mud rotary
Water Rotary
When using water rotary, potable water (that has been analyzed for contaminants of concern)
should be used If potable water (or a higher quality water) is not available on-site, then potable water will
have to be transported to the site or an alternative drilling method will have to be selected Water rotary
is the preferred rotary method because potable water is the only fluid introduced into the borehole during
drilling Water does not clog the formation materials reducing well development time, however this
potable water will flow out into the surrounding formation materials (if permeable) and mix with the natural
formation water This mixing of the drilling water and the natural formation water should be evaluated
when determining the drilling method Generally, a large majority of the drilling water will be recovered
during well development
Air Rotary
When using air rotary, the air compressor should have an in-line organic filter system to filter the
air coming from the compressor The organic filter system should be regularly inspected to insure that the
system is functioning properly Air compressors that do not have in-line organic filter systems are not
acceptable for air rotary drilling A cyclone velocity dissipator or similar air containment system should
be used to funnel the cuttings to one location instead of letting the cuttings blow uncontrolled out of the
borehole The conventional air rotary method does not control cuttings blowing out of the borehole, and
is not acceptable unless the above mentioned cyclone velocity dissipator or similar containment system is
emplo>ed Any air rotary method that allows cuttings to blow uncontrolled out of the borehole and does
not direct them to a discharge point with minimal disturbance is not acceptable. Air rotary that employs
the dual-tube (reverse circulation) drilling system is acceptable since the cuttings are contained in the drill
stems and blown to the surface through the cyclone velocity dissipator and to the ground with little surface
disturbance
Mud Rotary
Mud rotary is the least preferred rotary method because contamination can be introduced into the
borehole from the constituents in the drilling mud, and it is very difficult to remove the drilling mud from
the borehole after drilling and during well development The drilling mud can also carry contaminates
from a contaminated zone to an uncontammated zone thereby cross-contaminating the borehole If mud
rotary is selected, only potable water and pure (no additives) bentonite drilling muds should be used All
materials used should have adequate documentation as to manufacturer's recommendations and product
constituents The proper field QA/QC procedures should be initiated before and during drilling to
minimize the potential for contamination These QA/QC procedures include, but are not limited to,
sampling and analyzing of all drilling materials such as drilling muds, bentonite pellets, grouts, sand, etc.,
and the potable water to be used during drilling
EISOPQAM 6-3 May 19%
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6.3 4 Other Methods
Other methods such as the cable-tool method, the jetting method, the boring (bucket auger) method,
and various sonic drilling methods are available If these and/or other methods are selected for monitoring
well installations, they should be approved by a senior field geologist before Held work is initiated
6.4 Borehole Construction
6 4 1 Annular Space
The borehole should be of sufficient diameter so that well construction can proceed without major
difficulties. To assure an adequate size, a minimum 2-inch annular space is required between the casing
and the borehole wall (or the hollow-stem auger wall). For example, an 8-inch borehole is required to
install a 4-mch outside diameter (OD) casing However, if the inside diameter (ID) of the casing is 4
inches, the borehole will have to be larger than 8-mches to include the 2-inch annular space and the outside
diameter (OD) of the casing (4 inch ID plus the casing wall thickness). The 2-inch annular space around
the casing will allow the filter pack, bentonite pellet seal, and the annular grout to be placed at an accep-
table thickness Also, the 2-inch annular space will allow up to a 1.5-inch (OD) tremie tube to be used for
placing the filter pack, pellet seal, and grout at the specified intervals. An annular space less than the
2-inch minimum will not be acceptable When installing a well inside of hollow-stem augers, the inside
diameter (ID) of the augers is the area to be considered when determining the 2-inch annular space
642 Overdrillmg the Borehole
Sometimes it is necessary to overdrill the borehole so that any soils that have not been removed
or that have fallen into the borehole during augenng or drill stem retrieval, will fall to the bottom of the
borehole below the depth where the filter pack and well screen are to be placed. Normally, 3 to 5 feet is
sufficient for overdnllmg. The borehole can also be overdrilled to allow for an extra space or a "sump"
area below the well screen. This "sump" area provides a space to attach a 5 or 10 foot section of well
casing to the bottom of the well screen. The extra space or "sump" below the well screen serves as a catch
basin or storage area for sediment that flows into the well and drops out of suspension. These "sumps"
are added to the well screens when the wells are screened in aquifers that are naturally turbid and will not
yield clear formation water (free of visible sediment) even after extensive development. The seuiment can
then be periodically pumped out of the "sump" preventing the well screen from clogging or "silting up"
If the borehole is overdrilled deeper than desired, it can be backfilled to the designed depth with bentonite
pellets or the filter sand that is to be used for the filter pack.
643 Filter Pack Placement
When placing the filter pack into the borehole, a minimum of 6-inches of the filter pack material
should be placed under the bottom of the well screen to provide a firm footing and an unrestricted flow
under the screened area Also, the filter pack should extend a minimum of 2-feet above the top of the well
screen The filter pack should be placed by the tremie or positive displacement method. Placing the filter
pack b\ "pouring" may be acceptable m certain situations, which will be discussed in the next section
EISOPQAM 6-4 May 1996
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644 Filter Pack Seal-Bentonite Pellet Seal (Plug)
A seal should be placed on top of the filter pack. This seal should consist of a 30% solids bentonite
material in the form of bentonite pellets. Bentonite pellets are compressed to a density of 70-80 Ibs/cu ft
The preferred method of placing bentonite pellets is by the positive displacement or the tremie method
Use of the tremie method minimizes the risk of pellets bridging in the borehole and assures the placement
of pellets (also sand and grout) at the proper intervals. Pouring of the pellets (and filter pack materials)
is acceptable in shallow boreholes (less than SO feet) where the annular space is large enough to prevent
bridging and to allow measuring (with a tape measure) to insure that the pellets have been placed at the
proper intervals. In order to insure that the pellets have been placed at the proper intervals, the pellets
should be tamped, with the appropriate tamping tool, while measuring is being conducted. The tamping
process minimizes the potential for pellet bridging by forcing any pellets, that have lodged against the
borehole wall, hollow-stem auger wall, or the well casing, down to the proper interval. The bentonite seal
should be placed above the filter pack at a minimum of two feet vertical thickness. The hydration time for
the bentonite pellets should be a minimum of eight hours or the manufacturer's recommended hydration
time, whichever is greater. In all cases the proper depths should be documented by measuring and not by
estimating Other forms of bentonite such as granular bentonite, and bentonite chips have limited
applications, and are not recommended for the bentonite seal unless special conditions warrant their use
Deviation from bentonite pellets for the seal, should not be acceptable unless approved by a senior field
geologist If for some reason, the water table is temporarily below the pellet seal interval, potable water
(or a higher quality water) should be used to hydrate the pellets.
645 Grouting the Annular Space
The annular space between the casing and the borehole wall should be filled with either a 30%
solids bentonite grout, a neat cement grout, or a cement/bentonite grout. Each type of grout selected
should be evaluated as to us intended use and integrity.
The preferred grout to use should be a 30 % solids bentonite grout with a minimum density of 10
Ib/gal The grout should be placed into the borehole, by the tremie method, from the top of the bentonite
seal to within 2-feet of the ground surface or below the frostlme, whichever is greater. The tremie rube
should have an option of a side discharge pon or a bottom discharge port, to minimize damage to the filter
pack and/or the bentonite pellet seal, during grout placement. The grout should be allowed to cure for a
minimum of 24 hours before the concrete surface pad is installed. All grouts should be prepared in
accordance with the manufacturers specifications Bentonite grouts (not cement) should have a minimum
density of 10 Ibs/gal to ensure proper set-up The density of the bentonite grouts should be measured while
mixing and should not be pumped into the borehole until the minimum density of 10 Ibs/gal is attained
In addition, the grouting operation should not cease until the bentonite grout flowing out of the borehole
has a minimum density of 10 Ibs/gal A mud balance should be used to measure the specified grout density
of the bentonite grout Estimating the grout density is not acceptable. Drilling muds are not acceptable
for grouting
Cement grouts should be mixed using 6.5 to 7 gallons of water per 94-lb bag of Type 1 Portland
cement The addition of bentonite (5 to 10 percent) to the cement grout is generally used to delay the
"setting" time and may not be needed in all applications. The specific mixtures and other types of cement
and\or grout proposed should be evaluated on a case by case basis by a senior field geologist
EISOPQAM 6 - 5 May 1996
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6 4.6 Above Ground Riser Pipe and Outer Protective Casing
The well casing, when installed and grouted, should extend above the ground surface a minimum
of 2.5 feet. A vent hole should be drilled into the top of the well casing cap to permit pressure
equalization, if applicable. An outer protective casing should be installed into the borehole after the
annular grout has cured for at least 24 hours. The outer protective casing should be of steel construction
with a hinged, locking cap Generally, outer protective casings used over 2-inch well casings are 4 inches
square by 5 feet long. Similarly, protective casings used over 4-inch well casings are 6 inches square and
5 feet long Round protective casings are also acceptable. All protective casings should have sufficient
clearance around the inner well casings, so that the outer protective casings will not come into contact with
the inner well casings after installation. The protective casings should have a minimum of two weep holes
for drainage These weep holes should be a minimum 1/4-inch in diameter and drilled into the protective
casings just above the top of the concrete surface pads to prevent water from standing inside of the
protective casings. Protective casings made of aluminum or other soft metals are normally not acceptable
because they are not strong enough to resist tampering. Aluminum protective casing may be used in very
corrosive environments such as coastal areas A protective casing is installed by pouring concrete into the
borehole on top of the grout The protective casing is then pushed into the wet concrete and borehole a
minimum of 2 feet. Extra concrete may be needed to fill the inside of the protective casing so that the level
of the concrete inside of the protective casing is at or above the level of the surface pad. The protective
casing should extend a minimum of 3 feet above the ground surface or to a height so that the cap of the
inner well casing is exposed when the protective casing is opened.
647 Concrete Surface Pad
A concrete surface pad should be installed around each well at the same time as the outer protective
casing is being installed. The surface pad should be formed around the well casing. Concrete should be
placed into the formed pad and into the borehole (on top of the grout) in one operation making a contiguous
unit The protective casing is then installed into the concrete as described in the previous section The size
of the concrete surface pad is dependent on the well casing size. If the well casing is 2 inches in diameter,
the pad should be 3 feet x 3 feet x 6 inches If the well casing is 4 inches in diameter, the pad should be
4 feet x 4 feet x 6 inches Round concrete surface pads are also acceptable The finished pad should be
sloped so that drainage will now away from the protective casing and off of the pad. In addition, a
minimum of one inch of the finished pad should be below grade or ground elevation to prevent washing
and undermining by soil erosion At each site, all locks on the outer protective casings should be keyed
alike
648 Surface Protection-Bumper Guards
If the monitoring wells are located in a high traffic area, a minimum of three bumper guards
consisting of steel pipes 3 to 4 inches in diameter and a minimum 5-foot length should be installed. These
bumper guards should be installed to a minimum depth of 2 feet below the ground surface in a concrete
footing and extend a minimum of 3 feet above ground surface. Concrete should also be placed into the
steel pipe to provide additional strength. Steel rails and/or other steel materials can be used in place of
steel pipe but approval must be granted by a senior field geologist prior to field installation.
EISOPQAM 6-6 May 1996
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6.5 Construction Techniques
6 5 1 Well Installation
The borehole should be bored, drilled, or augered as close to vertical as possible, and checked with
a plumb bob or level. Slanted boreholes will not be acceptable unless specified in the design The depth
and volume of the borehole, including the overdrilling if applicable, should have been calculated and the
appropriate materials procured prior to drilling activities. The well casings should be secured to the well
screen by flush-jointed threads and placed into the borehole and plumbed by the use of centralizers and/or
a plumb bob and level. Another method of placing the well screen and casings into the borehole and
plumbing it at the same time is to suspend the string of well screen and casings in the borehole by means
of the wireline on the drill rig. The string of well screen and casings can be placed into the borehole and
plumbed in one easy operation. This wireline method is especially useful if the borehole is deep and a long
string of well screen and casings have to be set and plumbed. No lubricating oils or grease should be used
on casing threads. Teflon tape can be used to wrap the threads to insure a tight fit and minimize leakage
No glue of any type should be used to secure casing joints. Teflon "O" rings can also be used to insure
a tight fit and minimize leakage, however, "O" rings made of other materials are not acceptable if the well
is going to be sampled for organic compound analyses Before the well screen and casings are placed on
the bottom of the borehole, at least 6 inches of filter material should be placed at the bottom of the borehole
to serve as a firm footing. The string of well screen and casings should then be placed into the borehole
and plumbed Centralizers can be used to plumb a well, but centralizers should be placed so that the
placement of the filter pack, bentomte pellet seal, and annular grout will not be hindered Centralizers
placed in the wrong locations can cause bridging during material placement. Monitoring wells less than
50 feet deep generally do not need Centralizers If Centralizers are used they should be placed below the
well screen and above the bentomte pellet seal The specific placement intervals should be decided based
on site conditions When installing the well screen and casings through hollow-stem augers, the augers
should be slowly extracted as the filter pack, bentomte seal, and grout are tremied and/or poured into
place The gradual extraction of the augers will allow the materials being placed in the augers, to flow out
of the bottom of the augers into the borehole If the augers are not gradually extracted, the materials (sand.
pellets, etc ) will accumulate at the bottom of the augers causing potential bridging problems After the
string of well screen and casing is plumb, the filter material should then be placed around the well screen
(preferably by the tremie method) up to the designated depth. After the filter pack has been installed, the
bentomte pellet seal should be placed (preferably by the tremie method) directly on top of the filter pack
up to the designated depth or a minimum of 2 feet above the filter pack whichever is greater The
bentomte pellet seal should be allowed to hydrate a minimum of eight hours or the manufacturer's
recommended hydration time, whichever is longer. After the pellet seal has hydrated for the specified
time, the grout should then be pumped by the tremie method into the annular space around the casings up
to within 2 feet of the ground surface or below the frost line whichever is greater. The grout should be
allowed to set for a minimum of 24 hours before the surface pad and protective casing are installed. After
the surface pad and protective casing are installed, bumper guards should be installed (if needed) The
bumper guards should be placed around the concrete surface pad in a configuration that provides maximum
protection to the well Each piece of steel pipe or approved material should be installed into an 8-to 10-
inch diameter hole, to a minimum depth of 2 feet below ground surface, and filled with concrete. As
previously stated, the bumper guard should extend above the ground surface a minimum of 3 feet. The
total length of each bumper guard should be a minimum of 5 feet.
After the wells have been installed, the outer protective casing should be painted with a highly
visible enamel paint The wells should be permanently marked with the well number, date installed, site
name, elevation, etc., either on the cover or an appropriate place that will not be easily damaged and/or
vandalized
EISOPQAM 6 - 7 May 1996
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If the monitoring wells are installed in a high traffic area such as a parking lot, in a residential
yard, or along the side of a road it may be desirable to finish the wells to the ground surface and install
water-tight flush mounted traffic and/or man-hole covers. Flush mounted traffic and man-hole covers are
designed to extend from the ground surface down into the concrete plug around the well casing Although
flush mounted covers may vary in design, they should have seals that make the unit water-tight when closed
and secured. The flush mounted covers should be installed as far above grade as practical to minimize
standing water and promote runoff Permanent identification markings should be placed on the covers or
in the concrete plug around the cover
6.5 2 Double Cased Wells
Double cased wells should be constructed when there is reason to believe that interconnection of
two aquifers by well construction may cause cross contamination, and/or when flowing sands make it
impossible to install a monitoring well using conventional methods. A pilot borehole should be bored
through the overburden and/or the contaminated zone into the clay confining layer or bedrock An outer
casing (sometimes called surface or pilot casings) should then be placed into the borehole and sealed with
grout The borehole and outer casing should extend into tight clay a minimum of two feet and into
competent bedrock a minimum of 1 foot The total depths into the clay or bedrock will vary, depending
on the plasticity of the clay and the extent of weathering and\or fracturing of the bedrock The final depths
should be approved by a senior field geologist The size of the outer casing should be of sufficient inside
diameter (ID) to contain the inner casing, and the 2-inch minimum annular space. In addition, the borehole
should be of sufficient size to contain the outer casing and the 2-inch minimum outer annular space, if
applicable
The outer casing should be grouted by the tremie method from the bottom to within 2 feet of the
ground surface. The grout should be pumped into the annular space between the outer casing and the
borehole wall. This can be accomplished by either placing the tremie tube in the annular space and
pumping the grout from the bottom of the borehole to the surface, or placing a grout shoe or plug inside
the casing at the bottom of the borehole and pumping the grout through the bottom grout plug and up the
annular space on the outside of the casing. If the outer casing is set into very tight clay, both of the above
methods might have to be used, because the clay usually forms a tight seal in the bottom and around the
outside of the casing preventing grout from flowing freely during grout injection On the other hand, outer
casing set into bedrock normally will have space enough to allow grout to flow freely during injection
A minimum of 24 hours should be allowed for the grout plug (seal) to cure before attempting to drill
through it The grout mixture used to seal the outer annular space should be either a neat cement.
cement/bentonite, cement/sand, or a 30% solids bentonite grout However, the seal or plug at the bottom
of the borehole and outer casing should consist of a Type I portland cement/bentonite or cement/sand
mixture The use of a pure bentonue grout for a bottom plug or seal is not acceptable, because the
bentomie grout cures to a gel-like material, and is not rigid enough to withstand the stresses of drilling.
When drilling through the seal, care should be taken to avoid cracking, shattering, and/or washing out the
seal, which will be discussed in the next section. If caving conditions exist so that the outer casing cannot
be sufficiently sealed by grouting, the outer casing should be driven into place and a grout seal placed in
the bottom of the casing. Removal of outer casings, which are sometimes called temporary surface
casings, after the well screens and casings have been installed and grouted is not acceptable. Trying to
remove outer surface casings after the inner casings have been grouted could jeopardize the structural
integrity of the well.
EISOPQAM 6 - 8
May 1996
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Bedrock Wells
The installation of monitoring wells into bedrock can be accomplished in two ways'
1 The first method is to drill or bore a pilot borehole through the soil overburden into the bedrock
An outer casing is then installed into the borehole by setting it into the bedrock, and grouting it into
place as described in the previous section. After the grout has set, the borehole can then be
advanced through the grout seal into the bedrock. The preferred method of advancing the borehole
into the bedrock is rock coring Rock coring makes a smooth, round hole through the seal and into
the bedrock without cracking and/or shattering the seal. Roller cone bits are used in soft bedrock,
but extreme caution should be taken when using a roller cone bit to advance through the grout seal
in the bottom of the borehole because excessive water and "down" pressure can cause cracking.
eroding (washing), and/or shattering of the seal. Low volume air hammers may be used to
advance the borehole, but they have a tendency to shatter the seal because of the hammering
action If the structural integrity of the grout seal is in question, a pressure test can be utilized to
check for leaks. A visual test can also be made by examining the cement/concrete core that is
collected when the seal is cored with a diamond coring bit. If the seal leaks (detected by pressure
testing) and/ or the core is cracked or shattered, or if no core is recovered because of washing,
excessive down pressure, etc., the seal is not acceptable The concern over the structural integrity
of the grout seal applies to all double cased wells Any proposed method of double casing and/or
seal testing will be evaluated on its own merits, and will have to be approved by a senior field
geologist before and during drilling activities, if applicable. When the drilling is complete, the
finished well will consist of an open borehole from the ground surface to the bottom of the well
There is no inner casing, and the outer surface casing, installed down into bedrock, extends above
the ground surface, and also serves as the outer protective casing. If the protective casing becomes
cracked or is sheared off at the ground surface, the well is open to direct contamination from the
ground surface and will have to be repaired immediately or abandoned. Another limitation to the
open rock well is that the entire bedrock interval serves as the monitoring zone In this situation.
it is very difficult or even impossible to monitor a specific zone, because the contaminants being
monitored could be diluted to the extent of being nondetectable. The installation of open bedrock
wells is generally not acceptable in the Superfund and RCRA programs, because of the
uncontrolled monitoring intervals However, some sue conditions might exist, especially in
cavernous limestone areas (Karst topography) or in areas of highly fractured bedrock, where the
installation of the filter pack and its structural integrity are questionable Under these conditions
the design of an open bedrock well may be warranted
2 The second method of installing a monitoring well into bedrock is to install the outer surface casing
and drill the borehole (by an approved method) into bedrock, and then install an inner casing and
well screen with the filter pack, bentomte seal, and annular grout. The well is completed with a
surface protective casing and concrete pad This well installation method gives the flexibility of
isolating the monitoring zone(s) and minimizing inter-aquifer flow. In addition, it gives structural
integrity to the well, especially in unstable areas (steeply dipping shales, etc.) where the bedrock
has a tendency to shift or move when disturbed. Omitting the filter pack around the well screen
is a general practice in some open rock borehole installations, especially in drinking water and
irrigation wells. However, without the filter pack to protect the screened interval, sediment
particles from the well installation and/or from the monitoring zone could clog the well screen
and/or fill the screened portion of the well rendering it inoperable Also, the filter pack serves as
a barrier between the bentomte seal and the screened interval. Rubber inflatable packers have been
used to place the bentomte seal when the filter pack is omitted, but the packers have to remain m
the well permanently and, over a period of time, will decompose and possibly contribute
contaminates to the monitoring zone
E1SOPQAM 6-9 May 1996
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6.6 Well Construction Materials
6.6 1 Introduction
Well construction materials are chosen based on the goals and objectives of the proposed
monitoring program and the geologic conditions at the site(s). In this section, the different types of
available materials will be discussed
662 Well Screen and Casing Materials
When selecting the materials for well construction, the prime concern should be to select materials
that will not contribute foreign constituents, or remove contaminants of concern from the ground water
If the monitoring program is designed to analyze for organic compounds, stainless steel materials should
be used. If the monitoring program calls for the analyses of only inorganic compounds, then PVC
materials (Rigid PVC meeting NSF Standard 14 (NSF WQ) are acceptable. Generally, PVC materials
are not acceptable for monitoring organic compounds because of their sorption and leaching properties
Another concern is to select materials that will be rugged enough to endure the entire monitoring period
Site conditions will generally dictate the kind of materials that can be used. A preliminary field
investigation should be conducted to determine the geologic conditions, so that the most suitable materials
can be selected. The best grade or highest quality material for that particular application should be
selected Each manufacturer can supply the qualitative data for each grade of material that is being
considered All materials selected for monitoring well installation should be evaluated and approved by
a senior field geologist prior to Held activities.
Well screen and casing materials generally used in monitoring well construction on RCRA and
Superfund sites are listed in order of preference
(1) Stainless Steel (304 or 316)
(2) Rigid PVC meeting NSF Standard 14 (NSF WC)
(3) Other (where applicable)
There are other materials used for well screens and casings such as black iron, carbon steel,
galvanized steel, and fiberglass, but these materials are not recommended for use in long term monitoring
programs at hazardous waste sites, because of their low resistance to chemical attack and potential
constituent contribution to the ground water.
In addition to material selection, the minimum inside diameter (ID) for well screens and casings
used for permanent monitoring wells should be 2 inches. The wall thickness has to be considered when
selecting the 2-inch well screen and casing, because a 2-inch ID screen or casing having a total wall
thickness greater than 1/8 inch will make the outside diameter (OD) 2 1/4 inches which will reduce the
required 2-inch annular space. This is especially true for PVC and Teflon. Schedule 5 stainless steel,
which is commonly used for permanent monitoring wells has a very thin wall thickness (approximately 1/16
inch thick) which reduces the 2-inch annular space by only 1/8 inch However, all minimum requirements
for well design and installation should be adhered to when selecting the appropriate materials. For
example, if the ID of the screen or casing is 2 inches and the OD is 2 1/2 inches, then the borehole will
have 10 be at least 6 1/2 inches in diameter to satisfy the minimum requirements.
The length of well screens in permanent monitoring wells should be long enough to effectively
monitor the interval or zone of interest. However, well screens designed for long term monitoring
purposes should normally not be less than 5 feet in length. Well screens less that 5 feet long are acceptable
in only temporary monitoring wells where ground water samples are collected for screening purposes.
EISOPQAM 6 - 10 May 1996
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6 6.3 Filter Pack Materials
The filter pack materials should consist of clean, rounded to well-rounded, hard, insoluble particles
of siliceous composition. The required gram-size distribution or particle sizes of the filter pack materials
should be selected based upon a sieve analysis conducted on the soil samples collected from the aquifer
materials and/or the formation(s) to be monitored Filter pack materials should not be acceptable unless
proper documentation can be furnished as to the composition, grain-size distribution, cleaning procedure.
and chemical analysis. If a data search reveals that there is enough existing data to adequately design the
well screen and filter pack, then it may not be necessary to conduct a sieve analysis on the formation
materials to be monitored However, all data and design proposals will be evaluated and approved by a
senior staff geologist before field activities begin.
664 Filter Pack and Well Screen Design
The majority of monitoring wells are installed in shallow ground water aquifers that consist of silts.
clays, and sands in various combinations These shallow aquifers are not generally characteristic of sand
aquifers used for drinking water Therefore, a more technical approach rather than an estimative approach
should be taken in the design of filter packs and well screens for monitoring wells. The filter pack and well
screen design should be based on the results of a sieve analysis conducted on soil samples collected from
the aquifer or the formation(s) that will be monitored. The data from the sieve analysis are plotted on a
gram-size distribution graph, and a grain-size distribution curve is generated. From this gram-size
distribution curve, the uniformity coefficient (Cu) of the aquifer material is determined. The Cu is the ratio
of the 60 percent finer material (D60) to the 10 percent finer material (D10)
Cu = (D60/D10)
The Cu ratio is a way of grading or rating the uniformity of grain size. For example, a Cu of unir>
means that the individual gram sizes of the material are nearly all the same, while a Cu with a large number
means a large range of sizes As a general rule, a Cu of 2.5 or less should be used in designing the filter
pack and well screen
Before designing the filter pack and well screen, the following factors should be considered
1 Select the well screen slot openings that will retain 90 percent of the filter pack material
2 The filter pack material should be of the size that minimizes head losses through the pack and also
prevents excessive sediment (sand. silt, clay) movement into the well.
3 A filter material of varying gram sizes is not acceptable because the smaller panicles fill the spaces
between the larger panicles thereby reducing the void spaces and increasing resistance to flow
Therefore, filter material of the same gram size and well rounded is preferred.
4 The filter pack design is based on the gradation of the finest aquifer materials being analyzed
EISOPQAM 6-11 May 1996
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General steps to consider in designing a filter pack:
1. Construct a grain-size distribution curve, on a grain-size distribution graph, from the sieve analysis
of the aquifer materials. The filter pack design (as stated above) is based on the gradation of the
finest aquifer materials.
2 Multiply the D30 size (from the grain-size distribution graph) by a factor of four to nine (Pack-
Aquifer ratio). A factor of four is used if the formation is fine-grained and uniform (Cu is less
than 3), six if it is coarse-grained and non-uniform, and up to nine if it is highly non-uniform and
contains silt. Head losses through filter packs increase as the Pack-Aquifer(P-A) ratios decrease
In order to design a fairly stable filter pack with a minimum head loss, the D30 size should be
multiplied by a factor of four
3 Plot the point from step 2 on the 30% abscissa of a grain-size distribution graph and draw a smooth
curve with a uniformity coefficient of approximately 2 5.
4 A curve for the permissible limits of the filter pack is drawn plus or minus 8 per cent of the desired
curve with the Cu of 2.5.
5 Select the slot openings for the well screen that will retain 90 per cent or more of the filter pack
material.
The specific steps and procedures for sieve analysis and filter pack design can be found in soil
mechanics, ground water, and water well design books The staff geologists and/or engineers should be
responsible for the correct design of the monitoring wells and should be able to perform the design
procedures
6.7 Safety Procedures Tor Drilling Activities
A site health and safety plan should be developed and approved by the Branch Safety Officer or
designee prior to any drilling activities, and should be followed during all drilling activities The driller
or designated safety person should be responsible for the safety of the drilling team performing the drilling
activities All personnel conducting drilling activities should be qualified in proper drilling and safety
procedures Before any drilling activity is initiated, the area should be surveyed with the necessary
detection equipment to locate, flag, or mark, all under ground utilities such as electrical lines, natural gas
lines, fuel tanks and lines, water lines, etc Before operating the drill rig, a pilot hole should be dug (with
hand equipment) to a depth of two to three feet to check for undetected utilities or buried objects Proceed
with caution until a safe depth is reached where utilities normally would not be buried. The following
safety requirements should be adhered to while performing drilling activities:
1 All drilling personnel should wear safety hats, safety glasses, and steel toed boots. Ear plugs
are required and will be provided by the safety officer or driller.
2 Work gloves (cotton, leather, etc ) should be worn when working around or while handling
drilling equipment
3 All personnel directly involved with the drilling ng(s) should know where the kill switch(s) is
located in case of emergencies.
4 All personnel should stay clear of the drill rods or augers while in motion, and should not grab
or attempt to attach a tool to the drill rods or augers until they have completely stopped
rotating
E1SOPQAM 6. 12
May 1996
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5 Do not hold drill rods or any part of the safety hammer assembly while taking standard
penetration tests or while the hammer is being operated.
6 Do not lean against the drill rig or place hands on or near moving parts at the rear of the rig
while it is operating
7 Keep the drilling area clear of any excess debris, tools, or drilling equipment.
8 Do not climb on the drilling rig while it is being operated or attempt to repair the rig while it
is being operated The driller will direct all work on the rig.
9 Do not move or pick up any drilling equipment unless directed by the driller and/or the project
leader
10 Each drill rig will have a first-aid kit and a fire extinguisher located on the rig quickly
accessible for emergencies
11 Work clothes will be firm fitting, but comfortable and free of straps, loose ends, strings etc .
that might catch on some moving part of the drill rig.
12 Rings or other jewelry will not be worn while working around the drill rig
13 The drill rig should not be operated within a minimum distance of 20 feet of overhead
electrical power lines and/or buried utilities that might cause a safety hazard In addition, the
drill rig should not be operated while there is lightening in the area of the drilling site. If an
electrical storm moves in during drilling activities, vacate the area until it is safe to return
6.8 Well Development
A newly completed monitoring well should not be developed for at least 24 hours after the surface
pad and outer protective casing are installed This will allow sufficient time for the well materials to cure
before development procedures are initiated The mam purpose of developing new monitoring wells is to
remove the residual materials remaining in the wells after installation has been completed, and to try to re-
establish the natural hydraulic flow conditions of the formations which may have been disturbed by well
construction, around the immediate vicinity of each well A new monitoring well should be developed until
the column of water in the well is free of visible sediment, and the pH, temperature, turbidity, and specific
conductivity have stabilized. In most cases the above requirements can be satisfied, however, in some
cases the pH, temperature, and specific conductivity may stabilize but the water remains turbid In this
case the well may still contain well construction materials, such as drilling mud in the form of a mud cake
and/or formation soils, that have not been washed out of the borehole Excessive or thick drilling muds
can not be flushed out of a borehole with one or two well volumes of flushing. Continuous flushing over
a period of several days may be necessary to complete the well development If the well is pumped to
dryness or near dryness. the water table should be allowed to sufficiently recover (to the static water level)
before the next development period is initiated Caution should be taken when using high rate pumps
and/or large volume air compressors during well development because excessive high rate pumping and
high air pressures can damage or destroy the well screen and filter pack. The onsite geologist should make
the decision as to the development completion of each well All field decisions should be documented in
the field log book.
EiSOPQAM 6-13 May 1996
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The following development procedures are generally used to develop monitoring wells
1. Pumping;
2 Compressed air (with the appropriate organic filter system);
3 Bailing;
4 Surging;
5 Backwashmg ("rawhiding"); and
6. Jetting.
These developmental procedures can be used, individually or in combination, in order to achieve
the most effective well development. Except when compressed air is being used for well development,
sampling can be initiated as soon as the ground water has re-equilibrated, is free of visible sediment, and
the water quality parameters have stabilized Since site conditions vary, even between wells, a general
rule-of-thumb is to wait 24 hours after development to sample a new monitoring well. Wells developed
with compressed air normally should not be sampled for at least 48 hours after development so that the
formation can dispel the compressed air and restabilize to pre-well construction conditions. The selected
development method(s) should be approved by a senior field geologist before any well installation activities
are initiated
6.9 Well Abandonment
When a decision is made to abandon a monitoring well, the borehole should be sealed in such a
manner that the well can not act as a conduit for migration of contaminants from the ground surface to the
water table or between aquifers To properly abandon a well, the preferred method is to completely
remove the well casing and screen from the borehole, clean out the borehole, and backfill with a cement
or bentomte grout, neat cement, or concrete. In order to comply with state well abandonment
requirements, the appropriate state agency should be notified (if applicable) of monitoring well
abandonment However, some state requirements are not explicit, so a technically sound well abandonment
method should be designed based on the site geology, well casing materials, and general condition of the
well(s)
6 9 I Abandonment Procedures
As previously stated the preferred method should be to completely remove the well casing and
screen from the borehole. This may be accomplished by augering with a hollow-stem auger over the well
casing down to the bottom of the borehole, thereby removing the grout and filter pack materials from the
hole The well casing should then be removed from the hole with the drill rig. The clean borehole can
then be backfilled with the appropriate grout material. The backfill material should be placed into the
borehole from the bottom to the top by pressure grouting with the positive displacement method (tremie
method) The top 2 feet of the borehole should be poured with concrete to insure a secure surface seal
(plug). If the area has heavy traffic use, and/or the well locations need to be permanently marked, then
a protective surface pad(s) and/or steel bumper guards should be installed. The concrete surface plug can
also be recessed below ground surface if the potential for construction activities exists. This abandonment
method can be accomplished on small diameter (1-inch to 4-mch) wells without too much difficulty. With
wells having 6-mch or larger diameters, the use of hollow-stem augers for casing removal is very difficult
or almost impossible. Instead of trying to ream the borehole with a hollow-stem auger, it is more practical
to force a drill stem with a tapered wedge assembly or a solid-stem auger into the well casing and extract
it out of the borehole. Wells with little or no grouted annular space and/or sound well casings can be
removed in this manner. However, old wells with badly corroded casings and/or thickly grouted annular
space have a tendency to twist and/or break-off in the borehole. When this occurs, the well will have to
EISOPQAM 6 - 14 May 1996
-------
be grouted with the remaining casing left in the borehole The preferred method in this case should be to
pressure grout the borehole by placing the tremie tube to the bottom of the well casing, which will be the
well screen or the bottom sump area below the well screen. The pressurized grout will be forced out
through the well screen into the filter material and up the inside of the well casing sealing holes and breaks
that are present. The tremie tube should be retracted slowly as the grout fills the casing The well casing
should be cut off even with the ground surface and filled with concrete to a depth of 2 feet below the
surface If the casing has been broken off below the surface, the grout should be tremied to within 2 feet
of the surface and then finished to the ground surface with concrete. The surface pad or specified surface
protection shall then be installed
A PVC well casing may be more difficult to remove from the borehole than a metal casing, because
of its brittleness If the PVC well casing breaks during removal, the borehole should be cleaned out by
using a drag bit or roller cone bit with the wet rotary method to grind the casing into small cuttings that
will be flushed out of the borehole by water or drilling mud. Another method is to use a solid-stem auger
with a carbide tooth bit to grind the PVC casing into small cuttings that will be brought to the surface on
the rotating flights After the casing materials have been removed from the borehole, the borehole should
be cleaned out and pressure grouted with the approved grouting materials As previously stated, the
borehole should be finished with a concrete surface plug and adequate surface protection, unless directed
otherwise
6.10 Temporary Monitoring Well Installation
6 10 1 Introduction
Five types of temporary monitoring well installation techniques have been demonstrated as
acceptable The type selected for a particular site is dependent upon site conditions The project leader
and sue geologist should be prepared to test temporary well installations on site and select the best solution
Temporary wells are cost effective, may be installed quickly, and provide a synoptic picture of ground
water quality
Temporary monitoring well locations are not permanently marked, nor are their elevations
normalK determined Sand pack materials may or may not be used, but typically there is no bentonite seal.
grout, surface completion, or extensive development (as it normally applies to permanent monitoring
wells) Temporary wells are generally installed, purged, sampled, removed, and backfilled in a matter of
hours
Due to the nature of construction, turbidity levels may initially be high However, these levels
may be reduced by low flow purging and sampling techniques as described in Section 7.2 4
Temporary wells may be left overnight, for sampling the following day, but the well must be
secured If the well is not sampled immediately after construction, the well should be purged prior to
sampling as specified in Section 7.2 4
6102 Data Limitation
Temporary wells described in this section are best used for delineation of contaminant plumes, at
a point in time, and for some site screening purposes. They are not intended to replace permanent
monitoring wells Perhaps the best use for temporary wells is in conjunction with a mobile laboratory.
where quick analytical results can be used to delimnate contaminant plumes.
EISOPQAM 6-15 May 1996
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EISOPQAM 6 - 16 May 1996
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6103 Temporary Well Materials
Materials used in construction of temporary monitoring wells are the same standard materials used
in the construction of permanent monitoring wells. Sand used for the filter pack (if any) should be as
specified in Section 6.6.3. The well screen and casing should be stainless steel for ruggedness and
suitability for steam cleaning and solvent rinsing. Other materials may be acceptable, on a case by case
basis Some commercially available temporary well materials, pre-packed riser, screen and filter pack
assemblies are available commercially, however, these pre-assembled materials cannot be cleaned
Appropriate QA/QC must be performed to assure there will be no introduction of contamination
6 10 4 Temporary Monitoring Well Borehole Construction
Borehole construction for temporary wells is as specified in Section 6.4, using a drill rig
Alternatively, boreholes may be constructed using hand augers or portable powered augers (generally
limited to depths of ten feet or less) If a drill rig is used to advance the borehole, the augers must be
pulled back the length of the well screen (or removed completely) prior to sampling. When hand augers
are used, the borehole is advanced to the desired depth (or to the point where borehole collapse occurs)
In situations where borehole collapse occurs, the auger bucket is typically left in the hole at the point of
collapse while the temporary well is assembled. When the well is completely assembled, a final auger
bucket of material is quickly removed and the well is immediately inserted into the borehole, pushing, as
needed, to achieve maximum penetration into the saturated materials
6105 Temporary Monitoring Well Types
Five types of monitoring wells which have been shown to be acceptable are presented in the order
of increasing difficulty to install and increasing cost:
No Filter Pack
This is the most common temporary well and is very effective in many situations After the
borehole is completed, the casing and screen are simply inserted This is the most inexpensive and fastest
well to install This type well is extremely sensitive to turbidity fluctuations, because there is no filter
pack Care should be taken to not disturb the casing during purging and sampling.
Inner Filter Pack
This type differs from the "No Pack" only in that a filter pack is placed inside the screen to a level
approximately 6 inches above the well screen This ensures that all water within the casing has passed
through the filter pack. For this type well to function properly, the static water level must be 6-12 inches
above the filter pack
Traditional Filter Pack
For this type, the screen and casing are inserted into the borehole, and the sand is poured into the
annular space surrounding the screen and casing. Occasionally, it may be difficult to effectively place a
filter pack around shallow open boreholes, due to collapse. This method requires more sand than the
"inner filter pack" well, increasing material costs As the filter pack is placed, it mixes with the muddy
uater in the borehole, which may increase the amount of time needed to purge the well to an acceptable
level of turbidity.
EISOPQAM 6-17 May 1996
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Double Filter Pack
The borehole is advanced to the desired depth. As with the "inner filter pack" the well screen is
filled with filter pack material and the well screen and casing inserted until the top of the filter pack is at
least 6 inches below the water table Filter pack material is poured into the annular space around the well
screen This type temporary well construction can be very effective in aquifers where fine silts or clays
predominate This construction technique takes longer to implement and uses more filter pack material
than others previously discussed.
Well-m-a-Well
The borehole is advanced to the desired depth. At this point, a 1-inch well screen and sufficient
riser is inserted into a 2-inch well screen with sufficient riser, and centered. Filter pack material is then
placed into the annular space surrounding the 1-inch well screen, to approximately 6 inches above the
screen. The well is then inserted into the borehole.
This system requires twice as much well screen and casing, with subsequent increase in material
cost The increased amount of well construction materials results in a corresponding increase in
decontamination time and costs If pre-packed wells are used, a higher degree of QA/QC will result in
higher overall cost
6106 Backfilling
It is the generally accepted practice to backfill the borehole from the abandoned temporary well
with the soil cuttings Use of cuttings would not be an acceptable practice if waste materials were
encountered or a confining layer was inadvertently breached. If for some reason the borehole cannot be
backfilled with the soil cuttings, then the same protocols set forth in Section 6.9 should be applied Section
5 15 should be referenced regarding disposal of IDW
E1SOPQAM 6-18 May 1996
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SECTION 7
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SECTION 7
GROUND WATER SAMPLING
PERFORMANCE OBJECTIVES:
To collect a sample representative of ground water residing m the formation of
interest
To reduce the potential bias caused by the sampling equipment used to obtain the
sample
7.1 Introduction
Ground water sampling may be required for a variety of reasons, such as examining potable or
industrial water supplies, checking for and/or tracking contaminant plume movement in the vicinity of a
land disposal or spill site. Resource Conservation Recovery Act (RCRA) compliance monitoring, or
examining a site where historical information is minimal or non-existent but where it is thought that ground
water contamination may have occurred
Ground water samples are usually obtained from either temporarily or permanently installed ground
water monitoring wells. They can also be obtained, however, anywhere ground water is present, such as
in a pit or a dug or drilled hole
Occasionally, the ground water source may not be in the ideal location to meet a particular
objective (e g . to track a contaminant plume) In that case, either a temporary or permanent monitoring
well should be installed An experienced and knowledgeable person will need to locate the well and
supervise us installation so that samples will be representative of the ground water
Additional guidance is given in RCRA Ground-Water Monitoring. Technical Guidance (1) and
Chapter 11 of SW-846 (2). The ground water sampling procedures described in this SOP will meet or
exceed the requirements of these documents
Ground water sampling procedures can be sub-divided into two areas, purging and sampling, each
of which has different goals and objectives Within the topic of purging, it is necessary, because of the
inherently different characteristics of the two types of wells, to address permanent and temporary wells
separately The procedures and techniques which follow in this section reflect these differences
E1SOPQAM 7-1 May 19%
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7.2 Purging
7.2 1 Purging and Purge Adequacy
Purging is the process of removing stagnant water from a monitoring well, immediately prior to
sampling, causing its replacement by ground water from the adjacent formation, which is representative
of actual aquifer conditions. In order to determine when a well has been adequately purged, field
investigators should 1) monitor the pH, specific conductance, temperature, and turbidity of the ground
water removed during purging, and 2) observe and record the volume of water removed
Prior to initiating the purge, the amount of water standing in the water column (water inside the
well riser and screen) should be determined To do this, the diameter of the well should be determined
and the water level and total depth of the well are measured and recorded. Specific methodology for
obtaining these measurements is found in Section 15.8 of this SOP. Once this information is obtained, the
volume of water 10 be purged can be determined using one of several methods. One is the equation
V = 0041 d2h
Where, h = depth of water in feet
d = diameter of well in inches
V = volume of water in gallons
Alternatively, the volume may be determined using a casing volume per foot factor for the
appropriate diameter well, similar to that in Table 7.2.1. The water level is subtracted from the total
depth, providing the length of the water column This length is multiplied by the factor in the Table 7.2 1
which corresponds to the appropriate well diameter, providing the amount of water, in gallons, contained
in the well Other acceptable methods include the use of nomographs or other equations or formulae
With respect to volume, an adequate purge is normally achieved when three to five times the
volume of standing water in the well has been removed The field notes should reflect the single well
\olume calculations or determinations, according to one of the above methods, and a reference to the
appropriate multiplication of that volume, i e . a minimum three well volumes, clearly identified as a purge
volume goal
With respect to the ground water chemistry, an adequate purge is achieved when the pH, specific
conductance, and temperature of the ground water have stabilized and the turbidity has either stabilized
or is below 10 Nephelometnc Turbidity Units (NTUs) Ten NTUs is the goal for most ground water
sampling objectives This is twice the Primary Drinking Water standard of 5 NTUs Stabilization occurs
when pH measurements remain constant wiihm 0.1 Standard Unit (SU), specific conductance varies no
more that 10 percent, and the temperature is constant for at least three consecutive readings. There are
no criteria establishing how many sets of measurements are adequate for the determination of stability
If the calculated purge volume is small, the measurements should be taken frequently to provide a sufficient
number of measurements to evaluate stability. If the purge volume is large, measurements taken every 15
mmuies may be sufficient
If. after three well volumes have been removed, the chemical parameters have not stabilized
according to the above criteria, additional well volumes may be removed If the parameters have not
stabilized within five volumes, it is at the discretion of the project leader whether or not to collect a sample
or to continue purging The conditions of sampling should be noted in the field log.
EISOPQAM 7-2 May 1996
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TABLE 7.2.1
WELL CASING DIAMETER vs VOLUME
WELL CASING DIAMETER vs VOLUME (GALS.)/FEET of WATER
CASING
SIZE
1
2
3
4
5
6
7
8
9
10
11
12
GALLONS/FT
of WATER
0.041
0.163
0.367
0653
1 02
1 469
1.999
2611
3.305
408
4.934
5.875
In some situations, even with slow purge rates, a well may be pumped or bailed dry (evacuated)
In these situations, this generally constitutes an adequate purge and the well can be sampled following
sufficient recovery (enough volume to allow filling of all sample containers) It is not necessary that the
well be evacuated three times before it is sampled The pH, specific conductance, temperature, and
turbidity should be measured, during collection of the sample from the recovered volume, as the
measurements of record for the sampling event
Attempts should be made to avoid purging wells to dryness This can be accomplished, for
example, by slowing the purge rate If a well is pumped dry, it may result in the sample being comprised
partially of water contained in the sand pack, which may be reflective, at least in part, of initial, stagnant
conditions In addition, as water re-enters a well that is in an evacuated condition, it may cascade down
the sand pack or the well screen, stripping volatile organic constituents that may be present and/or
introducing soil fines into the water column
EISOPQAM
7-3
May 1996
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Equipment Available
Monitoring well purging is accomplished by using m-place plumbing and dedicated pumps or. b\
using portable pumps/equipment when dedicated systems are not present The equipment may consist of
a variety of pumps, including peristaltic, large and small diameter turbine (electric submersible), bladder,
centrifugal, gear-driven positive displacement, or other appropriate pumps. The use of any of these pumps
is usually a function of the depth of the well being sampled and the amount of water that is to be removed
during purging Whenever th= head difference between the sampling location and the water level is less
than the limit of suction and the volume to be removed is reasonably small, a peristaltic pump should be
used for purging Appendix E of this SOP contains the operating instructions for all pumps commonly used
during Branch ground water investigations
Bailers may also be used for purging in appropriate situations, however, their use is discouraged
Bailers tend to disturb any sediment that may be present in the well, creating or increasing sample turbidity
If a bailer is used, it should be a closed-top Teflon* bailer
722 Purging Techniques (Wells Without Plumbing or In-Place Pumps)
For permanently installed wells, the depth of water and depth of the well should be determined (if
possible) before purging. Electrical water level indicators/well sounders can be used for this purpose It
is standard practice to mark the top of casing, providing a point of reference from which these
measurements will be consistently made Field investigators should look for these markings when taking
these measurements Extreme caution should be exercised during this procedure to prevent cross-
contamination of the wells This is a critical concern when samples for trace organic compounds or metals
analyses are collected. At a minimum, the well sounding device should be cleaned by washing in a
laboratory detergent solution, followed b> rinses with tap water and analyte-free water. After cleaning,
n should be placed in a clean plastic bag or wrapped in foil
Purging with Pumps
When peristaltic pumps or centrifugal pumps are used, only the intake line is placed into the water
column The line placed into the water should be either standard-cleaned (see Appendix B) Teflon* tubing.
for peristaltic pumps, or standard-cleaned stainless steel pipe attached to a hose for centrifugal pumps
\\ hen submersible pumps (bladder, turbine, displacement, etc.) are used, the pump itself is lowered
mio the water column. The pump must be cleaned as specified in Appendix B
Purging with Bailers
Standard-cleaned (Appendix B) closed-top Teflon* bailers with Teflon* leaders and new nylon rope
are lowered into top of the water column, allowed to fill, and removed. The water is either discarded or
contained and managed as investigation derived waste It is critical that bailers be slowly and gently
immersed into the top of the water column, particularly during final stages of purging, to minimize
turbidity and disturbance of volatile organic constituents The use of bailers for purging and sampling is
discouraged because the correct technique is highly operator dependent.
EISOPQAM 7-4 May 1996
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Field Care of Purging Equipment
Regardless of which method is used for purging, new plastic sheeting should be placed on the
ground surface around the well casing to prevent contamination of the pumps, hoses, ropes, etc , in the
event they need to be placed on the ground during the purging or they accidentally come into contact with
the ground surface. It is preferable that hoses used in purging that come into contact with the ground water
be kept on a spool or contained in a plastic-lined tub, both during transporting and during field use. to
further minimize contamination from the transporting vehicle or ground surface.
Purging Entire Water Column
The pump/hose assembly or bailer used in purging should be lowered into the top of the standing
water column and not deep into the column This is done so that the purging will "pull" water from the
formation into the screened area of the well and up through the casing so that the entire static volume can
be removed If the pump is placed deep into the water column, the water above the pump may not be
removed, and the subsequent samples, particularly if collected with a bailer, may not be representative of
the ground water.
It is recommended that no more than three to five feet of hose be lowered into the water column
If the recovery rate of the well is faster than the pump rate and no observable draw down occurs, the pump
should be raised until the intake is within one foot of the top of the water column for the duration of
purging If the pump rate exceeds the recovery rate of the well, the pump will have to be lowered, as
needed, to accommodate the draw down. After the pump is removed from the well, all wetted portions
of the hose and the pump should be cleaned as outlined in Appendix B of this SOP.
Careful consideration shall be given to using pumps to purge wells which are excessively
contaminated with oily compounds, because it may be difficult to adequately decontaminate severely
contaminated pumps under field conditions When wells of this type are encountered, alternative purging
methods, such as bailers, should be considered
General Low Flow/Low Stress Method Preference
The device with the lowest pump or water removal rate and the least tendency to stress the well
during purging should be selected for use For example, if a bailer and a peristaltic pump both work in
a given situation, the pump should be selected because it will greatly minimize turbidity, providing a higher
qualit\ sample (Section 7.2 4 contains a description of low flow purging and sampling with a peristaltic
pump used in a temporary well) If a Fultz* pump or a Grundfos Redi-Flo2® could both be used, the Redi-
Flo2* may be given preference because the speed can be controlled to provide a lower pump rate, thereby
minimizing turbidity
Low Flow/Low Volume Purging Techniques/Procedures
Alternatives to the low flow purging procedures exist and may be acceptable The low flow/low
volume purging is a procedure used to minimize purge water volumes The pump intake is placed within
the screened interval at the zone of sampling, preferably, the zone with the highest flow rate. Low flow
rate purging is conducted after hydraulic conditions within the well have re-stabilized, usually within 24
to 48 hours Flow rates should not exceed the recharge rate of the aquifer. This is monitored by
measuring the top of the water column with a water level recorder or similar device while pumping These
techniques, however, are only acceptable under certain hydraulic conditions and are not considered
standard procedures.
E1SOPQAM 7-5 May 19%
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723 Purging Techniques - Wells with In-Place Plumbing
Wells with m-place plumbing are commonly found at municipal water treatment plants, industrial
water supplies, private residences, etc Many permanent monitoring wells at active facilities are also
equipped with dedicated, m-place pumps. The objective of purging wells with in-place pumps is the same
as with monitoring wells without m-place pumps, i.e., to ultimately collect a sample representative of the
ground water Among the types of wells identified in this section, two different approaches are necessary
The permanent monitoring wells with m-place pumps should, in all respects, be treated like the monitoring
well without pumps. They generally are sampled only occasionally and require purging as described for
wells without m-place pumps, i.e , 3 to 5 well volumes and stable parameters.
In the case of the other types of wells, however, not enough is generally known about the
construction aspects of the wells to apply the same criteria as used for monitoring wells, i.e., 3 to 5 well
volumes The volume to be purged in these situations, therefore, depends on several factors whether the
pumps are running continuously or intermittently and whether or not any storage/pressure tanks are located
between the sampling point and the pump. The following considerations and procedures should be
followed when purging wells with m-place plumbing under the conditions described.
Continuously Running Pumps
If the pump runs more or less continuously, no purge (other than opening a valve and allowing it
to flush for a few minutes) is necessary If a storage tank is present, a spigot, valve or other sampling point
should be located between the pump and the storage tank. If not, locate the valve closest to the tank
Measurements of pH, specific conductance, temperature, and turbidity are recorded at the time of
sampling
Intermittently Running Pumps
If the pump runs intermittently, it is necessary to determine, if possible, the volume to be purged,
including storage/pressure tanks that are located prior to the sampling location The pump should then be
run continuously until the required volume has been purged. If construction characteristics are not known.
best judgement should be used in establishing how long to run the pump prior to collecting the sample
Generally, under these conditions, 30 minutes will be adequate. Measurements of pH, specific
conductance, temperature and turbidity should be made and recorded at intervals during the purge and the
final measurements made at the time of sampling
724 Purging Techniques - Temporary Monitoring Wells
Temporary ground water monitoring wells differ from permanent wells because temporary wells
are installed in the ground water for immediate sample acquisition Wells of this type may include standard
well screen and riser placed in boreholes created by hand augermg, power augermg. or by drilling. They
max also consist of a rigid rod and screen that is pushed, driven, or hammered into place to the desired
sampling interval, such as the Direct Push Wellpomt*. the Geoprobe® and the Hydropunch® As such, the
efforts to remove several volumes of water to replace stagnant water do not necessarily apply in these
situations, because generally, stagnant water is non-existent It is important to note, however, that the
longer a temporary well is in place and not sampled, the more appropriate it may be to apply, to the extent
possible, standard permanent monitoring well purging criteria to it.
In cases where the temporary well is to be sampled immediately after installation, purging is
conducted primarily to mitigate the impacts of installation. In most cases, temporary well installation
EISOPQAM 7-6 May 1996
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procedures disturb the existing aquifer conditions, resulting primarily in increased turbidity Therefore.
the goal of purging is to reduce the turbidity and remove the volume of water in the area directly impacted
by the installation procedure Low turbidity samples in these types of wells are typically and routmeh
achieved by the use of low-flow purging and sampling techniques.
The following low-flow purging technique using peristaltic pumps has been used routine!) 10
achieve acceptably low NTU values in a variety of temporary monitoring well applications
In purging situations where the elevation of the top of the water column is no greater than approx-
imately 25 feet below the pump head elevation, a peristaltic pump may be used to purge temporary wells
Enough tubing is deployed to reach the bottom of the temporary well screen. At the onset of purging, the
tubing is slowly lowered to the bottom of the screen and is used to remove any formation material which
may have entered the well screen during installation. This is critical to ensuring rapid achievement of low
turbidity conditions. After the formation material is removed from the bottom of the screen, the tubing
is slowly raised through the water column to near the top of the column. The tubing can be held at this
level to determine if the pump is lowering the water level in the well If not, secure the tubing at the
surface to maintain this pumping level
If the water column is lowered, and the pump is not variable speed, continue to lower the tubing
as the water column is lowered If a variable speed peristaltic pump is being used and draw down is
observed on initiation of pumping, reduce the pump speed and attempt to match the draw down of the well
Sustained pumping at these slow rates will usually result in a relatively clear, low turbidity sample If the
draw down stabilizes, maintain that level, however, if it continues to lower, "chase" the water column until
the well is evacuated In this case, the recovered water column may be relatively free of turbidity and can
be sampled It may take several episodes of recovery to provide enough volume for a complete sample
With many of the direct push sampling techniques, no purging is conducted The sampling device
is simply pushed to the desired depth and opened and the sample is collected and retrieved
7.3 Sampling
Sampling is the process of obtaining, containerizing, and preserving the ground water sample after
the purging process is complete Non-dedicated pumps for sample collection generally should not be used
Many pumps are made of materials, such as brass, plastic, rubber, or other elastomer products which may
cause chemical interferences with the sample Their principle of operation may also render them
unacceptable as a sample collection device The pump may be turbine driven, which may release volatile
organic constituents It is recognized that there are situations, such as industrial or municipal supply wells
or private residential wells, where a well may be equipped with a dedicated pump from which a sample
would not normally be collected Discretion should always be used in obtaining a sample
7 3 1 Equipment Available
Because of the problems with most pumps described in the preceding paragraph, only three devices
should be used to collect ground water samples from most wells These are the peristaltic pump/vacuum
jug assembly, a stainless steel and Teflon* bladder pump, and a closed-top. Teflon* bailer
Other monitoring equipment used during sampling includes water level indicators, pH meters.
thermometers, conductivity bridges, and nephelometers
EISOPQAM 7-7 May 1996
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7 3.2 Sampling Techniques - Wells With In-Place Plumbing
Samples should be collected following purging from a valve or cold water tap as near to the well
as possible, preferably prior to any storage/pressure tanks that might be present Remove any hose thai
may be present before sample collection and reduce the flow to a low level to minimize sample disturbance.
particularly with respect to volatile organic constituents. Samples should be collected directly into the
appropriate containers (see Standard Sample Containers, Appendix A) Also, refer to the Potable Water
Supply discussion in Section 2 8 All measurements for pH, specific conductance, temperature, and
turbidity should be recorded at the time of measurement.
7 3.3 Sampling Techniques - Wells without Plumbing
Following purging, samples should be collected using a peristaltic pump/vacuum jug assembly, a
Teflon®/siainless steel bladder pump, or a closed-top Teflon* bailer. These techniques are described
below
Peristaltic pump/vacuum jug
The peristaltic pump/vacuum jug can be used for sample collection because it allows for sample
collection without the sample coming in contact with the pump tubing This is accomplished by placing
a Teflon* transfer cap assembly onto the neck of a standard cleaned 4-liter (1-gallon) glass container
Teflon* tubing (14-inch O.D ) connects the container to both the pump and the sample source The pump
creates a vacuum in the container, thereby drawing the sample into the container without it coming into
contact with the pump tubing
Samples for volatile organic compound analysis should be collected using a bailer or by filling the
Teflon* tube, by one of two methods, and allowing it to drain into the sample vials The tubing can be
momentarily attached to the pump to fill the rube with water After the initial water is discharged through
the pump head, the tubing is quickly removed from the pump and a gloved thumb placed on the tubing to
stop the water from draining out The tubing is then removed from the well and the water allowed to dram
into the sample vials Alternatively, the tubing can be lowered into the well the desired depth and a gloved
thumb placed over the end of the tubing This method will capture the water contained in the tubing It
can then be removed from the well and the water collected by draining the contents of the tubing into the
sample vials Under no circumstances should the sample for volatile organic compound analysis be
collected from the content of any other previously filled container. All equipment should be cleaned usinc
the procedures described in Appendix B Also, refer to the Potable Water Supply discussion. Section 2 2.
tor additional information
Bladder Pumps
After purging has been accomplished with a bladder pump, the sample is obtained directly from
the pump discharge If the discharge rate of the pump, during purging, is too great, so as to make sample
collection difficult, care should be taken to reduce the discharge rate at the onset of actual sample
collection This is necessary to minimize sample disturbance, particularly with respect to samples collected
for volatile organic compounds analysis
EISOPQAM 7-8 May 1996
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Bailers
When bailing, new plastic sheeting should be placed on the ground around each well to provide
a clean working area The nylon rope should be attached to the bailer via a Teflon* coated stainless steel
wire This coated wire is semi-permanently attached to the bailer and is decontaminated for reuse as the
bailer is cleaned The bailer should be gently immersed in the top of the water column until just filled
At this point, the bailer should be carefully removed and the contents emptied into the appropriate sample
containers.
734 Sample Preservation
Immediately after collection, all samples requiring preservation must be preserved with the
appropriate preservative. Consult Appendix A for the correct preservative for the particular analytes of
interest All samples preserved using a pH adjustment (except VOCs) must be checked, using pH strips,
to ensure that they were adequately preserved This is done by pouring a small volume of sample over the
strip Do not place the strip in the sample
735 Special Sample Collection Procedures
Trace Organic Compounds and Metals
Special sample handling procedures should be instituted when trace contaminant samples are being
collected All sampling equipment, including pumps, bailers, water level measurement equipment, etc .
which comes into contact with the water in the well must be cleaned in accordance with the cleaning
procedures described in Appendix B Pumps should not be used for sampling, unless the interior and
exterior portions of the pump and the discharge hoses are thoroughly cleaned Blank samples should be
collected to determine the adequacy of cleaning prior to collection of any sample using a pump
Filtering
Asa standard practice, ground water samples will not be filtered for routine analysis Filtering
will usually only be performed to determine the fraction of major ions and trace metals passing the filter
and used for flow system analysis and for the purpose of geochemical speciation modeling Filtration is
not allowed to correct for improperly designed or constructed monitoring wells, inappropriate sampling
methods, or poor sampling technique
When samples are collected for routine analyses and are filtered, such as under conditions of
excessive turbidity, both filtered and non-filtered samples will be submitted for analyses Samples for
organic compounds analysis should not be filtered Prior to filtration of the ground water sample for
an\ reason other than geochemical speciation modeling, the following criteria must be demonstrated to
jusuf) the use of filtered samples for inorganic analysis
1 The monitoring wells, whether temporary or permanent, have been constructed and
developed in accordance with Section 6.
2 The ground water samples were collected using sampling techniques in accordance with
this section, and the ground water samples were analyzed in accordance with US-EPA
approved methods.
EISOPQAM 7-9 May 1996
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Efforts have been undertaken to minimize any persistent sample turbidity problems These
efforts may consist of the following
• Redevelopment or re-installation of permanent ground water monitoring wells
• Implementation of low flow/low stress purging and sampling techniques
Turbidity measurements should be taken during purging and sampling to demonstrate
stabilization or lack thereof These measurements should be documented in the field notes
If the ground water sample appears to have either a chemically-induced elevated turbidity, such
as would occur with precipitate formation, or a naturally elevated colloid or fine, paniculate-related
turbidity, filtration will not be allowed
If filtration is necessary for purposes of geochemical modeling or other pre-approved cases, the
following procedures are suggested
1 Accomplish in-line filtration through the use of disposable, high capacity filter cartridges
(barrel-type) or membrane filters in an in-line filter apparatus. The high capacity, barrel-
type filter is preferred due to the higher surface area associated with this configuration
If a membrane filter is utilized, a minimum diameter of 142 mm is suggested
2 Use a 5 /im pore-size filter for the purpose of determining the colloidal constituent
concentrations A 0.1 fim pore-size filter should be used to remove most non-dissolved
particles
3 Rinse the cartridge or barrel-type filter with 500 milliliters of the solute (ground water to
be sampled) prior to collection of sample If a membrane filter is used, rinse with 100
milliliters of solute prior 10 sample collection.
Potential differences could result from variations in filtration procedures used to process water
samples for the determination of trace element concentrations. A number of factors associated with
filtration can substantially alter "dissolved" trace element concentrations; these include filter pore size.
filter type, filter diameter, filtration method, volume of sample processed, suspended sediment
concentration, suspended sediment gram-size distribution, concentration of colloids and colloidally-
associated trace elements, and concentration of organic matter. Therefore, consistency is critical m the
comparison of short-term and long-term results Further guidance on filtration may be obtained from the
following I) Metals in ground Water Sampling Artifacts and Reproducibilitv (3): 2) Filtration of Ground
\\ater Sgmples for MetalS Analysis (4). and 3) Ground Water Sampling - A Workshop Summary (5).
Bacterial Sampling
Whenever wells (normally potable wells) are sampled for bacteriological parameters, care must
be taken to ensure the sterility of all sampling equipment and all other equipment entering the well. Fur-
ther information regarding bacteriological sampling is available in the following: 1) Sampling for Organic
Chemicals and Microorganisms in the Subsurface (6), 2) Handbook for Evaluating Water Bacteriological
Laboratories (7). and 3) Microbiological Methods for Monitoring the Environment. Water and Wastes (8)
EISOPQAM 7 - 10 May 1996
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736 Specific Sampling Equipment Quality Assurance Techniques
All equipment used to collect ground water samples shall be cleaned as outlined in Appendix B and
repaired, if necessary, before being stored at the conclusion of field studies Cleaning procedures utilized
in the field (Appendix B), or field repairs shall be thoroughly documented in field records
737 Auxiliary Data Collection
During ground water sample collection, it is important to record a variety of ground water related
data Included in the category of auxiliary data are water level measurements, well volume determinations.
pumping rates during purging, and occasionally, drillers or boring logs. This information should be
documented in the field records Well volume determinations are described in Section 7.2 1
Water Level Measurements
Water table measurements from the top of the well casings (referenced to National Geodetic
Vertical Datum) in permanent wells, and ground surface elevations in temporary wells should be made to
assist in determining the general direction of ground water flow and gradient. The methodology to be used
to determine well water levels are given in Section 15.8 Tracer dyes and radioactive and thermal detection
methods can be used to determine direction and velocities of flow (9). Also, a study of the general
topography and drainage patterns will generally indicate direction of ground water flow
The ground surface elevation and top of casing elevation at the wells should be determined by
standard engineering survey practices as outlined in Section 15
Well Pumping Rate - Bucket/Stop Watch Method
The pumping rate for a pump can be determined by collecting the discharge from the pump in a
bucket of known volume and timing how long it takes to fill the bucket The pumping rate should be in
gallons per minute This method shall be used primarily with pumps with a constant pump rate, such as
gasoline-powered or electric submersible pumps. Care should be taken when using this method with some
battery-powered pumps. As the batteries' charge decreases, the pump rate also decreases so that pumping
rate calculations using initial, high pump rates may be erroneously high. If this method is used with
battery-powered pumps, the rate should be re-checked frequently to ensure accuracy of the pumping rate
calculations
EISOPQAM 7-11 May 1996
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7.4 References
1 US EPA., RCRA Ground-Water Monitoring- Draft Technical Guidance. November 1992. Office
of Solid Waste, EPA/530-R-93-001
2 US EPA , Test Methods for Evaluating Solid Waste, volume II- Field Manual. Physical/Chemical
Methods. November 1986. Office of Solid Waste and Emergency Response, SW-846
3 Puls. Robert W., Don A Clark, and Bert Bledsoe. Metals in Ground Water Sampling Artifacts
and Reproducibility Hazardous Waste and Hazardous Materials 9(2): 149-162 (1992)
4 Puls, Robert W , and Michael J. Barcelona, filtration of Ground Water Samples for Meials
Analysis Hazardous Waste and Hazardous Materials 6(4): 385-393 (1989).
5 Ground Water Sampling - A Workshop Summary. Proceedings from the Dallas, Texas November
30 - December 2, 1993 Workshop US EPA Office of Research and Development Robert S Kerr
Environmental Research Laboratory. EPA/600/R-94/205, January 1995
6 Sampling for Organic Chemicals and Microorganisms in the Subsurface. US EPA, EPA-600/2-
77/176(1977)
7 Handbook for Evaluatmp Waier Bacteriological Laboratories US EPA, ORD, Municipal
Environmental Research Laboratory, Cincinnati, Ohio, 1975.
8 Microbiological Methods for Monitoring the Environment. Water and Wastes US EPA, ORD.
Environmental Momiormg and Support Laboratory, Cincinnati, Ohio, 1978
9 "Groundwater". Section 18. USDA-SCS National Engineering Handbook United States
Department of Agriculture. Soil Conservation Service, 1978
EISOPQAM 7 . 12
May 1996
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SECTION 8
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SECTION 8
SAMPLING OF POTABLE WATER SUPPLIES
PERFORMANCE OBJECTIVES:
• To collect a sample representative of the drinking water supply.
• To reduce the bias of system related variables (pumps, piping, holding tanks, etc.)
8.1 Introduction
The same sampling techniques used for wastewater, ground water, surface water, etc , (including
thorough documentation of location, date, time, etc.) are to be used during potable water supply sampling
There are certain additional procedures which apply.
8.2 Sampling Site Selection
The following should be considered when choosing the location to collect a potable water sample
• Taps selected for sample collection should be supplied with water from a service pipe
connected directly to a water main in the segment of interest.
Whenever possible, choose the tap closest to the water source, and prior to the water lines
entering the residence, office, building, etc., and also prior to any holding or pressunzation
tanks
• The sampling tap must be protected from exterior contamination associated with being too
close to a sink bottom or to the ground Contaminated water or soil from the faucet exterior
may enter the bottle during the collection procedure since it is difficult to place a bottle under
a low tap without grazing the neck interior against the outside faucet surface. If the tap is too
close to the ground for direct collection into the appropriate container, it is acceptable to use
a smaller (clean) container to transfer sample to a larger container.
• Leaking taps that allow water to discharge from around the valve stem handle and down the
outside of the faucet, or taps in which water tends to run up on the outside of the lip, are to
be avoided as sampling locations
• Disconnect any hoses, filters, or aerators attached to the tap before sampling. These devices
can harbor a bacterial population if they are not routinely cleaned or replaced when worn or
cracked
• Taps where the water flow is not constant should be avoided because temporary fluctuation in
line pressure may cause clumps of microbial growth that are lodged in a pipe section or faucet
connection to break loose A smooth flowing water stream at moderate pressure without
splashing should be used The sample should be collected without changing the water flow
It may be appropriate to reduce the flow for the volatile organic compounds aliquot to
minimize sample agitation.
EISOPQAM 8-1 May 1996
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Occasionally, samples are collected to determine the contribution of system related variables (e g .
transmission pipes, water coolers, water heaters, holding tanks, pressurization tanks, etc.) to the quality
of potable water supplies In these cases, it may be necessary to insure that the water source has not been
used for a specific time interval (e g , over a weekend or a three- or four-day holiday period) Sample
collection may consist of collecting a sample of the initial flush, collecting a sample after several minutes.
and collecting another sample after the system being investigated has been completely purged
When sampling for bacterial content, the sample container should not be rinsed before use due to
possible contamination of the sample container or removal of the thiosulfate dechlonnating agent (if used)
When filling any sample container, care should be taken that so splashing drops of water from the ground
or sink do not enter into either the bottle or cap
When sampling at a water treatment plant, samples are often collected from the raw water supply
and the treated water after chlonnation
Obtain the name(s) of the resident or water supply owner/operator, the resident's exact mailing
address, and the resident's home and work telephone numbers. The information is required so that the
residents or water supply owner/operators can be informed of the results of the sampling program (See
Section 2 2)
Sampling Technique (1)
The following procedures should be followed when collecting samples from potable water supplies-
1 Purge the system for at least 15 minutes Ideally, the sample should be collected from a tap
or spigot located at or near the well head or pump house and before the water supply is
introduced into any storage tanks or treatment units. If the sample must be collected at a point
in the water line beyond a pressurization or holding tank, a sufficient volume of water should
be purged to provide a complete exchange of fresh water into the tank and at the location
where the sample is collected If the sample is collected from a tap or spigot located just
before a storage tank, spigots located inside the building or structure should be turned on to
prevent any backflow from the storage tank to the sample tap or spigot It is general!)
advisable to open as many taps as possible during the purge, to ensure a rapid and complete
exchange of water in the tanks.
2 After purging for 15 minutes, measure the turbidity (if appropriate), pH, specific
conductivity, and temperature of the water Continue to monitor these parameters until three
consistent readings are obtained
3 After three consistent readings have been obtained, samples may be collected
EISOPQAM 8-2 May 1996
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8.3 Reference
Sampling for Organic Chemicals and Microorganisms in the Subsurface. United Slates
Environmental Protection Agency, EPA-600/2-77-176, 1977.
EISOPQAM 8-3 May 1996
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SECTION 9
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SECTION 9
WASTEWATER SAMPLING
SECTION OBJECTIVE:
• To provide guidance for the proper collection of wastewater samples.
9.1 Introduction
The variety of conditions at different sampling locations require that considerable judgment be
exercised regarding the methodologies and procedures for the collection of representative samples of
wastewater Each sampling location warrants attention commensurate with its complexity. There are,
however, basic rules and precautions generally applicable to sample collection. Acceptable procedures are
generally those outlined in the NPDES Compliance Inspection Manual (1). Some important considerations
for obtaining a representative wastewaier sample include:
• The sample should be collected where the wastewater is well mixed. Therefore, the sample
should be collected near the center of the flow channel, at approximately 40 to 60 percent of
the water depth, where the turbulence is at a maximum and the possibility of solids settling is
minimized Skimming the water surface or dragging the channel bottom should be avoided
However, allowances should be made for fluctuations in water depth due to flow variations
• In sampling from wide conduits, cross-sectional sampling should be considered. Rhodamme
WT dye (See Section 15 7 for procedures) may be used as an aid in determining the most
representative sampling locations
• !f manual compositing is employed, the individual sample portions must be thoroughly mixed
before pouring the individual aliquots into the composite container. For manual composite
sampling, the individual sample aliquots should be preserved at the time of sample collection
(2)
• When collecting samples or installing sampling equipment, field investigators should always
wear a new pair of the appropriate protective gloves (disposable latex gloves, rubber gloves,
etc ) to prevent contamination of the sample and reduce exposure to hazardous substances
EISOPQAM 9-1 May 1996
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9.2 Site Selection
Where applicable, wasiewater samples should be collected at the location specified in the NPDES
permit (if the source has such a permit) In some instances the sampling location specified in the permit.
or the location chosen by the permittee, may not be acceptable for the collection of a representative waste-
water sample In such instances, the investigator is not limited by permit specifications and may collect
a sample at a more representative location When a conflict exists between the permittee and the regulatory
agency regarding the most representative sampling location, both sites should be sampled, and the reason
for the conflict should be noted in the inspection or study report and field notes Recommendations and
reasons for a change in sampling locations should be given to the appropriate permitting authority
9 2 1 Influent
Influent wastewaters are preferably sampled at locations of highly turbulent flow in order to ensure
good mixing, however, in many instances the most desirable location is not accessible. Preferable influent
wastewater sampling locations include 1) the upflow siphon following a comminutor (in absence of grit
chamber), 2) the upflow distribution box following pumping from main plant wet well, 3) aerated grit
chamber, 4) flume throat; 5) pump wet well when the pump is operating; or 6) downstream of preliminary
screening When possible, influent samples should be collected upstream from sidestream returns
922 Effluent
Effluent samples should be collected at the site specified in the permit, or if no site is specified in
the permit, at the most representative site downstream from all entering wastewater streams prior to
discharge into the receiving waters If a conflict exists between the permittee and inspector regarding the
source being sampled or the location of the most representative site, follow the procedures previously
described under "Site Selection"
923 Pond and Lagoon Sampling
Generally, composite effluent wastewater samples should be collected from ponds and lagoons
Even if the ponds or lagoons have long retention times, composite sampling is necessary because of the
tendency of ponds and lagoons to have flow paths that short circuit and changes the design detention time
EISOPQAM 9-2 May 1996
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9.3 Sample Types
For NPDES sampling, two types of sampling techniques are used: grab and composite For these
procedures, the NPDES permn specifies the appropriate sample type. A complete description of all
NPDES sampling procedures and techniques is presented in the NPDES Compliance Inspection Manual
(1)
9 3 1 Grab Samples
Grab samples consist of either a single discreet sample or individual samples collected over a
period of time not to exceed 15 minutes. The grab sample should be representative of the wastewaier
conditions at the time of sample collection The sample volume depends on the type and number of
analyses to be performed
932 Composite Samples
Composite samples are collected over time, either by continuous sampling or by mixing discrete
samples A composite sample represents the average wastewater characteristics during the compositing
period Various methods for compositing are available and are based on either time or flow proportioning
The choice of a flow proportional or time composite sampling scheme depends on the permit requirements.
variability of the wastewater flow or concentration of pollutants, equipment availability, and sampling
location The investigator must know each of these criteria before a sampling program can be initiated
If an investigator knows or suspects that there is significant variability in the wastewater flow or if the
investigator knows nothing about the facility, a flow proportional sample is preferable Otherwise, a time
composite sample would be acceptable
A time composite sample consists of equal volume discrete sample ahquots collected at constant
time intervals into one container A time composite sample can be collected either manually or with an
automatic sampler
A flow proportional composite sample can be collected using one of two methods One method
consists of collecting a constant sample volume at varying time intervals proportional to the wastewater
flow For the other method, the sample is collected by varying the volume of each individual aliquot
proportional to the flow, while maintaining a constant time interval between the aliquots Prior to collecting
flow proportional samples, the facility's flow measuring system should be examined for proper installation
and accuracy (see Section 18) If the facility's primary flow measuring device does not meet standard
conditions (see Section 18). or is in an unsafe or inaccessible location, then the investigator may collect
time composite samples If the flow measurement system is acceptable, samples should be collected using
the appropriate flow proportioning methods
Flow proportional samples can be collected with an automatic sampler and a compatible flow
measuring device, semi-automatically with a flow chart and an automatic sampler capable of collecting
discrete samples, or manually
EISOPQAM 9-3 May 1996
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9.4 Use of Automatic Samplers
9 4 1 Introduction
Automatic samplers may be used to collect composite or grab samples when several aliquots are
to be collected at frequent intervals or when a continuous sample is required. For composite sampling
applications, the automatic samplers may be used to collect time composite or flow proportional samples
In the flow proportional mode, the samplers are activated by a compatible flow meter. Flow proportional
samples can also be collected using an automatic sampler equipped with multiple containers and manually
compositing the individual sample portions proportional to the flow (1).
Automatic samplers must meet the following requirements.
• Sampling equipment must be properly cleaned to avoid cross-contamination which could result
from prior use (see Appendix B for cleaning procedures)
• No plastic or metal parts of the sampler shall come in contact with the water or wastewater
stream when parameters to be analyzed could be impacted by these materials
• The automatic sampler must be capable of providing adequate refrigeration during the
sampling period. This can be accomplished in the field by using ice.
• The automatic sampler must be able to collect a large enough sample for all parameter
analyses
• The individual sample aliquot must be at least 100 mis
• The automatic sampler should be capable of providing a lift of at least 20 feet and the sampler
should be adjustable since the volume is a function of the pumping head
• The pumping velocity must be at least 2 Msec to transport solids and not allow solids to settle
• The intake line leading to the pump must be purged before each sample is collected
• The minimum inside diameter of the intake line should be 1/4 inch.
• An adequate power source should be available to operate the sampler for the time required to
complete the project Facility electrical outlets may be used if available
• Facility automatic samplers should only be used if 1) field conditions do not allow for the
installation of EPA sampling equipment, and 2) the facility sampling equipment meets all of
the requirements of this SOP
Specific operating instructions, capabilities, capacities, and other pertinent information for
automatic samplers are included in the respective operating manuals.
EISOPQAM 9.4 May 1996
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942 Conventional Sampling (Inorganic Parameters)
Conventional sampling includes all inorganic parameters (e.g , BOD5, TSS, COD, nutrients, and
metals) that can be collected using an automatic sampler.
New tubing (Silastic*. or equal, in the pump and either Teflon8 or Tygon®, or equal, in the sample
train) will be used for each sampler installation.
Installation procedures include cutting the proper length of tubing, positioning it in the wastewater
stream, and sampler programming Protective gloves should be worn to reduce exposure and to maintain
the integrity of the sample
For a time composite sample, the sampler should be programmed to collect at least 100-miIliliter
aliquots at a frequency that provides a representative sample and enough sample volume to conduct all
required analyses
For a flow proportional sample, the sampler should be programmed to collect a minimum of 100
milliluers for each sample aliquot with the interval predetermined based on the flow of the monitored
stream
At the end of the compositing period, the sample collected should be properly mixed and
transferred into the respective containers, followed by immediate preservation, if required. For routine
inspections, the permittee should be offered a split sample
943 Metals
When an automatic sampler is used for collecting samples for metals analyses, the entire sampler
collection system should be rinsed with orgamc/analyte free water, and an equipment blank should be
collected Approximately one gallon of rinse water should be pumped through the sample tubing into the
composite container and discarded Nitric acid must be added to the metals blank container for proper
preservation The sampler may then be positioned in the appropriate location and the sampler program
initiated
If the sampler tubing is attached to a metal conduit pipe, the sampler intake tubing should be
carefully installed upstream and away from the conduit to prevent metals contamination This can be
accomplished by clamping the tubing upstream of the conduit using laboratory clamps and wrapping the
submerged portion of conduit pipe with a protective barrier (e.g., duct tape).
944 Extractable Organic Compounds. Pesticides, and PCBs
When an automatic sampler is used for collecting samples for the analyses of extractable organic
compounds, pesticides, and/or PCBs. the installation procedures include cutting the proper length of new
Teflon* tubing, rinsing of the entire sampler collection system with orgamc/analyte free water, and
collection of appropriate blanks for organic compounds analysis. For the organic/analyte free water rinse.
approximately one-half gallon is initially pumped into the composite sample container and discarded. An
additional one and one-half gallons are then pumped into the composite sample container for distribution
into the appropriate blank container Finally the collection tubing should be positioned in the wastewater
stream and the sampler programmed and initiated.
EISOPQAM 9-5 May 1996
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945 Automatic Sampler Security
Field investigators should take whatever steps are necessary to prevent tampering with EPA
equipment A lock or custody seal may be placed on the sampler to detect tampering. However, this does
not prevent tampering with the sample collection tubing. If necessary, seals may be placed on the sampling
pole and tubing line to further reduce tampering possibilities
946 Auiomatic Sampler Maintenance, Calibration, and Quality Control
To insure proper operation of automatic samplers, and thus the collection of representative samples,
the following maintenance and calibration procedures should be used and any deviations should be
documented m the log book
Prior to being used, the sampler operation will be checked by Field Equipment Center personnel
This includes operation (forward, reverse, automatic) through three cycles of purge-pump-purge, checking
desiccant and replacing if necessary, checking the 12-volt batteries to be used with the sampler, and
repairing any item if necessary
During each field trip, prior to initiating the automatic sampler, the rinse and purge-pump-purge
cycle shall be checked at least once The pumping volume should be checked at least twice using a
graduated cylinder or other calibrated container prior to initiating the sampler. For flow proportional
sampling, the flow pacer that activates the sampler should be checked to insure that it operates properly
Upon return from a field trip, the structural integrity of the sampler should be examined and
repaired, if necessary The desiccant will be checked and replaced if appropriate The operation (forward.
reverse, automatic, etc ) will be checked and any required repairs will be made and documented. The
sampler will then be cleaned as outlined in Appendix B
The automatic sampler should be checked against the manufacturer's specifications and documented
whenever one or more of the sampler functions appears to be operating improperly
9.5 Manual Sampling
Manual sampling is normally used for collecting grab samples and/or for immediate m-siru field
analyses However, it can also be used in lieu of automatic equipment over extended periods of time for
composite sampling, especially when it is necessary to evaluate unusual waste stream conditions
The best method to manually collect a sample is to use the actual sample container which will be
used to transport the sample to the laboratory This eliminates the possibility of contaminating the sample
w ith intermediate collection containers If the water or wastewater stream cannot be physically reached
b> the sampling personnel or it is not safe to reach for the sample, an intermediate collection container may
be used, from which the sample can be redistributed to other containers If this is done, however, the
container used to collect the sample must be properly cleaned (Appendix B) and must be made of a material
that meets the requirements of the parameter(s) being investigated Samples for oil and grease, bacteria,
phenols, volatile organic compounds, and sulfides analyses must always be collected directly into the
sample container.
In some cases it may be best to use a pump, either power or hand operated, to withdraw a sample
from the water or wastewater stream If a pump is used, it is imperative that all components of the pump
that come in contact with the sample are properly cleaned (Appendix B) to insure the integrity of the
EISOPQAM 9.6 May
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sample
In general, samples are manually collected by first selecting a location in the wastestream that is
well mixed (Section 9.1) then dipping the container in the water or wastewater stream so the mouth of the
container faces upstream The container should not be overfilled if preservatives are present in the
container
9.6 Special Sample Collection Procedures
9 6 1 Organic Compounds and Metals
Trace organic compounds and metals detection limits are usually in the parts per billion or parts
per trillion range, so extreme care must be exercised to insure sample integrity.
All containers, composite bottles, tubing, etc., used for sample collection for trace organic
compounds and metals analyses should be prepared as described in Appendix B
When possible, the sample should be collected directly into the appropriate sample container If
the material to be sampled cannot be physically reached, an intermediate collection device may be used
This should be a Teflon®, glass, or stainless steel vessel on a pole or rope or Teflon* tubing via a peristaltic
rype pump and a Teflon* vacuum container attachment which converts a sample container into a vacuum
container The device which is used should be cleaned as described in Appendix B.
962 Bacteriological
Samples for bacteriological analyses must always be collected directly into the prepared glass or
plastic sample container. The sample container should be kept unopened until it is to be filled When the
cap is removed, care should be taken not to contaminate the cap or the inside of the bottle The bottle
should be held near the base and filled to within about one inch of the top without rinsing and recapped
immediately During sample collection, the sample container should be plunged with the neck partially
below the surface and slightly upward The mouth should be directed against the current Appendix A
lists preservation procedures and holding times
When the sample container must be lowered into the waste stream, either because of safety or
impracticality (manhole, slippery effluent area, etc }, care must be taken to avoid contamination
963 Immiscible Liquids/Oil and Grease
Oil and grease may be present in wastewater as a surface film, an emulsion, a solution, or as a
combination of these forms Since it is very difficult to collect a representative sample for oil and grease
analysis, the inspector must carefully evaluate the location of the sampling location The most desirable
sampling location is the area of greatest mixing Quiescent areas should be avoided The sample container
should be plunged into the wastewater using a swooping motion with the mouth facing upstream Care
should be taken to insure that the bottle does not over fill during sample collection.
Because losses of oil and grease will occur on sampling equipment, an automatic sampler should
not be used to collect samples for oil and grease analysis Individual portions collected at prescribed time
intervals must be analyzed separately to obtain the average concentrations over an extended period
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EISOPQAM 9-8 May 1996
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964 Volatile Organic Compounds
Samples to be analyzed for volatile organic compounds (VOCs) should be collected in 40-ml
septum vials with screw caps with a Teflon* lined silicone disk in the cap to prevent contamination of the
sample by the cap The disks should be placed in the caps (Teflon* side to be in contact with the sample)
in the laboratory prior to the beginning of the sampling program.
When sampling for VOCs. triplicate samples should always be collected from each location The
investigator should determine if the water to be sampled contains chlorine. If the water contains no
chlorine, three pre-preserved 40-ml vials should be filled with the sample. The samples may be held for
up to 14 days before analysis When preservation is not feasible, samples can be held up to 7 days before
analysis
If the water contains chlorine, fill an 8-ounce sampling container with 2 drops of a 25% ascorbic
acid solution and the water sample Cap and mix thoroughly but gently by swirling to eliminate residual
chlorine Transfer the sample to three pre-preserved 40-ml vials (see Appendix A) The ascorbic acid and
preservative must be added in this order and in two separate steps.
The 40-ml vials should be completely filled to prevent volatilization, and extreme caution should
be exercised when filling each vial to prevent any turbulence which could also produce volatilization The
sample should be carefully poured down the side of the vial to minimize turbulence. As a rule, it is best
to gently pour the last few drops into the vial so that surface tension holds the water in a "convex
meniscus " The cap is then applied and some overflow is lost, but air space in the bottle is eliminated
After capping, turn the bottle over and tap it to check for bubbles, if any are present, repeat the procedure
using a new 40-ml vial.
Sampling containers with preservatives should be prelabeled (i.e., P) prior to any field activities
This will reduce the chances of confusion during sampling activities by the investigation team Sample
preservation, containers, holding times, and sample volumes are listed in Appendix A
9.7 Special Process Control Samples and Tests
During diagnostic evaluations, process control tests may be conducted to evaluate and troubleshoot
the performance of the biological treatment processes of a municipal or industrial wastewater treatment
facilitN The EPA Activated Sludge Process Control Testing handbook is the standard reference for
activated sludge process control testing (3) The manual includes a complete description of the step-by-step
procedures for each test and the interpretation of the results The six basic activated sludge process control
tests are
• Sludge settleability (settlometer)
• Centrifuge spins
Aeration basin DO profiles
• Oxygen uptake rate (OUR) measurements
• Mixed liquor microscopic examinations
• Sludge blanket depth (SBD) measurements
Additional references are available that provide a more comprehensive evaluation of the methods
used to conduct a diagnostic evaluation (4, 5, 7, 8. and 9) Completion of the Sacramento Operation of
\h astewater Treatment Plants course is highly recommended for all personnel prior to serving as the project
leader on a Diagnostic Evaluation (6).
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EISOPQAM 9 - 10 May 1996
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9.8 Supplementary Data Collection
While conducting wastewater sampling, the following information will also be obtained (it
applicable)
• Field measurements -- pH, dissolved oxygen, conductivity, and temperature (see Section
16 for standard field analytical techniques).
• Flows associated with the samples collected ~ continuous flows with composite samples
and instantaneous flows with grab samples (Section 18).
• Diagrams and/or written descriptions of the wastewater treatment systems (if available)
• Photographs of pertinent wastewater associated equipment, such as flow measuring
devices, treatment units, etc (keep photolog as specified in section 3.2)
• Process control information on the wastewater treatment process (if applicable)
• Completion of applicable forms required during specific investigations
All observations, measurements, diagrams, etc., will be entered in bound field logbooks or attached
thereto (where applicable as specified in Section 3.5).
EISOPQAM 9-11 May 1996
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9.9 References
1 NPDES Compliance Inspection Manual. United States Environmental Protection Agent \
Office of Environment and Compliance Assurance, September 1994
2 Code of Federal Regulations. 40 CFR. Part 136.3, Table II, (latest issue)
3 US-EPA. "Activated Sludge Process Control Testing", ESD, Water Compliance Unit. Athens.
GA. 1990.
4 US-EPA, "Process Control Manual Aerobic Biological Treatment Facilities MD-14", EPA
430/09-77-006, Office of Water. Washington, D.C., 1977
5 Metcalf and Eddy, Inc . "Wastewater Engineering: Treatment, Disposal, Reuse", McGraw-
Hill Book Co., New York. NY, 1991.
6 California State University - Sacramento, "Operation of Wastewater Treatment Plants -
Volumes I. II, III", Sacramento, California.
7 US-EPA, "Retrofitting POTWs". EPA 625/6-89/020, Center for Environmental Research
Information, Cincinnati. Ohio. 1989
8 "Operation Of Municipal Wastewater Treatment Plants", WEF Manual Of Practice No. 11,
Water Pollution Control Federation, Alexandria, Virginia, 1990
9 "Design Of Municipal Wastewater Treatment Plants", WEF Manual Of Practice No 8, Book
Press. Inc.. Brattleboro. Vermont. 1991
EISOPQAM 9-12 May 1996
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SECTION 10
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SECTION 10
SURFACE WATER SAMPLING
PERFORMANCE OBJECTIVE:
• To collect a representative sample of the surface water of interest
10.1 Introduction
Surface water sampling techniques and equipment are designed to minimize effects on the chemical
and physical integrity of the sample If the guidance provided in this section is followed, a representative
sample of the surface water should be obtained
The physical location of the investigator when collecting a sample may dictate the equipment to
be used If surface water samples are required, direct dipping of the sample container into the stream is
desirable This is possible, however, only from a small boat, a pier, etc., or by wading in the stream
Wading, however, may cause the re-suspension of bottom deposits and bias the sample Wading is
acceptable if the stream has a noticeable current (is not impounded), and the samples are collected while
facing upstream If the stream is too deep to wade, or if the sample must be collected from more than one
water depth, or the sample must be collected from a bridge, etc., supplemental sampling equipment must
be used
10.2 Surface Water Sampling Equipment
1021 Dipping Using Sample Container
A sample may be collected directly into the sample container when the surface water source is
accessible by wading or other means The sampler should face upstream and collect the sample without
disturbing the sediment The surface water sample should always be collected prior to a sediment sample
at the same location The sampler should be careful not to displace the preservative from a pre-preserved
sample container such as the 40-ml VOC vial
1022 Scoops
Stainless steel scoops are useful for reaching out into a body of water to collect a surface water
sample The scoop may be used directly to collect and transfer a surface water sample to the sample
container, or it may be attached to an extension in order to access the selected sampling location The
scoop is one of the most versatile sampling tools available to the field investigator.
1023 Peristaltic Pumps
Another device that can be effectively used to sample a water column is the peristaltic
pump/vacuum jug system. The use of a metal conduit to which the tubing is attached, allows for the
collection of a vertical sample (to about a 25 foot depth) which is representative of the water column
Commercially available pumps vary in size and capability, with some being designed specifically for the
simultaneous collection of multiple water samples.
EISOPQAM 10 - 1 May 1996
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EISOPQAM 10 - 2 May 1996
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10 2 4 Discrete Depth Samplers
When discrete samples are desired from a specific depth, and the parameters to be measured do
not require a Teflon* coated sampler, a standard Kemmerer or Van Dorn sampler may be used The
Kemmerer sampler is a brass cylinder with rubber stoppers that leave the ends of the sampler open while
being lowered in a vertical position, thus allowing free passage of water through the cylinder The Van
Dorn sampler is plastic and is lowered in a horizontal position. In each case, a messenger is sent down
a rope when the sampler is at the designated depth, to cause the stoppers to close the cylinder, which is
then raised Water is removed through a valve to fill respective sample containers With a rubber rube
attached to the valve, dissolved oxygen sample bottles can be properly filled by allowing an overflow of
the water being collected With multiple depth samples, care should be taken not to stir up the bottom
sediment and thus bias the sample
1025 Bailers
Teflon* bailers may also be used for surface water sampling, if the study objectives do not
necessitate a sample from a discrete interval of the water column A closed top bailer with a bottom check-
valve is sufficient for many studies As the bailer is lowered through the water column, water is
continually displaced through the bailer until the desired depth is reached, at which point the bailer is
retrieved This technique may not be successful where strong currents are found
1026 Buckets
A plastic bucket can be used to collect samples for in-situ analyses, e.g., pH, temperature and
conductivity However, the bucket should be rinsed twice with the sample water prior to collection of the
sample
EISOPQAM 10 - 3 May 1996
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SECTION 11
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SECTION 11
SEDIMENT SAMPLING
PERFORMANCE OBJECTIVE
To collect a representative sample of sediment from a surface water body
11.1 Introduction
Sampling techniques and equipment are designed to minimize effects on the chemical and physical
integrity of the sample. If the guidance in this section is followed, a representative sample of the sediment
should be obtained
The physical location of the investigator when collecting a sample may dictate the equipment to
be used Wading is the preferred method for reaching the sampling location, particularly if the stream has
a noticeable current (is not impounded) However, wading may disrupt bottom sediments causing biased
results If the stream is too deep to wade, the sediment sample may be collected from a boat or from a
bridge
To collect a sediment sample from a streambed, a variety of methods can be used
Dredges (Peterson, Eckman. Ponar),
• Coring (tubes, augers)
• Scoops (BMH-60. standard scoop) and spoons
Regardless of the method used, precautions should be taken to insure that the sample collected is
representative of the streambed These methods are discussed in the following paragraphs
11.2 Sediment Sampling Equipment
1121 Scoops and Spoons
If the surface water body is wadeable. the easiest way to collect a sediment sample is by using a
stainless steel scoop or spoon The sampling method is accomplished by wading into the surface water
bod\ and while facing upstream (into the current), scooping the sample along the bottom of the surface
water body in the upstream direction Excess water may be removed from the scoop or spoon However,
this may result in the loss of some fine panicle size material associated with the bottom of the surface water
bod> Aliquots of the sample are then placed in a glass pan and homogenized according to the quartering
method described in Section 5.13.8 of this SOP.
In surface water bodies that are too deep to wade, but less than eight feet deep, a stainless steel
scoop or spoon attached to a piece of conduit can be used either from the banks if the surface water body
is narrow or from a boat The sediment is placed into a glass pan and mixed according to Section 5.138
of this SOP.
EISOPQAM il-i May 1996
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If the surface water body has a significant flow and is too deep to wade, a BMH-60 sampler ma>
be used The BMH-60 is not particularly efficient in mud or other soft substrates because its weight will
cause penetration to deeper sediments, thus missing the most recently deposited material at the sediment
water interface It is also difficult to release secured samples in an undisturbed fashion that would readih
permit subsamplmg The BMH-60 may be used provided that caution is exercised by only taking
subsamples that have not been in contact with the metal walls of the sampler
1122 Dredges
For routine analyses, the Peterson dredge can be used when the bottom is rocky, in very deep
water, or when the stream velocity is high The dredge should be lowered very slowly as it approaches
bottom, since it can displace and miss fine particle size sediment if allowed to drop freely
The Eckman dredge has only limited usefulness. It performs well where the bottom material is
unusually soft, as when covered with organic sludge or light mud. It is unsuitable, however, for sandy,
rocky, and hard bottoms and is too light for use in streams with high velocities. It should not be used from
a bridge that is more than a few feet above the water, because the spring mechanism which activates the
sampler can be damaged by the messenger if dropped from too great a height.
The Ponar dredge is a modification of the Peterson dredge and is similar in size and weight It has
been modified by the addition of side plates and a screen on the top of the sample compartment The
screen over the sample compartment permits water to pass through the sampler as it descends thus reducing
turbulence around the dredge. The Ponar dredge is easily operated by one person in the same fashion as
the Peterson dredge. The Ponar dredge is one of the most effective samplers for general use on all types
of substrates
The "mini" Ponar dredge is a smaller, much lighter version of the Ponar dredge li is used to
collect smaller sample volumes when working in industrial tanks, lagoons, ponds, and shallow water
bodies It is a good device use when collecting sludge and sediment containing hazardous constituents
because the size of the dredge makes it more amenable to field cleaning.
1123 Coring
Core samplers are used to sample vertical columns of sediment. They are particularly useful when
a historical picture of sediment deposition is desired since they preserve the sequential layering of the
deposit, and when it is desirable to minimize the loss of material at the sediment-water interface Many
t\pes of coring devices have been developed depending on the depth of water from which the sample is
to be obtained, the nature of the bottom material, and the length of core to be collected. They vary from
hand push rubes to weight or gravity driven devices
Coring devices are particularly useful m pollutant monitoring because turbulence created by descent
through the water is minimal, thus the fines of the sediment-water interface are only minimally disturbed,
the sample is withdrawn intact permuting the removal of only those layers of interest, core liners
manufactured of glass or Teflon* can be purchased, thus reducing possible sample contamination, and the
samples are easily delivered to the lab for analysis in the rube in which they were collected
The disadvantage of coring devices is that a relatively small surface area and sample size is
obtained often necessitating repetitive sampling in order to obtain the required amount of material for
analysis Because it is believed that this disadvantage is offset by the advantages, coring devices are
recommended in sampling sediments for trace organic compounds or metals analyses
EISOPQAM 11.2 May 1996
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In shallow, wadeable waters, the direct use of a core liner or tube manufactured of Teflon9, plastic.
or glass is recommended for the collection of sediment samples. (Plastic tubes are principally used for
collection of samples for physical parameters such as panicle size analysis) Their use can also be extended
to deep waters when SCUBA diving equipment is utilized Teflon* or plastic are preferred to glass since
they are unbreakable which reduces the possibility of sample loss Stainless steel push tubes are also
acceptable and provide a better cutting edge and higher strength than Teflon*. The use of glass or Teflon*
tubes eliminates any possible metals contamination from core barrels, cutting heads, and retainers The
tube should be approximately 12 inches in length if only recently deposited sediments (8 inches or less) are
to be sampled Longer tubes should be used when the depth of the substrate exceeds 8 inches Sofi or
semi-consolidated sediments such as mud and clays have a greater adherence to the inside of the tube and
thus can be sampled with larger diameter tubes Because coarse or unconsolidated sediments such as sands
and gravel tend to fall out of the tube, a small diameter is required for them A tube about two inches in
diameter is usually the best size The wall thickness of the tube should be about 1/3 inch for Teflon*.
plastic, or glass The inside wall may be filed down at the bottom of the tube to provide a cutting edge and
facilitate entry of the liner into the substrate
Caution should be exercised not to disturb the bottom sediments when the sample is obtained b>
wading in shallow water The core tube is pushed into the substrate until four inches or less of the tube
is above the sediment-water interface When sampling hard or coarse substrates, a gentle rotation of the
tube while it is being pushed will facilitate greater penetration and decrease core compaction The top of
the tube is then capped to provide a suction and reduce the chance of losing the sample A Teflon® plug
or a sheet of Teflon* held in place by a rubber stopper or cork may be used After capping, the tube is
slowly extracted with the suction and adherence of the sediment keeping the sample in the tube Before
pulling the bottom part of the core above the water surface, it too should be capped
When extensive core sampling is required, such as a cross-sectional examination of a streambed
(with an objective of profiling both the physical and chemical contents of the sediment), a whole core must
be collected A strong coring rube such as one made from aluminum, steel or stainless steel is needed to
penetrate the sediment and underlying cla> or sands A coring device can be used to collect an intact
sediment core from streambeds that have soft bottoms which allows several inches of penetration It is
recommended that the corer have a checkvalve built into the driving head which allows water and air to
escape from the cutting core, thus creating a partial vacuum which helps to hold the sediment core m the
tube The corer is attached to a standard auger extension and handle, allowing it to be corkscrewed into
the sediment from a boat or while wading The coring tube is easily detached and the intact sediment core
is removed with an extraction device
Before extracting the sediment from the coring tubes, the clear supernatant above the sediment-
water interface in the core should be decanted from the tube This is accomplished by simply turning the
core tube to its side, and gently pouring the liquid out until fine sediment particles appear in the waste
liquid The loss of some of the fine sediments usually occurs with this technique
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SECTION 12
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SECTION 12
SOIL SAMPLING
PERFORMANCE OBJECTIVES:
To collect a soil sample that is representative of conditions as they exist at the site
• By selecting the appropriate sampling device(s).
• By taking measures to avoid introducing contamination as a result of poor sampling
and/or handling technique.
• By reducing the potential of cross contamination between samples.
12.1 Introduction
Prior to conducting a soil sampling investigation, a sampling strategy should be developed based
on the objectives of the investigation (Section 5.5 of this SOP contains a discussion of soil sampling
strategies) After designing a soil sampling strategy, the appropriate equipment and techniques must be
used to conduct the investigation This section discusses the sampling equipment available and collection
methods which have been shown to be technically appropriate.
Manual techniques and equipment, such as hand augers, are usually used for surface or shallow,
subsurface soil sampling. Power operated equipment is usually associated with collecting deep samples.
but this equipment can also be used for collecting shallow samples when the auger hole begins to collapse.
or when the soil is so tight that manual auguring is not practical. This section discusses the various sample
collection methods employed by Held investigators
12.2 Equipment
Soil sampling equipment used for sampling trace contaminants should be constructed of inert
materials such as stainless steel Ancillary equipment such as auger flights, post hole diggers, etc. may
be constructed of other materials since this equipment does not come in contact with the samples
However, plastic, chromium, and galvanized equipment should not be used routinely in soil sampling
operations Painted or rusted equipment must be sandblasted before use.
Selection of equipment is usually based on the depth of the samples to be collected, but it is also
controlled to a certain extent by the characteristics of the material. Manual techniques and equipment such
as hand augers, are usually used for collecting surface or shallow, subsurface soil samples Power operated
equipment is usually associated with deep sampling but can also be used for shallow sampling when the
auger hole begins to collapse or when the soil is so tight that manual augenng is not practical
EISOPQAM 12 - 1 May 1996
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12.3 Sampling Methodology
This discussion of soil sampling methodology reflects both the equipment used (required/needed)
10 collect the sample, as well as how the sample is handled and processed after retrieval Selection of
equipment is usually based on the depth of sampling, but it is also controlled, to a certain extent, by the
characteristics of the material Simple, manual techniques and equipment, such as hand augers, are usually
selected for surface or shallow, subsurface soil sampling As the depth of the sampling interval increases.
some type of powered sampling equipment is usually needed to overcome torque induced by soil resistance
and depth The following is an overview of the various sample collection methods employed over three
general depth classifications- surface, shallow subsurface, and deep subsurface. Any of the deep collection
methods described may be used to collect samples from the shallower intervals.
1231 Manual (Hand Operated) Collection Techniques and Equipment
These methods are used primarily to collect surface and shallow subsurface soil samples Surface
soils are generally classified as soils between the ground surface and 6 to 12 inches below ground surface
The shallow subsurface interval may be considered to extend from approximately 12 inches below ground
surface to a site-specific depth at which sample collection using manual methods becomes impractical
Surface Soils
Surface soils may be collected with a wide variety of equipment. Spoons, shovels, hand-augers.
push tubes, and post-hole diggers, made of the appropriate material, may be used to collect surface soil
samples As discussed in the section on powered equipment, surface soil samples may also be collected
in conjunction with the use of heavy equipment
Surface samples are removed from the ground and placed in pans, where mixing, as appropriate
(Section 5.13 8). occurs prior to filling of sample containers. Section 12.4.1 contains specific procedures
for handling samples for volatile organic compounds analysis. If a thick, matted root zone is encountered
at or near the surface, it should be removed before the sample is collected
Subsurface Soils
Hand-augermg is the most common manual method used to collect subsurface samples Typically.
4-mch auger-buckets with cutting heads are pushed and twisted into the ground and removed as the buckets
are filled The auger holes are advanced one bucket at a time The practical depth of investigation usmc
a hand-auger is related to the material being sampled In sands, augermg is usually easily accomplished"
but the depth of investigation is controlled by the depth at which sands begin to cave At this point, auger
holes usually begin to collapse and cannot practically be advanced to lower depths, and further samples.
if required, must be collected using some type of pushed or driven device Hand-augermg may also
become difficult in tight clays or cemented sands At depths approaching 20 feet, torqumg of hand-auger
extensions becomes so severe that in resistant materials, powered methods must be used if deeper samples
are required Some powered methods, discussed later, are not acceptable for actual sample collection, but
are used solely to gam easier access to the required sample depth, where hand-augers or push tubes are
generally used to collect the sample
EISOPQAM 12 - 2 May 1996
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When a vertical sampling interval has been established, one auger-bucket is used to advance the
auger hole to the first desired sampling depth. If the sample at this location is to be a vertical composite
of all intervals, the same bucket may be used to advance the hole, as well as to collect subsequent samples
in the same hole However, if discrete grab samples are to be collected to characterize each depth, a new
bucket must be placed on the end of the auger extension immediately prior to collecting the next sample
The top several inches of soil should be removed from the bucket to minimize the chances of cross-
contamination of the sample from fall-in of material from the upper portions of the hole
Another hand-operated piece of soil sampling equipment commonly used to collect shallow
subsurface soil samples is the Shelby* or "push tube". This is a thin-walled tube, generally of stainless
steel construction and having a beveled leading edge, which is twisted and pushed directly into the soil
This type of sampling device is particularly useful if an undisturbed sample is required. The sampling
device is removed from the push-head, then the sample is extruded from the tube into the pan with a spoon
or special extruder Even though the push-head is equipped with a check valve to help retain samples, the
Shelby rube will generally not retain loose and watery soils, particularly if collected at lower depths
12 3 2 Powered Sampling Devices
Powered sampling devices and sampling aids may be used to acquire samples from any depth but
are generally limited to depths of 20 feet or less Among the common types of powered equipment used
to collect or aid in the collection of subsurface soil samples are Little Beaver* type power augers; split-
spoon samplers driven with a drill rig drive-weight assembly or hydraulically pushed using drill rig
hydraulics, continuous split-spoon samplers, specialized hydraulic cone penetrometer rigs, and back-hoes
The use of each of these is described below
Power Augers
Power augers are commonly used to aid in the collection of subsurface soil samples at depths where
hand augermg is impractical This equipment is a sampling aid and not a sampling device, and 20 to 25
feet is the typical lower depth range It is used to advance a hole to the required sampling depth, at which
point a hand auger is usually used to collect the sample
Drill Rigs
Drill rigs offer the capability of collecting soil samples from greater depths. For all practical
purposes, the depth of investigation achievable by this method is controlled only by the depth of soil
overlying bedrock, which may be in excess of 100 feet
When used in conjunction with drilling, split-spoon samplers are usually driven either inside a
hollow-stem auger or inside an open borehole after rotary drilling equipment has been temporarily
removed The spoon is driven with a 140-pound hammer through a distance of up to 24 inches and
removed If geotechmcal data are also required, the number of blows with the hammer for each six-inch
interval should be recorded.
Continuous split-spoon samplers may be used to obtain five-foot long, continuous samples
approximately 3 to 5 inches in diameter These devices are located inside a five-foot section of hollow-
siem auger and advanced with the auger during drilling As the auger advances, the central core of soil
moves into the sampler and is retained until retrieval
EISOPQAM 12 - 3 May 1996
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Cone Penetrometer Rigs
This method uses a standard split-spoon has been modified with a releasable tip which keeps the
spoon closed during the sampling push Upon arrival at the desired depth, the tip can be remotely released
and the push continued. During the subsequent push, the released tip floats freely up the inside of the
spoon as the soil core displaces it Split-spoon soil samples, therefore, can be collected without drilling.
as has historically been required, by simply pushing the device to the desired depth This technique^
particularly beneficial at highly contaminated sites, because cuttings are not produced as with drill rigs
The push rods are generally retrieved with very little residue. This results in minimal exposure 10 sampling
personnel and very little contaminated residue is produced as a result of equipment cleaning
Back-Hoes
Back-hoes are often utilized in shallow subsurface soil sampling programs Samples may either
be collected directly from the back-hoe bucket or they may be collected from the trench wall if proper
safety protocols are followed. Trenches offer the ability to collect samples from very specific intervals and
allow visual correlation with vertically and horizontally adjacent material Prior to collecting samples from
trench walls, the wall surface must be dressed with a stainless steel shovel, spatula, knife, or spoon to
remove the surface layer of soil which was smeared across the trench wall as the bucket passed If back-
hoe buckets are not cleaned according to the procedures described in Appendix B of this SOP, samples
should be collected from material which has not been in contact with the bucket surface.
12.4 Special Techniques and Considerations
1241 Collection of Soil Samples for Volatile Organic Compounds (VOC) Analysis
These samples should be collected in a manner that minimizes disturbance of the sample For
example, when sampling with a hand auger, the sample for VOC analysis may be collected directly from
the auger bucket or immediately after an auger bucket is emptied into the pan The sample should be
placed in the appropriate container with no head-space, if possible, as is the practice with water samples
Samples for VOC analysis are not mixed
1242 Dressing Soil Surfaces
Any time a vertical or near vertical surface, such as is achieved when shovels or back-hoes are
used for subsurface sampling, is sampled, the surface should be dressed to remove smeared soil This is
necessar\ to minimize the effects of cross-contamination due to smearing of material from other levels
12 4 3 Sample Mixing
It is extremely important that soil samples be mixed as thoroughly as possible to ensure that the
sample is representative of the interval sampled Soil samples should be mixed as specified in Section
5 138
EISOPQAM 12-4
Mav 1996
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1244 Special Precautions for Trace Contaminant Soil Sampling
The procedures outlined in Section 5 13.7 should be followed. All soil sampling equipment used
for sampling for trace contaminants should be constructed of stainless steel where possible Pans used for
mixing should be made of Pyrex® (or equivalent) or glass. In no case will chromium, cadmium, or
galvanized plated or coated equipment be used for soil sampling operations when inorganic contamination
is of concern Similarly, no painted or plastic equipment should be used when organic contaminants are
of concern All paint and primer must be removed from soil sampling equipment by sandblasting or other
means before such equipment can be used for collecting soil samples.
1245 Specific Sampling Equipment Quality Assurance Techniques
Drilling rigs and other major equipment used to collect soil samples should be identified so that
tins equipment can be traced through field records. A log book should be established for this equipment
so that all cleaning, maintenance, and repair procedures can be traced to the person performing these
procedures and to the specific repairs made. Sampling spoons, hand augers, Shelby tubes, and other minor
disposable type equipment are exempted from this equipment identification requirement All equipment
used to collect soil samples should be cleaned as outlined in Appendix B and repaired, if necessary, before
being stored at the conclusion of field studies. Equipment cleaning conducted in the field (Appendix B)
or field repairs should be thoroughly documented in field records.
EISOPQAM 12 - 5 May 1996
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SECTION 13
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SECTION 13
WASTE SAMPLING
SECTION OBJECTIVE:
• To describe equipment and procedures that can safely be used to collect waste samples
13.1 Introduction
Hazardous wastes are regulated by the US EPA under 40 CFR Parts 260-299 As a consequence.
many of the methods that are used to manage, store, treat, and dispose hazardous wastes and potential
hazardous wastes are of concern to both the regulators and the regulated community
Samples are often required of regulated or potentially regulated materials. While it is understood
thai each facility and wastestream may present its own unique sampling and analytical challenges, this
section will list equipment and procedures that have been used to safely and successfully sample specific
waste units
13 1 1 Safety
Sampling of waste units should be assessed for potential hazards by both the project leader and the
site safety officer (SSO). It is the SSOs responsibility to enforce the site safety plan, and to ensure that
procedures used during waste sampling are in accordance with Branch safety procedures and protocols
found in Section 4 The procedures outlined in the Region 4 Field Health and Safety Manual f n will be
followed during sampling of all potentially hazardous wastes
Sampling equipment contaminated during waste sampling investigations must be at a minimum
cleaned with laboratory detergent and rinsed with tap water prior to returning the equipment from the field
Contaminated sampling equipment that is to be discarded must be properly disposed according to Section
5 IS and should be specified in the site-specific study plan
1312 Quality Control Procedures
In some instances, special decontamination procedures will be necessary and should be developed
on a case-by-case basis according to the specific material encountered. Any cleaning procedures and
equipment repairs conducted in the field which deviate from those specified in Appendix B or the study
plan, should be thoroughly documented in the logbooks.
All air monitoring and field analytical/screening equipment should be checked and calibrated before
being issued for field studies, as specified in Sections 16 and 17 of this SOP.
EISOPQAM 13 - 1 May 1996
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13 1 3 Collection of Auxiliary Information and Data
The collection of auxiliary information and data is particularly important when collecting waste
samples Any field analyses or field screening results should be recorded in a logbook as outlined in
Section 3 5 Sketches of waste units, sampling locations, containers, tanks and ancillary equipment.
markings/labels, etc , should be fully documented in logbooks. Photographs are extremely useful for
recording this information and may be used during waste sampling operations A field log of the
photographs taken should be maintained as outlined in Section 3.2.2.
13.2 Waste Unit Types
Waste management units can be generally categorized into two types: open and closed In practice,
open units are larger than closed units. Open units include waste piles and surface impoundments whereas
closed units include containers and tanks as well as ancillary tank equipment. Besides containers and tanks.
sumps may also be considered closed units because they are designed to collect the spillage of liquid wastes
and are sometimes configured as a confined space
Although both may pose hazards, units that are open to the environment are generally less
hazardous than closed units Sampling of closed units is considered a higher hazard risk because of the
potential of exposure to toxic gases and flammable/explosive atmospheres Because closed units prevent
the dilution of the wastes by environmental influences, they are more likely to contain materials that have
concentrated levels of hazardous constituents. While opening closed units for sampling purposes,
investigators shall use Level B personnel protective equipment, air monitoring instruments to ensure that
the working environment does not contain hazardous levels of flammable/explosive gasses or toxic vapors,
and follow the appropriate safety requirements stipulated in the site specific safety plan
Buried waste materials should be located and excavated with extreme caution Once the buried
waste is uncovered, the appropriate safety and sampling procedures utilized will depend on the type of
waste unit
13 2 I Open Units
While open units may contain many types of wastes and come in a variety of shapes and sizes, they
can be generally regarded as either waste piles or surface impoundments Definitions of these two types
of open units from 40 CFR Pan 260 10 are
• Waste pile -- any non-containerized accumulation of solid, non-flowing hazardous waste that
is used for treatment or storage and that is not a containment building
• Surface impoundment -- " ..a facility or part of a facility which is a natural topographic
depression, man-made excavation, or diked area formed primarily of earthen materials
(although it may be lined with man-made materials), which is designed to hold the
accumulation of liquid wastes or wastes containing free liquids, and which is not an injection
well Examples of surface impoundments are storage, settling and aeration pits, ponds, and
lagoons "
One of the distinguishing features between waste piles and surface impoundments is the state of
die waste Waste piles typically contain solid or non-flowing materials whereas liquid wastes are usually
contained in surface impoundments The nature of the waste will also determine the mode of delivering
the waste to the unit Wastes are commonly pumped or gravity fed into impoundments while heavy
equipment or trucks may be used to dump wastes in piles Once the waste has been placed in an open unit,
the state of the waste may be altered by environmental factors (e.g., temperature, precipitation, etc.)
E1SOPQAM 13-2 May 1996
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Surface impoundments may contain several phases such as floating solids, liquid phase(s). and
sludges Waste piles are usually restricted to solids and semi-solids. All of the potential phases contained
in a waste unit should be considered in developing the sample design to meet the study's objective
1322 Closed Units
There are a variety of designs, shapes, sizes, and functions of closed units In addition to the
challenges of the various designs and the safety requirements for sampling them, closed units are difficult
to sample because they may contain liquid, solid, semi-solid/sludge, or any combination of phases Based
on the study's design, it may be necessary to obtain a cross sectional profile of the closed unit m an attempt
to characterize the unit The following are definitions of types of closed waste units described m 40 CFR
Part 260.10
• Container -- any portable device in which waste is stored, transported, treated, disposed, or
otherwise handled. Examples of containers are drums, overpacks, pails, totes, and roll-offs
Portable tanks, tank trucks, and tank cars vary in size and may range from simple to extremely
complex designs. Depending on the unit's design, it may be convenient to consider some of
these storage units as tanks for sampling purposes even though they meet the definition of a
container
• Tank -- a stationary device, designed to contain an accumulation of waste which is constructed
primarily of non-earthen materials which provide structural support.
• Ancillary tank equipment « any device including, but not limited to, such devices as piping,
fittings, flanges, valves, and pumps that is used to distribute, meter, or control the flow of
waste from its point of generation to a storage or treatment tank(s), between waste storage and
treatment tanks to a point of disposal on-site, or to a point of disposal off-site
• Sump - any pit or reservoir that meets the definition of a tank and those troughs/trenches
connected to it that serve 10 collect liquid wastes (Note some outdoor sumps may be
considered open units/surface impoundments).
Although any of the closed units may not be completely sealed and may be partially open to the
environment, the unit needs to be treated as a closed unit for sampling purposes until a determination can
be made Once a closed unit is opened, a review of the proposed sampling procedures and level of
protection can be performed to determined if the personal protection equipment is suitable for the sue
conditions
Samples collected from different waste units should not be composited into one sample container
u ithout additional analytical and/or field screening data to determine if the materials in the units are
compatible and will not cause an inadvertent chemical reaction
EISOPQAM 13 - 3 May 1996
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13.3 Equipment
Selecting appropriate equipment to sample wastes is a challenging task due the uncertainty of the
physical characteristics and nature of the wastes. It may be difficult to separate, homogenize and/or
containerize a waste due to its physical characteristics (viscosity, particle size, etc.). In addition, the
physical characteristic of a waste may change with temperature, humidity, or pressure. Waste streams may
vary depending on how and when a waste was generated, how and where it was stored/disposed, and the
conditions under which it was stored/disposed Also, the physical location of the wastes or the unit
configuration may prevent the use of conventional sampling equipment.
Given the uncertainties that a waste may present, it is desirable to select sampling equipment that
will facilitate the collection of samples that will meet the study's objective, and that will not unintentionally
bias the sample by excluding some of the sample population that is under consideration. However, due
to the nature of some waste matrices or the physical constraints of the waste unit, it may be necessary to
collect samples knowing that a portion of the desired population was omitted due to limitations of the
equipment Any deviations from the study plan or difficulties encountered in the field concerning sample
collection that may have an effect on the study's objective, should be documented in a log book, reviewed
with the analytical data, and presented in the report
1331 Waste Sampling Equipment
Waste sampling equipment should be made of non-reactive materials that will neither add to or alter
the chemical or physical properties of the material that is being sampled. Table 13.3.1 lists some
conventional equipment for sampling waste units/phases and some potential limitations of the equipment
1332 Ancillary Equipment for Waste Sampling
In addition to the equipment listed in Table 1331 which provides the primary device used to
collect various waste samples, ancillary equipmeni may be required during the sampling for safety and/or
analytical reasons Some examples of these types of equipment are glass mixing pans, particle size
reducers, remote drum opening devices, and spark resistant tools. See Section 13 7 for particle size
reduction procedures Any influences thai these types of ancillary equipment may have on the data should
be evaluated and reported as necessary
EISOPQAM 13-4 May 1996
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TABLE 13.3.1
SAMPLING EQUIPMENT for VARIOUS WASTE UNITS
Equipment
scoop with
bracket/conduit
(stainless steel)
spoon (stainless steel)
push tube (stainless
steel)
auger (stainless steel)
sediment sampler
(stainless steel)
ponar dredge
(stainless steel)
COLIWASA or drum
thief (glass)
Mucksucker™.
Dipstick™ (Teflon*)
bacon bomb (stainless
steel)
bailer (Tenon*,
stainless steel)
peristaltic pump
with vacuum jug
assembly (Teflon*)
back-hoe bucket
split-spoon
roto-hammer
Waste Units/Phases
impoundments, piles,
containers, tanks/liquids,
solids, sludges
impoundments, piles,
containers/solids, sludges
piles, containers/cohesive
solids, sludges
impoundments, piles, con-
tainers/solids
impoundments, piles/
solids, sludges
impoundments/solids,
sludges
impoundments, con-
tainers, tanks/liquids
impoundments, con-
tainers, tanks/liquids,
sludges
impoundments, tanks/
liquids
impoundments, tanks/
liquids
impoundments, tanks/
liquids
piles/solids, sludges
piles/solids
piles, containers/solids
Limitations
Can be difficult to collect deeper phases in
multiphase wastes. Depth constraints
Similar limitations as the scoop Generally
not effective in sampling liquids
Should not be used to sample solids with
dimensions > '/4 the diameter of the tube
Depth constraints
Can be difficult to use in an impoundment or
a container, or for solidified wastes
Should not be used to sample solids with
dimensions > '/2 the diameter of the tube
Must have means to position equipment to
desired sampling location. Difficult to
decon
Not for containers > 4 feet deep Not good
with viscous wastes
Not recommended for tanks > 1 1 feet deep
Not good with viscous wastes
Only if waste is homogeneous Not good
with viscous wastes
Cannot be used in flammable atmospheres
Not good with viscous wastes.
May be difficult to access desired sampling
location Difficult to decon. Can lose
volatiles
Requires drill rig.
Physically breaks up sample. May release
volatiles. Not for flammable atmospheres
E1SOPQAM
13-5
May 1996
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13.4 Waste Sampling Procedures
134 1 Waste Piles
Waste piles vary m size, shape, composition, and compactness, and may vary in distribution of
hazardous constituents and characteristics (strata). These variables will affect safety and access
considerations The number of samples, the type of sample(s), and the sample location(s) should be based
on the study's objectives Commonly used equipment to collect samples from waste piles are listed in
Table 13.3 1 All equipment should be compatible with the waste and should have been cleaned to prevent
any cross contamination of the sample
1342 Surface Impoundments
Surface impoundments vary in size, shape, and waste content, and may vary in distribution of
hazardous constituents and characteristics (strata). The number of samples, the type of sample(s), and the
sample location(s) should be based on the study's objectives. Commonly used equipment to collect samples
from surface impoundments are listed in Table 133.1. All equipment should be compatible with the waste
and should have been cleaned to prevent any cross contamination of the sample.
Because of the potential danger of sampling waste units suspected of containing elevated levels of
hazardous constituents, personnel should never attempt to sample surface impoundments used to manage
potentially hazardous wastes from a boat All sampling should be conducted from the banks or piers of
surface impoundments Any exception must be approved by the appropriate site safety officer and/or the
Occupational Health and Safety Designee (OHSD)
1343 Drums
The most frequent type of containers sampled for hazardous constituents or characteristics by field
investigators are drums Caution should be exercised by the field investigators when sampling drums
because of the potential presence of explosive/flammable gases and/or toxic vapors Therefore, the
following procedures should be used when collecting samples from drums of unknown material
1 Visually inspect all drums that are being considered for sampling for the following
• pressunzation (bulging/dimples).
• crystals formed around the drum opening.
• leaks, holes, stains.
• labels, markings.
• composition and type (steel/poly and open/bung);
• condition, age. rust, and
• sampling accessibilit)
Drums showing evidence of pressunzation and crystals should be furthered assessed to
determine if remote drum opening is needed If drums cannot be accessed for sampling, heavy
equipment is necessary to stage drums for the sampling activities. Adequate time should be
allowed for the drum contents to stabilize after a drum is handled
2 Identify each drum that will be opened (e.g., paint sticks, spray paint, cones, etc)
EISOPQAM 13-6 May 1996
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LEVEL "B" PROTECTION IS REQUIRED FOR THE FOLLOWING PROCEDURES.
3 Before opening, ground each metal drum that is not in direct contact with the earth using
grounding wires, alligator clips, and a grounding rod or metal structure If a metal drum is
m an overpack drum, the metal drum should be grounded.
4 Touch the drum opening equipment to the bung or lid and allow an electrical conductive path
to form Slowly remove the bung or drum ring and/or lid with spark resistant tools
(brass/beryllium).
5 Screen drums for explosive gases and toxic vapor with air monitoring instruments as bung or
drum lid is removed. Depending on site conditions screen for one or more of the following
• radioactivity,
• cyanide fumes,
• halogen vapors,
• pH; and/or
• flash point (requires small volume of sample for testing).
Note the state, quantity, phases, and color of the drum contents Record all relevant results.
observations, and information in a logbook or on a Drum Data Form Figure 13-1 is an
example of a Drum Data Form Review the screening results with any pre-existing data to
determine which drums will be sampled
6 Select the appropriate sampling equipment based on the state of the material and the type of
container Sampling equipment should be made of non-reactive materials that will neither add
or alter the chemical or physical properties of the material that is to be sampled
7 Place oil wipe, sampling equipment, and sample containers near drum(s) to be sampled
AIR MONITORING FOR TOXIC VAPORS AND EXPLOSIVE GASES AND OXYGEN
DEFICIENT ATMOSPHERES SHOULD BE CONDUCTED DURING DRUM SAMPLING.
Liquids -- Slowly lower the COL1WASA or drum thief to the bottom of the container Close
the COLIWASA with the inner rod or create a vacuum with the sampler's gloved thumb on
the end of the thief and slowly remove the sampling device from the drum Release the sample
from the device into the sample contamer(s) splitting each COLIWASA volume among the
containers, if possible Repeat the procedure until a sufficient sample volume is obtained
Solids/Semi-Solids -- Use a push tube, bucket auger, or screw auger or if conditions permit
a pneumatic hammer/drill to obtain the sample. Carefully use a clean stainless steel spoon to
place the sample into contamer(s) for analyses.
8 Close the drums when sampling is complete Segregate contaminated sampling equipment and
investigative derived wastes (IDW) containing incompatible materials as determined by the
drum screening procedure (Step #5) At a minimum, contaminated equipment should be
cleaned with laboratory detergent and rinsed with tap water prior to returning it from the field
IDW should be managed according to Section 5 IS
EISOPQAM 13 - 7 May 1996
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FIGURE 13-1
DRUM DATA FORM
Date Page
SAMPLE COLLECTED- Y / N
PROJECT NO SITE NAME-
CITY STATE-
EPA DRUM ID# OTHER DRUM ID#
DRUM OBSERVATIONS:
DOVERPACK Y / N METAL / PLASTIC / OTHER
SIZE 85 / 55 /
2) DRUM METAL / PLASTIC / OTHER
SIZE 85 / 55 /
CONDITION: GOOD / FAIR / POOR
MARKINGS/LABELS
3) DRUM OPENING TEAM-
4) ESTIMATED VOLUME FULL / K / fc / '/4 / EMPTY
5) PHYSICAL APPEARANCE OF DRUM CONTENTS:
COLOR VISCOSITY: LOW / MED / HIGH
PHASED Y / N . DESCRIPTION
OTHER
6) AIR MONITORING RESULTS
PID ppm EXPLOS %CK %LE1.
FID ppm HALOGEN Yes No
CN ppm pH
RAD Mrem
7) FLASH POINT SAMPLE COLLECTED YES / NO
FLASH RESULTS AT 140°F YES / NO
HOT WIRE TEST FOR HALOGEN POS / NEC
8) SAMPLE COLLECTED YES / NO TIME-
COLLECTOR^):
EISOPQAM 13 - 8 May 1996
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1344 Tanks
Sampling tanks is considered hazardous due to the potential for them to contain large volumes of
hazardous materials and therefore, appropriate safety protocols must be followed Unlike drums, tanks
may be compartmentalize or have complex designs Preliminary information about the tank's contents and
configuration should be reviewed prior to the sampling operation to ensure the safety of sampling personnel
and that the study's objectives can be achieved.
In addition to having discharge valves near the bottom of tanks and bulk storage units, most tanks
have hatches at the top It is desirable to collect samples from the top hatch because of the potential for
the tank's contents to be stratified Additionally, when sampling from the discharge valve, there is a
possibility of a stuck or broken valve which could cause an uncontrolled release. Investigators should not
utilize valves on tanks or bulk storage devices unless they are operated by the owner or operator of the
facility, or a containment plan is in place should the valve stick or break. If the investigator must sample
from a tank discharge valve, the valvmg arrangement of the particular tank must be clearly understood to
insure that the compartment(s) of interest is sampled.
Because of the many different types of designs and materials that may be encountered, only general
sampling procedures that outline sampling a tank from the top hatch are listed below:
1 All relevant information concerning the tank such as the type of tank, the tank capacity.
markings, condition, and suspected contents should be documented in a logbook
2 The samplers should inspect the ladder, stairs, and catwalk that will be used to access the top
hatch to ensure that they will support the samplers and their equipment
LEVEL "B" PROTECTION IS REQUIRED FOR THE FOLLOWING PROCEDURES.
3 Before opening, ground each metal tank using grounding wires, alligator clips, and a
grounding rod or metal structure
4 Any vents or pressure release valves should be slowly opened to allow the unit to vent to
atmospheric pressure Air monitoring for explosive/flammable gases and toxic vapors should
be conducted during the venting with the results recorded in a log book If dangerous
concentrations of gases evolve from the vent or the pressure is too great, leave the area
immediately
5 Touch tank opening equipment to the bolts in the hatch lid and allow electrical conductive path
to form Slowly remove bolts and/or hatch with spark resistant tools (brass/beryllium) If a
pressure build up is encountered or detected, cease opening activities and leave the area
6 Screen tanks for explosive/flammable gases and toxic vapors with air monitoring instruments
Depending on the study objectives and site conditions, conduct characteristic screening (e g ,
pH. halogen, etc ) as desired Collect a small volume of sample for flash point testing, if
warranted. Note the state, quantity, number of phases, and color of the tank contents. Record
all relevant results, observations, and information in a logbook. Compare the screening results
with any pre-existing data to determine if the tank should be sampled.
7 Select the appropriate sampling equipment based on the state of the material and the type of
tank Sampling equipment should be constructed of non-reactive materials that will neither add
to or alter the chemical or physical properties of the material that is to be sampled
EISOPQAM 13-9 May 1996
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8 Place oil wipe, sampling equipment, and sample containers near tanks(s) to be sampled
AIR MONITORING FOR TOXIC VAPORS, EXPLOSIVE GASES AND OXYGEN
DEFICIENT ATMOSPHERES SHOULD BE CONTINUOUS DURING TANK SAMPLING.
Liquids -- Slowly lower the bailer, bacon bomb. Dipstick™, COLIWASA, or Teflon* tubing
to the desired sampling depth (NOTE In work areas where explosive/flammable atmospheres
could occur, peristaltic pumps powered by 12 V batteries should not be used ) Close the
sampling device or create a vacuum and slowly remove the sampling device from the tank
Release the sample from the device into the sample containers). Repeat the procedure until
a sufficient sample volume is obtained.
Solids/Semi-Solids - Use a push tube, bucket auger, screw auger, Mucksucker™, or if
conditions permit a pneumatic hammer/drill to obtain the sample. Carefully extrude the
sample from the sampling device or use a clean stainless steel spoon to place the sample into
containers for analyses.
9 Close the tank when sampling is complete. Segregate contaminated sampling equipment and
investigative derived wastes (IDW) containing incompatible materials as determined by the
drum screening procedure (Step #6). At a minimum, contaminated equipment should be
cleaned with laboratory detergent and rinsed with tap water prior to returning it from the field
IDW should be managed according to Section 5.15
13.5 Miscellaneous Contaminated Materials
Sampling may be required of materials or equipment (e.g., documents, building materials,
equipment, etc ) to determine whether or not various surfaces are contaminated by hazardous constituents,
or to evaluate the effectiveness of decontamination procedures
Wipe or swab samples may be taken on non-absorbent surfaces such as metal, glass, plastic, etc
The wipe materials must be compatible with the solvent used and the analyses to be performed, and should
not come apart during use. The wipes are saturated with either methylene chloride, hexane. or analyte free
water depending on the parameters to be analyzed (consult with laboratory performing the analyses) Wipe
samples should not be collected for volatile organic compounds analysis. Sampling personnel should be
aware of hazards associated with the selected solvent and should take appropriate precautions to prevent
any skin contact or inhalation of these solvents All surfaces and areas selected for sampling should be
based on the study's objectives Typicallj. 10 cm by 10 cm templates are prepared from aluminum foil
which are secured to the surface of interest The prepared (saturated with solvent) wipe(s) is removed from
its container with tongs or gloves, and used to wipe the entire area with firm strokes using only one side
of the wipe The wipe is then placed into the sample container This procedure is repeated until the area
is free of visible contamination or no more wipes remain Care should be taken to keep the sample
container tightly sealed to prevent evaporation of the solvent Samplers must also take care to not touch
the used side of the wipe All requests for support from the Region 4 laboratory for wipe preparations and
v, ipe analyses should be made well in advance of the scheduled sampling event. (Note if gloves are used
to collect the wipe samples, control samples should be collected to determine if the gloves could potentially
contribute constituents to the parameters of interest.)
For items with porous surfaces such as documents (usually business records), insulation, wood,
etc . actual samples of the materials are required. It is therefore important, that during the collection
and/or analyses of the sample that evidentiary material is not destroyed. Use scissors or other particle
reduction device that have been cleaned as specified in Appendix B to cut/shred the sample. Mix in a glass
EISOPQAM 13-10 May 1996
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pan as specified in Section 5 13.8 The shredded, homogenized material is then placed in sample
containers
13.6 Waste Sample Handling Procedures
Waste samples should not be preserved because of the potential for an inadvertent chemical
reaction of the sample with the preservative. After the samples have been collected and containerized, the
outside of the containers should be cleaned with water, paper towels, and/or oil wipes to remove any
spilled sample from the exterior of the container Sample containers should be identified with tags and
sealed for custody purposes as specified in Section 3 as soon as possible. After the sample container has
been tagged and sealed, each container should placed in a separate plastic bag and secured with electrical
tape before being placed in a cooler Waste samples that are suspected of being acutely toxic or extremely
hazardous should be placed in paint cans with absorbent materials prior to being placed in a cooler Waste
samples should not be placed on ice because the potential of a sample being water reactive
EISOPQAM 13-11 May 1996
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13.7 Particle Size Reduction
Particle size reduction of waste samples is periodically required in order to complete an analytical
scan or the Toxicity Characteristic Leaching Procedure (TCLP) test. Samples that may require particle
size reduction include slags, bricks, glass/mirror cullet, wire, etc. Method 1311 (TCLP) states "Particle
size reduction is required, unless the solid has a surface area per gram of material equal to or greater than
3.1 cm2, or is smaller than 1 cm in its narrowest dimension (i.e., capable of passing through a 9 5 mm
(0.375 inch) standard sieve) If the surface area is smaller or the particle size larger than described above,
prepare the solid portion of the waste for extraction by crushing, cutting, or grinding the waste to a surface
area or particle size as described above" (55 FR 26990). The method also states that the surface criteria
are meant for filamentous (paper, cloth, etc.) waste materials, and that "Actual measurement of the surface
area is not required, nor is it recommended". Also, the loss of volatile organic compounds could be
significant during particle size reduction.
Waste samples that require panicle size reduction are often too large for standard sample
containers If this is the case, the sample should be secured in a clean plastic bag and processed using
normal cham-of-custody procedures (Section 3). Note that the tags that will be required for the various
containers should be prepared in the field and either inserted into or attached to the sample bag The bag
should then be sealed with a custody seal
Because of the difficulty in conducting particle size reduction, it is typically completed at the Field
Equipment Center (FEC) The following procedure may be used for crushing and/or grinding a solid
sample
1 Remove the entire sample, including any fines that are contained in the plastic bag and place
them on the standard cleaned stainless steel pan.
2 Using a clean hammer, carefully crush or grind the solid material (safety glasses are required),
attempting to minimize the loss of any material from the pan. Some materials may require
vigorous striking by the hammer, followed by crushing or grinding. The material may be
subject to crushing/grinding rather than striking
3 Continue crushing/grinding the solid material until the sample size approximates 0.375 inch
Attempt to minimize the creation of fines that are significantly smaller than 0.375 inch in
diameter
4 Pass the material through a clean 0 375-inch sieve into a glass pan
5 Continue this process until sufficient sample is obtained. Thoroughly mix me sample as
described in Section 5 13 8 of this SOP Transfer the contents of the glass pan into the
appropriate containers
6 Attach the previously prepared tags and submit for analyses.
EISOPQAM 13 - 12 May 1996
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13.8 REFERENCES
1 Field Health and Safety Manual. United States Environmental Protection Agency, Region IV.
1990 Edition
2 Title 40 Code of Federal Regulations. Parts 260-299, US-EPA, July 1, 1995
3 Standard Guide for Sampling Heterogeneous Wastes (Draft), ASTM Standard, D34 0112
4 Test Methods for Evaluating Solid Waste - Physical/Chemical Methods (SW-846). Third
Edition, Final (Promulgated) Update II, US-EPA, Office of Solid Waste and Emergency
Response, Washington. D C , September, 1994.
5 Compendium of ERT Waste Sampling Procedures. US-EPA, EPA/540/P-91/008 (OSWER
Directive 9360 4-07), January 1991
6 Characterization of Hazardous Waste Sites - A Methods Manual- Volume I -Sue
Investigations. US-EPA. EMSL, Las Vegas, EPA-600/4-84-075, April 1985
7 Characterization of Hazardous Waste Sites - A Methods Manual Volume II -Available
Sampling Methods. 2nd Edition. US-EPA, EMSL, Las Vegas, EPA 600/4-84-076. December
1984
EISOPQAM 13-13 May 1996
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SECTION 14
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SECTION 14
AMBIENT AIR MONITORING
PERFORMANCE OBJECTIVE:
• To present the standard operating procedures and sample collection methodologies for
conducting air monitoring in ambient air.
14.1 Introduction
This section discusses the sample collection and analytical procedures used for air monitoring in
Region 4 Air toxics as used in this SOP means air pollutants for which National Ambient Air Quality
Standards have not been established
1411 Formaldehyde Sampling Using Dimtrophenylhydrazine Cartridges Using Method TO-11
The following is a synopsis of procedures which should be strictly adhered to for the handling and
field use of dimtrophenylhydrazine (DNPH) cartridges for formaldehyde sampling This summary is
adapted from METHOD TO-11 of the COMPENDIUM OF METHODS FOR THE DETERMINATION
OF TOXIC ORGANIC COMPOUNDS IN AMBIENT AIR. The following generic procedures should be
adhered to at all times
• Polyethylene or Nylon gloves must be worn whenever handling any of the DNPH cartridges
(in the extraction laboratory, during preparation for shipment, during field set-up, in the field
during preparation for return shipment, and in the laboratory during preparation for analysis
and during analysis).
• Coated DNPH cartridges which have been prepared for longer than 90 days shall not be used
• All padding material shall be either clean tissue paper or polyethylene-air bubble padding
Never use polvurethane foam, cardboard, or newspaper as padding material DNPH
cartridges which have been properly prepared for shipment may be shipped in cardboard
containers or preferably in coolers with eutectic salt packs (Blue Ice).
• Cham-of-custody shall be maintained for all samples.
• A minimum of one trip blank shall be transported per one to ten samples collected
Extraction Laboratory
Upon completion of preparation of the DNPH cartridges, both ends shall be plugged with
polypropylene Luer* male plugs and each DNPH cartridge placed in a borosilicate glass culture tube with
polypropylene screw caps (tightened) A serial number, expiration date, and a lot number label will be
placed on each glass culture tube. The batches of culture tubes shall be placed in sealed friction-top metal
containers which contain 1-2 inches of granular activated charcoal (or a pouch filled with a similar amount
of charcoal) for storage in the refrigerator in the Air Laboratory The culture tubes should be enclosed in
EISOPQAM 14 - 1 May 1996
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two Zip-Lock® bags to prevent contamination from charcoal dust.
Air Monitoring Team
The Air Monitoring Team will notify and keep the Region 4 laboratory informed as to the
anticipated number of prepared DNPH cartridges needed for field use. On routine studies, the Air
Monitoring Team will notify the laboratory of needs at least two weeks in advance of needed pick-up date
Only the number of DNPH cartridges needed for a maximum of 60 days (including trip blanks and extra
DNPH cartridges for breakage) will be requested
• On the date of shipment or when loading out for a study, the Air Monitoring Team will
remove the sealed cans (which contain the DNPH cartridges sealed in glass culture tubes) from
the refrigerator in the Air Laboratory. If only a small number of tubes are needed for a
particular study, the correct number of tubes will be transferred to another, smaller, solvent-
washed shipping can.
• An appropriate amount of packing material shall be placed in the metal container to prevent
breakage of the glass culture tubes A label shall be affixed onto each metal container listing
the number of DNPH cartridges in the container. The metal containers should be shipped in
coolers containing eutectic salt packs (e.g.. Blue Ice) to maintain a temperature of
approximately 4°C. The DNPH cartridges shall be shipped the same day they are packed
• On each sampling date, the metal container(s) will be removed from the refrigerator or cooler
for transport to the field. At each sampling location the metal container will be opened and
one glass culture rube will be removed (wearing clean polyethylene or nylon gloves) and
allowed to warm to ambient temperature before removing the DNPH cartridge from the glass
culture tube The plugged DNPH cartridge will be removed from the culture tube and the two
Luer* end plugs will be removed from each end of the DNPH cartridge which will be
immediately placed on the sampling train The Luer* end plugs will be placed back into the
glass culture tube and the cap placed on the tube and tightened. The culture rube will be left
m the sampler enclosure at the site The same procedure will be adhered to at each sampling
location A trip blank (in a sealed culture tube) will be placed in a sampler enclosure at one
on the sites for the duration of a sampling event
The sampler will be manually turned on and allowed to run for two minutes An initial flowrate
should be recorded on the sample data sheet The timer should be set to turn the sampler on and off at the
desired times
• The operator should retrieve and secure the sample as soon as possible after the sampling
period ends. The sampler should manually be turned on and allowed to run for two minutes
and a final flowrate and the elapsed time from the time meter should be recorded on the sample
data sheet The exposed DNPH cartridge will then be removed from the sampling tram
(wearing clean polyethylene or nylon gloves). The two Luer* end caps will be removed from
the glass culture tube and placed on the ends of the DNPH cartridge. The DNPH cartridge
will be placed back into the glass culture tube, the lid tightened, and placed back into the metal
container The same procedure is to be followed at each sampling site.
• At the end of each day on which the samples are collected, the sealed metal can (which
contains the exposed DNPH cartridges) shall be either placed in a refrigerator for storage
overnight or placed in a cooler. The cooler will be used to transport the samples to the
EISOPQAM 14 - 2 May 1996
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laboratory The duration of the non-refrigerated period shall be kept to a minimum bui
absolutely not more than two days
Laboratory
Upon arrival of the metal container at the laboratory, the samples shall be stored in the metal
container in a refrigerator until submitted to the chemist for extraction.
1412 Volatile Organic Compounds (VOC) Sampling with SUMMA* Electropohshed Stainless Steel
Canisters Using Method TO-14
The following is a synopsis of procedures which should be strictly adhered to for the cleanup and
use of Summa* canisters for sampling air for Volatile Organic Compounds (VOC) analysis. This summary
is adapted from Method TO-14 of the COMPENDIUM OF METHODS FOR THE DETERMINATION
OF TOXIC ORGANIC COMPOUNDS IN AMBIENT AIR. The following procedures must be followed
in the preparation and use of Summa* canisters for collecting samples for VOC analysis
• AM new Summa* canisters must be individually checked for contamination by the laboratory
before use One of each batch of 10 Summa* canisters that are subsequently cleaned must be
analyzed to check for contamination.
• All sampler tubing, fittings, and wetted parts of valves must be solvent washed in hexane and
heated to > 100° C These parts should then be assembled and flushed with nitrogen for at
least 8 hours prior to use m the sample tram or in the canister cleanup apparatus
• Each canister's valve and fining will be inspected for damage before cleaning Any damaged
valve will be replaced with a previously cleaned (see procedure above) valve After replacing
any valve, the canister will be cleaned and analyzed to verify that it is free of contamination
• If any canister is used to sample a high concentration source, it must be cleaned and analyzed
to verify it is free of contamination before it can be used again.
• Cham-of-custody must be maintained for all samples
SUM MA* Canister Cleanup
The following cleanup procedure will be followed for the preparation of all Summa* canisters
• The canisters should inmalk be pressurized to >2 atm with humidified nitrogen1 then
evacuated to 1 atm This filling and evacuation sequence shall be repeated five times to dilute
any residual contaminants The addition of the water from the humidified nitrogen may also
displace some of the more reactive contaminants that could adhere to active sites on the wall
of the canister. After the fifth evacuation to 1 atm, the vacuum pump will be left on for a
minimum of 3 hours or until a vacuum of < 150 millitorr is reached. The identification
number of the canister, the date, and the final vacuum will be recorded in the canister cleanup
logbook After cleaning, the canister's valve should be capped with a Swagelok* plug A
label will then be affixed to the canister denoting the date it was cleaned and the name of the
person who performed the cleaning
EISOPQAM 14 - 3 May 1996
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1 (The nitrogen should be certified 99 999% pure by the manufacturer A molecular sieve scrubber should be atuihed
to the nitrogen line after the regulator to remove any trace impurities)
Sample Collection
Two types of samples for VOC analysis can be collected with Summa® canisters The canister can
be opened and allowed to fill rapidly to obtain a grab sample or filled slowly by using a flow controller to
collect a time integrated sample With either type of sample, the following general procedures should be
followed
• An EPA, pre-numbered sample tag should be tied to the handle of the Summa* canister prior
to sampling.
• A Chain-Of-Custody Record should be completed detailing time of sampling, sampling
interval, and signed by the person collecting the sample.
• After the sample has been collected, the Summa« canister should be capped, the pre-numbered
EPA tag should be completed, and the canister should be placed in a shipping container with
a copy of the Chain-Of-Custody Record and sealed with EPA sample custody tape
Grab Sample Collection
Before a grab sample is collected for VOC analysis in a Summa* canister, the canister inlet valve
should be fined with a pre-cleaned stainless steel paniculate filter. At the sample collection location, the
mam valve should be opened and the canister allowed to fill After about one minute (when no audible
sound of rushing gas can be heard), the mam valve of the Summa* canister should be closed and capped
Time Integrated Sample Collection
This sample collection method involves the use of a flow controller or a sampler containing a flow
controller to slowly meter the flow of air entering a Summa* canister. With this method, a sample is
collected over a longer period of time than with a grab sample. If a constant flowrate was maintained, the
resulting sample will have a VOC content that is the average of the VOC concentrations during the
sampling interval
The following procedures should be followed to collect time integrated samples
All sampler systems should be checked for contamination prior to use or after any major
repair. This is accomplished by metering zero air or nitrogen1 to the inlet of the sampler
Excess zero air or nitrogen should be vented with a Swagelok® tee from the sampler inlet to
atmosphere. The evacuated canister should then be filled at the normal sampling rate with the
zero gas
• The initial flowrate will be determined with a mass flow meter. The initial flowrate and initial
vacuum (at least 29 inches of Hg) should be recorded on the sample data sheet. The flowrate
should be adjusted so that at the end of the sampling interval the ending pressure of the canister
is approximately 0.9 aim
• The final flowrate should also be determined with a mass flow meter. The final flowrate and
final vacuum should be recorded on tne sample data sheets. The final vacuum should be
between 5 inches and 1 inch of Hg. The final flowrate should be at least 1 sec/mm
EISOPQAM 14 .4
May 1996
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After sample collection, all canisters should be double checked to verify that each has an EPA pre-
numbered tag with all of the information filled out Place the canister in a shipping container and seal the
container with EPA sample custody tape
14 1.3 Sampling for Semi-Volatile Organic Compounds (SVOC) Analysis with High Volume PUF
Samplers Using Methods TO-4 & TO-13
The following is a synopsis of procedures which should be strictly adhered to for use of the High
Volume Polyurethane Foam (PUF) sampling method for collecting samples for semi-volatile organic
compound (SVOC) analysis including pesticides and polychlonnated biphenyls. This summary is adapted
from Method TO-4 (pesticides and PCBs) and TO-13 (polynuclear aromatic compounds) of the
COMPENDIUM OF METHODS FOR THE DETERMINATION OF TOXIC ORGANIC COMPOUNDS
IN AMBIENT AIR.
The following procedures must be followed during preparation of PUF sampling media when using
the High Volume PUF method for collecting samples for SVOC analysis:
• All PUF sampling media should be pre-cleaned, loaded into High Volume PUF sample
cartridges, and sealed in solvent washed cans by the extraction laboratory prior to use
• Cham-of-custody shall be maintained for all samples.
PUF Cleaning
The Air Monitoring Team has responsibility for buying the PUF media and cutting the PUF plugs
PUF media should be specified as not containing any fire retardants. It should be stored in the dark to
prevent photo-oxidation It should be less than two years old, and should be stored in a pesticide free
environment
Care should be exercised in cutting the PUF It should be thoroughly wet with tap water prior to
cutting A drill press and stainless steel PUF cutting die should be used. The drill press area should be
free of oil and a polyethylene cutting block should be used to stop the die at the bottom of the drill press
stroke (do not use wood) Water should be sprayed on the die to help prevent snagging as the PUF is cut
Afier the plugs are cut, they should be rinsed with tap water and followed by a rinse with analyte-free
water Fmallj, the excess water should be squeezed out
The PUF/XAD-2 cartridges are assembled using a modified glass sleeve containing an extra-extra
coarse frit to retain the XAD-2 resin in the following manner. A 3/4-mch layer of XAD-2 resin is poured
on top of the frit followed by a 1 '/i-mch PUF plug to retain the XAD-2 resin.
The assembled PUF/XAD-2 cartridges are delivered to the extraction laboratory for cleaning and
checking The extraction laboratory will be given a minimum of three weeks notice for cleaning and
checking the PUF/XAD-2 cartridges. The cleaned PUF/XAD-2 cartridges should be wrapped in aluminum
foil and packed in metal cans cushioned by cleaned polyurethane foam to prevent breakage during
shipment Prepared PUF/XAD-2 sample cartridges that are pre-packed in solvent washed metal cans will
be obtained from the extraction laboratory prior to sampling The cans should be packed inside coolers
which are lined with polyurethane foam for shipment.
EISOPQAM 14 - 5 May 1996
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Sample Collection
The following procedures will be followed for all High Volume PUF sampling
Nylon gloves will be used when handling all PUF cartridges and quartz paniculate pre-filteri
Assure thai the red silicon upper and lower gaskets, located in the cartridge housing, are in place Then
remove the PUF cartridge from the shipping can, remove from the foil and insert the cartridge into the
High Volume PUF sampler's chamber. The pre-filter should be installed in the filter holder using caution
not to over tighten the fittings. The foil should be placed back in the shipping can. The can should be
labeled with site ID, operators name, and sample date, and placed in the High Volume PUF sampler
enclosure until the sample is collected.
The High Volume PUF sampler should be turned on and allowed to run for two minutes An initial
flowrate should be recorded on the sample data sheet. The timer should be set to turn the sampler on and
off at the desired times.
The operator should retrieve and secure the sample as soon as possible after the sampling period
ends The sampler should then be manually turned on and allowed to run for two minutes A final
flowrate should be recorded on the sample data sheet. The final flowrate should be at least 150 liters per
minute The PUF cartridge should be removed, and the quartz pre-filter folded and placed in the top of
the PUF cartridge The PUF cartridge and pre-filter should be re-wrapped in the original aluminum foil
and placed back in the shipping can The can should then be tightly sealed. Complete the sample data
sheei and Cham-Of-Cusiody Record and seal the shipping can with a sample custody seal Finally, the
shipping can containing the sample should be placed in a cooler containing frozen eutectic salt packs (at
a nominal temperature of - 4° C) When all samples are collected from all sites, the cooler should be
sealed with sample custody tape for transport back to the laboratory.
Laboratory
Upon arrival of the metal container at the laboratory, the samples shall be stored in the metal
container in a refrigerator until submitted for extraction.
14 1 4 Collecting Samples for Metals Analysis Using the High Volume Sampler
The following is a synopsis of procedures which should be strictly adhered to for the collection of
samples for metals analysis in air This summary is adapted from 40 CFR. PART 50. APPENDIX B -
Reference Method For The Determination Of Suspended Paniculate Matter In The Atmosphere (High
V olume Method), and 40 CFR. PART 50. APPENDIX G - Reference Method For The Determination Of
Lead In Suspended Paniculate Matter Collected From Ambient Air.
The following procedures must be followed m preparation for collecting samples for metals analyses with
the High Volume sampler.
• All filters used will be supplied by the EPA National Filter Distribution Program, and of the
same quality as supplied to the State and Local Agency Air Monitoring Stations.
• Prior to use. all filters will be checked for pinholes, and desiccated at 15°C - 30°C, ± 3°C, and
less than 50 percent relative humidity. ± 5 percent, for at least 24 hours.
E1SOPQAM 14 - 6 May 1996
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E1SOPQAM 14-7 May 1996
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• A filter field blank will be taken to the field, but not exposed. Filter field blanks will be
analyzed by the laboratory to determine the concentration of metals contained in the filler
matrix The number of filter blanks will be determined based on a minimum of one blank for
each ten samples collected
• Cham-of-custody must be maintained for all samples.
Sample Collection Procedures
Samples will be collected using the High Volume sampler as described, and operated in accordance
with 40 CFR, PART 50, APPENDIX B-
• All flow calibration orifices will be traceable to a Primary Standard Rootsmeter Flows will
be corrected to EPA standard temperature and pressure (25°C and 760 mm Hg).
• Digital manometers used to determine flow rates will be checked against a U-Tube water
manometer prior to use in each study.
• Air Monitoring Team personnel will remove a 2-inch strip of the exposed filter from one end
and discard it Two 1-inch strips will be cut from the same end and transported to the
laboratory for analysis
Integrated Sample Collection
The following procedures should be followed to collect time integrated samples
• Initial and final flow rates will be determined with a calibrated orifice and a digital manometer
• After the sample has been collected, the filter will be folded lengthwise and placed in a filter
holder. The filter holder is then placed in an envelope and the envelope sealed
• A Cham-Of-Custody Record should be completed which contains the time of sampling, the
sampling interval, and the signature of the person taking the sample
After sample collection, all sample envelopes will be placed in an appropriate container. An EPA
custody seal will be placed on the container Filters will be cut by the Air Monitoring Team and
transported to the laboratory for analysis
1-4 1 5 Sampling and Analysis of Mercun in Ambient Air Using Arizona Instrument* Mercury Dosimeter
Tubes and the Model 511 Gold Film Mercury Vapor Analyzer
The following is a synopsis of procedures which should be strictly adhered to for the sampling and
analysis of mercury (Hg) in ambient air This summary- is adapted from the Arizona Instruments* (AZI),
Model 511. Gold Film Mercury Vapor Analyzer Manual
EISOPQAM 14 - 8 May 1996
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The following generic procedures should be adhered to at all times:
• Cham-of-custody shall be maintained for all samples
• A minimum of one trip blank shall be transported one per ten samples collected
• All mercury dosimeter rubes shall be cleaned and analyzed each sampling day prior to use
Dosimeter Cleanup
Each dosimeter tube should be connected to the AZI* model 412 dosimeter controller and AZI*
Gold Film Mercury Analyzer as shown in Figure 1 of the AZI* model 511 Mercury Analyzer Operation
Manual The mercury analyzer analysis cycle should be started and immediately afterward the dosimeter
controller's START button should be depressed. This will cause the gold plated wire inside the dosimeter
tube to heat up and liberate any elemental mercury that forms an amalgam on the gold plated wire inside
the dosimeter Continue this cycle until less than 2 ng of Hg is detected from the dosimeter tube Remove
the clean dosimeter tube from the dosimeter controller, tag it with the cleanup date and the operators name.
and connect the inlet and outlet dosimeter ports together with a clean - 8-inch section of 3/16-inch ID x
1/16-inch wall Tygon® tubing (this effectively caps the dosimeter tube).
Sample Collection
Each sampling pump will be calibrated with a mass flow meter before and after each sampling
event Connect the dosimeter to the battery powered sampling pump with Tygon* tubing Adjust the
sampling pump to obtain a flowrate of 50 cc/mm The sampling interval should not extend beyond 8
hours The following steps should be followed to collect each sample
Disconnect one end of the Tygon* tubing from the dosimeter tube and connect it to the battery
powered sampling pump
• Program the pump to run the desired number of hours Position the dosimeter rube inlet so
that there is no obstruction of flow Record the dosimeter tube number, site ID. sample date.
start time, and initial flowrate on the sample data form
• As soon as possible after the sampling event, disconnect the Tygon* tubing from the sample
pump and connect the loose end to the inlet of dosimeter tube. Record the elapsed time from
the pump display. Check the ending flowrate with a mass flow meter and record it on the
sample data form
Sample Analysis
Before any mercury analysis of dosimeter tubes, the AZI* model 511 should be calibrated The
AZI* model 511 should only be used under laboratory conditions. All glassware should be scrupulously
cleaned and used exclusively for mercury analysis. All Tygon tubing that is used should be new. The
following calibration procedure is adapted from the AZI* model 511 operation manual:
EISOPQAM 14 - 9 May 1996
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Calibration
• Calibration of the AZI* model 511 is accomplished by the reaction of a mercuric chloride
standard solution with stannous chloride which liberates elemental mercury. The elemental
mercury is sparged from an impmger for analysis in the mercury analyzer
• Before calibration, a film heat cycle should be initiated to clean the mercury analyzer sensor
• Fresh working 100 ng/ml mercuric chloride standards should be prepared daily from a 1000
ug/ml stock solution From the 100 ng/ml working standard, calibration standards of 10
ng/ml, 20 ng/ml, and 40 ng/ml should be prepared. Use the procedure outlined in the AZI*
operation manual to introduce the stannous chloride solution into the impinger containing the
40 ng/mJ standard. IMMEDIATELY depress the SAMPLE START button on the analyzer.
Use the calibration potentiometer to adjust the analyzer to read 40. Analyze the 10, 20. and
40 ng/ml standards to verify that the calibration curve is linear. All analyzer readings should
be within 2 ng of the actual values of the standards. Record the readings in the logbook
• Once the mercury analyzer is calibrated, connect an exposed dosimeter tube to the model 412
dosimeter controller Connect a zero filter to the inlet of the dosimeter tube Simultaneously
press the mercury analyzer SAMPLE START button and the dosimeter controller START
button Record the analyzer reading (in ng) in the logbook. Repeat this sequence three times
and sum the values. This value is the total ng of mercury that was captured on the dosimeter
rube
• Divide the sum of the mercury analyzer readings (in ng) by the total volume of air sampled (in
liters) to give the concentration of mercury present in ug/MJ
1416 Sampling for Dioxm And Dibenzoruran Analyses with High Volume PUF Samplers Using Method
TO-9
The following is a synopsis of procedures which should be strictly adhered to for use of the High
Volume Polyurethane Foam (PUF) sampling method for collecting samples for polychlormated dibenzo-p-
dio.xms and dibenzofurans analyses This summary is adapted from Method TO-9 of the COMPENDIUM
OF METHODS FOR THE DETERMINATION OF TOXIC ORGANIC COMPOUNDS IN AMRIFNT
A IK
Since this method requires High-Resolution Mass Spectrometry which the Region 4 laboratory does
not have, all sample media preparation and analysis will have to be contracted. At least one months notice
prior to sampling should be given to obtain a contract laboratory program (CLP) contract for any dioxm
and dibenzofiiran analysis It is important that the contract specify a number of details to assure accurate
results
• All of the PUF media and a representative number of each batch of quartz pre-filters should
be checked by the contract laboratory to assure that there is no contamination Each PUF plug
should be pre-spiked by the contract laboratory with dioxm and dibenzofuran surrogates as a
check of the accuracy of the method
EISOPQAM 14 - 10
May 1996
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• Each set of PDF plugs and quartz filters should be securely packed in sealed containers and
in coolers to prevent damage during shipment. The sampling media should be shipped air
freight to minimize the time between cleanup and sampling
• Cham-of-custody shall be maintained for all samples.
Sample Collection
The following procedure will be followed for the collection of all High Volume PUF samples for
dioxms and dibenzofurans analyses
Nylon gloves will be used when handling all PUF cartridges and quartz paniculate pre-filters
Assure that the red silicon upper and lower gaskets are in place in the PUF cartridge housing Remove
the PUF cartridge from the shipping can Unwrap and insert the PUF cartridge into the High Volume (Hi-
Vol) PUF sampler's chamber. Install the pre-filter in the filter holder using caution not to over tighten the
fittings The removed aluminum foil should be placed in the shipping container which then should be
resealed The container should be labeled with the site ID, the operators name, and the sample date, and
placed in the Hi-Vol PUF sampler enclosure until the sample is collected The Hi-Vol PUF sampler should
be turned on and allowed to run for two minutes An initial flowrate should be recorded on the sample data
sheet The timer should be set to turn the sampler on and off at the desired limes
The operator should retrieve and secure the sample as soon as possible after the sampling period
ends The sampler should then be manually turned on and allowed to run for two minutes and a final
flowrate recorded on the sample data sheet The final flowrate should be at least 150 liters/minute The
PUF cartridge should be removed, and the quartz pre-filter folded and placed in the top. of the PUF
cartridge The PUF cartridge and pre-filter should be re-wrapped in the original aluminum foil and placed
back in the shipping container and the container should be tightly sealed Complete the sample data and
sample custody sheets. Each shipping container should have a sample custody seal. Finally, the shipping
container containing the sample should be placed in a cooler containing frozen eutectic salt packs (at a
nominal temperature of - 4° C). When all samples are collected from all sites, the cooler should be
sealed with sample custody tape for shipment to the contract laboratory
Contract Laboratory
Upon arrival of the metal container at the contract laboratory, the samples shall be stored in the
metal container in a refrigerator until submitted for extraction
14 1 7 Mercury Sampling Using Gold-Coated Glass Bead Tubes
The following is a synopsis of procedures which should be strictly adhered to for the handling and
field use of gold-coated glass bead mercury sampling tubes
The following generic procedures should be adhered to at all times
• Polyethylene or Nylon gloves must be worn whenever handling any of the mercury sampling
traps (in the laboratory, during preparation for shipment, during field set-up, in field during
preparation for return shipment, and in the laboratory during preparation for analysis and
during analysis)
• Pre-cleaned mercury sampling traps which have been prepared for longer than 60 days shall
EISOPQAM 14-11 May 1996
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not be used
• Cham-of-custody shall be maintained for all samples.
• A minimum of one trip blank shall be transported one per ten samples collected
Laboratory
Upon completion of preparation of the mercury sampling traps, both ends shall be plugged with
Teflon male plugs, the plug connection wrapped in Teflon tape, and each trap placed in a plastic shipping
tube A serial number, expiration date, and a lot number label will be placed on each shipping tube The
batches of shipping tubes shall be placed in sealed lock-top plastic containers.
Air Monitoring Team
The Air Monitoring team will notify and keep the laboratory informed as to the anticipated number
of prepared mercury sampling traps needed for field use. On routine studies, the Air Monitoring Team
will notify the laboratory of needs at least two weeks in advance of needed pick-up date. Only the number
of mercury sampling traps needed for a maximum of 60 days (including trip blanks and extra sampling
traps for breakage) will be requested
• On the date of shipment or when loading out for a study, the Air Monitoring team will remove
the sealed plastic containers (which contain the mercury sampling traps sealed in plastic
shipping tubes) from the Air Laboratory.
• An appropriate amount of packing material shall be placed in the shipping container to prevent
breakage of the mercury sampling tubes
• On each sampling date, the plasnc container(s) will be removed from the refrigerator or cooler
for transport to the field At each sampling location the plastic container will be opened and
one mercury sampling tube will be removed (wearing clean polyethylene or nylon gloves)
The end plugs will then be removed from each end of the mercury sampling trap which will
be immediately placed on the sampling tram The end plugs will be placed back into the
shipping tube and the cap placed on the tube wrapped in Teflon tape. The shipping tubes will
be left in the sealed plastic container The same procedure will be adhered to at each sampling
location A trip blank will be opened, handled, and resealed at one site to evaluate potential
passive contamination
The sampler will be manually turned on and allowed to run for two minutes An initial flowrate
should be recorded on the sample data sheet The timer should be set to turn the sampler on and off at the
desired times
• Air monitoring personnel should retrieve and secure the sample as soon as possible after the
sampling period ends The sample pump should be manually turned on and allowed to run for
two minutes, and a final flowrate and the elapsed time from the elapsed time meter should be
recorded on the sample data sheet. The exposed mercury sampling trap should then be
removed from the sampling train wearing clean polyethylene or nylon gloves. The two end
caps shall then be removed from the shipping tube and placed on the ends of the sampling trap
The sampling trap will be placed back into the shipping tube, the lid tightened, and placed back
into the plastic container The same procedure must be followed at each sampling site.
EISOPQAM 14 . 12 May I996
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At the end of each study, the samples will be transported to the laboratory
EISOPQAM 14 -13 May 1996
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14.2 Criteria Pollutant Monitoring (Reference Monitors) for Air Pollutants for which National
Ambient Air Quality Standards have been Established
14 2 1 Monitoring Ozone in Ambient Air
The following is a synopsis of procedures which should be strictly adhered to for the monitoring
of ozone in air This summary is adapted from 40 CFR Part 50. Appendix D -Measurement Principle and
Calibration Procedure For The Measurement Of Ozone In The Atmosphere, and the Quality Assurance
Handbook for Air Pollution Measurement Systems. Volume II. Section 2 7 fEPA-600/4-77-Q27al
• Calibration systems will meet 40 CFR Part 50, Appendix D specifications for a Primary
Standard Calibration Photometer
• Calibration systems will be verified against the National Institute of Standards and Technology
(NIST) Standard Reference Photometer #10 before use.
• Monitor enclosures will meet the specifications of monitor reference/equivalent designation for
temperature control
• Probes must meet the requirements stated in 40 CFR Part 58 for materials and sample
residence time.
• All flow calibrations will be traceable to a primary standard. Flows will be corrected to EPA
standard temperature and pressure (25°C and 760 mm Hg).
• Cham-of-custody must be maintained at all times.
Monitoring Procedure
Monitoring will be conducted using the procedure as described, and in accordance with 40 CFR
Pan 50. APPENDIX D
• Monitors will be calibrated at the beginning and end of each study, and at least quarterly
during the study.
Monitors will be calibrated after major maintenance or when a quality assurance (QA) check
shows an out-of-control condition exists
• A zero/span check will be conducted daily on all monitors.
• Precision checks of all monitors will be conducted at least weekly.
• Quality assurance audits as specified in 40 CFR Pan 58, Appendix A will be conducted
quarterly, or at least once for short duration studies
• Data telemetry systems will be run in parallel with strip chart recorders. Strip charts will serve
as a permanent record and diagnostic tool.
After completion of the study, all monitoring equipment will be returned for final check-out. All
field documentation will be retained by the Air Monitoring Team.
EISOPQAM 14 - 14 May 1996
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14 2.2 Sampling of Paniculate Matter in Ambient Air as PM,0
The following is a synopsis of procedures which should be strictly adhered to for the sampling of
paniculate matter as PM,0 in air This summary is adapted from 40 CFR Pan SO. Appendix J - Reference
Method For The Determination Of Paniculate Matter as PMlf In The Atmosphere . and the Oualns
Assurance Handbook for Air Pollution Measurement Systems. Volume II. Section 2.11 (EPA-600/4-77-
027a)
• All filters used will be supplied by the EPA National Filter Distribution Program, and of the
same quality as supplied to the State and Local Agency Air Monitoring Stations
• Prior to use, all filters will be checked for pinholes, and desiccated at 15°C - 30°C ± 3°C. and
less than 50 ± 5 percent relative humidity, for at least 24 hours
• Initial and final (exposed) filter weights will be determined by air monitoring personnel One
of ten filters will be reweighed as a quality assurance check For batches less than ten, one
filter will be reweighed
• After sampling, filters will be desiccated as previously described.
• Cham-of-custody must be maintained for all samples
Sample Collection
Samples will be collected using the High Volume sampler as described, and operated in accordance
with 40 CFR Part 50. Appendix J
• All flow calibration orifices will be traceable to a primary standard Rootsmeter Flows will
be corrected to EPA standard temperature and pressure (25°C and 760 mm Hg)
• Digital manometers used for flow rate determinations will be checked against a U-Tube water
manometer prior to use in each study
• Volumetric flow controllers will be used on all PMIO samplers Flows will be determined using
the manufacturer's flow rate table supplied with the controllers. Flow rate tables will be
verified using a calibrated orifice on a routine basis, or at least annually.
Integrated Sample Collection
The following procedures should be followed to collect time integrated samples
• Initial and final flow rates will be determined with a digital manometer based on the
manufacturer's flow rate look-up table
• After the sample is collected, the filter will be folded lengthwise and placed in a filter holder.
The filter holder is then placed in an envelope and the envelope sealed
• A Cham-Of-Custody Record should be completed detailing the time of sampling and the
sampling interval, and should be signed by the person collecting the sample
After sample collection, all sample envelopes will be placed in an appropriate container An EPA
custody seal will be placed on the container prior to transpon to the Region 4 laboratory for final weighing
EISOPQAM 14 - 15 May 1996
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of filters
EISOPQAM 14 - 16 May 1996
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SECTION 15
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SECTION 15
FIELD PHYSICAL MEASUREMENTS
SECTION OBJECTIVE:
• Present the standard practices used for making field physical measurements.
15.1 Introduction
Field measurements of topographic features, water levels, time-of-travel, geophysical parameters.
physical dimensions, etc., are frequently required during field investigations conducted by the Branch. The
purpose of the investigation will determine the scope of these measurements.
All sampling locations used during field investigations should be depicted on an accurate drawing,
topographic or other standard map. or be referenced in such a manner that the location(s) can be firmly
established The Region 4 library has a complete collection of 7.5 minute USGS (1 24,000 scale)
topographic maps and a map copier is available
Each field measurement made should be traceable to the person(s) making the measurement and
to the field equipment used to make that measurement Equipment maintenance and calibration records
shall be kept in log books and field records so that the procedures are traceable. Time records shall be kept
in local time using the hour format, with the time recorded to the nearest five minutes or less
New employees should perform each of the physical field measurements described in this section
under the supervision of a senior technical staff member at least once before being permitted to make these
measurements on their own.
15.2 Horizontal Location Surveys
15 2 1 Introduction
Surveying is described as the an and science of determining the area and configuration of portions
of the earth's surface, and representing them on maps. Generally, surveying can be divided into two
categories or classes horizontal control surveying and vertical control surveying Horizontal control
sun-eying pertains to the measurement of the relative difference in the horizontal location of two or more
control points Vertical control surveying involves the measurement of the relative difference in vertical
location or elevation, of two or more control points and is presented in Section 15.3. This section discusses
the standard procedures, techniques, and methods used to survey or locate sampling locations or site
features horizontally. Basic surveying and field geology textbooks should be consulted for more detailed
information on this topic (See References 1, 2, and 3).
Several field methods, from traditional or classical methods to Global Positioning System (GPS)
techniques, may be used to horizontally locate sampling locations or various site features during field
investigations Traditional traverse methods used by the Branch utilize horizontal angle or direction
EISOPQAM 15 - 1 May 1996
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(azimuth/bearing) measurements and calculated horizontal distances from a starting point to a second point.
and from the second to the third, and so forth to the last point. The last point in a traverse is usually a
return to the starting point, thus making a closed loop. During a traverse for site control, sampling
locations or sue features may be located by employing various techniques at the traverse control points.
e g , by angle (azimuth or bearing) and distance measurements from a control point, by angular intersection
from two control points, by perpendicular offset from a line between two control points, by angle from one
control point and distance from another control point, etc
GPS methods utilize radio frequency measurements with multichannel receivers of the signals from
the global network of satellites that the Department of Defense has established Measurements of the
horizontal sampling locations or site features by GPS technology is based on the same principles used m
traditional surveying methods However, with GPS, hand held receivers measure distances to three or
more satellites of known positions and triangulate the position of the sampling location, site feature, or
point on earth More fundamental information on GPS technology may be found in Reference 4.
Regardless of the method(s) used, horizontal location surveys should be based on established
control points. A network of horizontally (and vertically) located control points has been established and
is continually maintained by the National Oceanic and Atmospheric Administration (NOAA) through us
National Ocean Survey (formerly U.S Coast and Geodetic Survey) The old horizontal datum, called the
North American Datum of 1927 (NAD27). has been replaced with the newer datum of 1983 (NAD83)
The system of horizontal control points has established latitude and longitude positions and provides the
basis for the coordinate grid systems used by many States.
When measuring horizontal angles, compensation should be made for the angle between true north
and magnetic north. This angle is called the magnetic declination. Field surveying methods should be
referenced to true north. The first step in this procedure is to determine the declination for the area of
work from an isogonic map Isogonic maps may be found in basic surveying and field geology textbooks
Existing information on horizontal control stations or coordinate grid data and their exaci locations
may be obtained from local, state, or federal departments or agencies. Typically, engineering or public
uorks departments of counties, cities, or towns may have data on file that is near the particular site being
investigated State or federal agencies which are good sources of useful data include.
• State highway or transportation departments
• State geodetic or land surveying offices
• State natural or water resources bureaus
• State geological surveys
• NOAA/National Ocean Survey
• United Slates Geological Survey
• Corps of Engineers, Department of the Army
• Soil Conservation Service
• Tennessee Valley Authority
• Bureau of Land Management
When exact locations of sampling points or other physical features at a site are needed, surveying
methods must be based on existing control data. If unavailable at the time of the investigation, and if
necessary, the sue property boundary survey, legal description, and any physical property corners or
monuments must be established by a professional Registered Land Surveyor (RLS). Often times, before
or when the surveyor is at a sue. the registered surveyor could be requested to set control data points for
use At a minimum, the registered surveyor would be asked to establish at least two control points upon
which the elevation and the State Plain (SP) coordinates are set Data on control points shall be of at least
E1SOPQAM 15 - 2 May 1996
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third-order accuracy. Control points will be permanent markers set at locations that are unlikely to be
disturbed by future site activities
If no existing control data exists in the site vicinity, an arbitrary point or points may be established
at a permanent location, e.g., set a nail or spike beneath the ground or set a nail and cap in asphalt or
foundation Coordinates for those points (and, therefore all other points) should be determined at a later
date Location of all control data used and all field measurements should be recorded in the field logbook
as outlined in Section 3 5
1522 Equipment Available
The following equipment is available for field use in conducting horizontal surveys-
• Topcon GTS-2, total station theodolite/electronic distance meter (EDM)
• Trimble Pathfinder Pro XL 8 channel or 12 channel GPS receiver
• tnpod(s)
• reflector prism(s)
• prism pole
• steel tape
• cloth tape
• right angle prism
• compass
1523 Specific Equipment Quality Control Procedures
Field surveying methods using appropriate and available equipment should be made only by those
personnel who have been trained to use them Field investigators must be trained and checked out in
surveying procedures by qualified staff before using this equipment.
Each piece of field equipment (as appropriate) should be numbered, and a log book should be kept
containing maintenance and calibration records for the equipment. Maintenance and calibration procedures
used for all surveying equipment are listed in the inspection logbooks.
Theodolite - This equipment should.
• be serviced and calibrated by a qualified private service shop annually or sooner if damaged
or suspected to be in error.
• be checked out using procedures outlined in basic surveying textbooks and appropriate users
manuals before use (See References 1. 2, and 3). and,
• be cleaned and maintained using procedures outlined in basic surveying textbooks and
appropriate users manuals during field use and before being returned to storage (See
References 1, 2, and 3)
GPS Receivers -- This equipment should.
• be serviced and calibrated by the manufacturer if damaged or suspected to be in error,
• be checked out using procedures outlined in the appropriate users manuals before use, and.
EISOPQAM 15 - 3 May 1996
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• be cleaned and maintained using procedures outlined in the appropriate users manuals durmt
field use and before being returned to storage.
Steel and Cloth Measuring Tapes - The following procedures should be used for all measuring tapes
• Measuring tapes will be calibrated against an Invar steel surveyors chain or the
theodohte/EDM both of which are traceable to the National Bureau of Standards (NBS)
Those steel tapes that are not within 0 01 foot per 100 feet or cloth tapes not within 0 02 foot
per 100 feet should be discarded
• All tapes should be checked for damage and should be cleaned before and after use
Compass - All compasses should
• be checked for proper movement of the compass needle. If the compass needle movement is
sluggish, the glass cover can be removed by prying a knife point under the spring washer. The
copper wire on the needle is then moved until the needle lies level (Reference 3),
• be checked for proper alignment of clinometer level. The clinometer is checked by setting the
clinometer to 0, and placing the compass on a surface that has been leveled exactly with either
a carpenters level or a water rube level. If the horizontal level bubble on the clinometer does
not rest at the center, the compass should be opened as previously described and the clinometer
level vial should be moved and rechecked as appropriate If the level vial becomes broken,
the compass must be sent to the manufacturer to be repaired (Reference 3), and
• be cleaned after use and before storage If the compass should become wet, the compass
should be opened as previously described and the interior dried using a toothpick and a piece
of soft cloth or soft paper Compasses should not be used, exposed to. or stored in strong
electrical fields (Reference 3)
Prism Poles and Reflector Prisms -- All of this equipment should:
• be checked for warpage and/or damage before use by sighting through the theodolite/EDM
while the poles/prisms are rotated in two planes at 90° intervals The bullseye bubble should
be reset if needed, and
• be cleaned daily after use and before being returned to storage.
1524 Procedures for Traversing
When traverse methods are used, at least two stations or control points of known horizontal
location (expressed in terms of a local or State Plane coordinate system) must be in the site vicinity These
control points can usually be set for the specific site by a governmental agency or registered land surveyor
The total station theodolite, which measures horizontal angles, vertical and/or zenith angles, and
slope distances, is set up over an existing control point. The theodolite is attached to the plate of the tripod
b\ a fastening screw and the bubble in the bullseye level is centered, or brought level by adjusting the
three-screw leveling heads appropriately Once the bullseye bubble is centered, the theodolite is rotated
90° at a time and the horizontal level bubble is checked and brought level using the three-screw leveling
heads The instrument is ready for use when, after repeated rotations, the bubble in the horizontal level
remains exactly in the center or middle of its housing
EISOPQAM 15-4 May 1996
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The rodman has either a range pole equipped with a reflector prism (single or triple) or a tripod
with the reflector prism. The prism is used to reflect the signal from the electronic distance meter in the
total station theodolite While located over the point(s) whose location is desired, the rodman holds the
range pole vertically by means of centering the bullseye bubble, or sets up the tripod and reflector prism
similarly as stated above The instrument man sights through the telescope on the theodolite, lines up the
horizontal and vertical cross-hairs on the center of the prism, and records the horizontal angle (H<).
vertical angle (V<), or zenith angle (Z<), and the slope distance (Ds) to the prism. The difference in
location between the point where the theodolite is set up and the point where the prism is held is determined
trigonometrically A compass and measuring tape could also be used to reference field measurements to
a map or vice versa.
The following examples depict some of the field measurements that must be considered and
accounted for, the calculations that must be performed, and the conversions that must be made when
traverse methods to horizontally locate sampling points or other site features are used
EXAMPLE 1, Horizontal Angles
Figure IS.2.1 illustrates that while the
instrument is at point A (a control point),
one reads the backsight angle (azimuth or
bearing) to point B. then turns and measures
the foresight angle (azimuth or bearing) to
point C The difference between the two
angles is the interior angle included at the
intersection of line AB and line AC. or the
horizontal angle (H<) The field notation
for the measurement of the angle above
would be represented as angle B-A-C
Typically, the first column to the left in the
field book is labeled (BS - =? • FS) or
Station and the second column is labeled H< (see Example 5, Field Notation).
Example 1:
Figure 15.2.1. Map view
showing horizontal angle B-A-C
EXAMPLE 2. Vertical or Zenith
Angles After the horizontal angle is
determined, the vertical angle (V<) is
measured (Figure 15 2.2) from point B to
point C to determine the angle between the
line of sight AC and the horizontal line AB
The vertical angle is the included angle
between a line connecting two points of
different elevations and a line horizontal to
the earths gravity The vertical angle in
Figure IS 2 2 is above the horizontal line
AB and is also called an angle of elevation
or positive angle and the field notation
should be preceded by a + sign If the
vertical angle is below the horizontal line
AB. it is called an angle of depression or
negative angle and the field notation should
be preceded by a - sign Note that most theodolites measure the adjacent zenith angle instead of the vertical
angle A zenith angle is simply the included angle between a line connecting the point exactly overhead
Dh (nonzontal angle)
Example 2:
Figure 15.2.2. Side view
showing vertical angle B-A-C.
EISOPQAM
15-5
May 1996
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and the point in question. For example: a zenith angle of 90° is a horizontal line or right angle and the
complimentary vertical angle would be 0°. The vertical angle can be obtained by subtracting the zenith
angle from 90°.
To determine the height of the point C, measure the slope distance (Ds) with the electronic distance
meter from A to C. Using the theodolite or transit, measure the vertical angle between line AC and AB
or the zenith angle. The height of point C would be obtained by the appropriate trigonometric formula:
Dv = (sin V<) Ds
or
Dv = (cos Z<) Ds
The horizontal distance (Dh), which is the distance used when drawing the map, would be obtained
by the appropriate formula:
Dh = (cos V<) Ds
or
Dh = (sin Z<) Ds
If the vertical distance to be measured was to the top of a building, tank, or other location where
the measurement of the slope distance is impractical, simply measure the horizontal distance and determine
the height by:
Dv = (tan V<) Dh
The field notation for the third column from the left in the field book is labeled: Z< or V< and
the forth column is labeled Ds/Dh (see Example 5 Field Notation).
EXAMPLE 3, Azimuths and Bearings:
When surveying, personnel should be able to
convert bearings to azimuths or azimuths to
bearings. An azimuth is an angular direction
based on the compass rose (Figure 15.2.3) which
divides a circle into 360°. The direction of
northeast is expressed as an azimuth of 45°. Its
reciprocal azimuth or the southwest azimuth
direction is 225°. An azimuth is always turned
clockwise from north or 0°. A bearing is the
direction turned, either clockwise or counter-
clockwise, with respect to north or south
(whichever is closer) on a compass. As a bearing,
the direction of northeast is expressed as North
45° East, while its reciprocal, or reverse bearing,
is expressed as South 45° West.
N
A bearing of N 25° E equals
an azimuth of 25°.
S
An azimuth of 135° equals
a bearing of S45°E.
Example 3: Figure 15.2.3. Compass
rose showing conversion
between azimuths and
bearings.
The following are examples of conversions:
EISOPQAM
15-6
May 1996
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BEARING TO AZIMUTH
N25°E 25°
S15°E 165°
N89°53'57"W 270006'03"
S10°18'W 190°18'
AZIMUTH TO BEARING
135° S45°E
280° N80°W
353°06'49" N06°53'H"W
06°35' N06°35'E
EXAMPLE 4, Coordinates When the rectangular grid coordinate points near a particular site are
obtained, personnel should be able to convert rectangular coordinates to polar coordinates This is
important since through this conversion, the azimuths and distances between each point can be obtained
and then used as the starting control points for the site control traverse. Computers or simple
programmable or non-programmable calculators are extremely useful in providing precise results from the
field surveying measurements The following is an example of manual conversion from rectangular to
polar coordinates
The instrument is set up at JORDAN88 and given the rectangular coordinates
Control Point North (y) East (x)
JORDAN88 9302.24 5605.23
SONIA93 8811 19 5706.13
The relative change m location between the north and east coordinates (from JORDAN88 to
SONIA93) respectively is
AN = -491 05 AE = 100.90
The negative symbol for AN indicates the relative movement from JORDAN88 to SONIA93
downward (-) along the y axis The positive symbol for AE indicates relative movement from JORDAN88
to SONIA93 to the right ( + ) along the x axis Solving the formula (Pythagorean theorem)
c =
b:
The resulting distance between JORDAN88 and SONIA93 is c = 501.31'
The azimuth is obtained by first computing the inverse tangent of the change in north divided by
the change m east
tan '(AN - AE) = -78.3886°
Note: The trigonometric formula above always gives the angle measured from the east-west
(x) axis. Depending on which quadrant that the angle points toward, the inverse tangent result that is
obtained is either subtracted from 90° or 270° (DO NOT CHANGE THE SIGN). When using this
procedure, n is wise to make a sketch showing the change in direction between the points relative to north
This will aid in visually and mentally seeing which geometric quadrant that the foresight angle falls in
relation to the instrument In the case above, this is a negative angle, expressed in decimal degrees, and
is measured from the (x) axis and points into the southeast quadrant The azimuth from JORDAN88 to
SONIA93 is obtained by subtracting from 90° (e g., 90° - (-78.3886°)) and then converting to degrees,
minutes, and seconds The resulting azimuth from JORDAN88 to SONIA93 is 168°23' 19" Note that the
two negatives cancel If the inverse tangent result pointed in the northeast quadrant direction, the azimuth
would also be subtracted from 90° and convened to degrees, minutes, and seconds. On the other hand.
EISOPQAM
15-7
May 1996
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when the inverse tangent result points in the southwest or northwest quadrant direction, the angle would
be subtracted from 270° (e.g., 270° - (inverse tangent result)) and then converted to degrees, minutes, and
seconds
EXAMPLE 5, Field Notation- The following is an example of the field notations for a traverse
to horizontally locate sampling points. Figures 15.2.4 and 15.2.5 show the field notations, on the left hand
side of the field log book and some of the physical features, sampling points, and traverse control points
that should be sketched on the right hand side of the field log book. The coordinates for each point are
then determined and usually entered in red ink after the traverse is finished. If the original coordinates are
from the old NAD27 datum, then the resulting coordinates should be converted to the new NAD83 datum
The official computer program, developed by the USGS, to convert latitude/longitude from the old NAD27
to the new NAD83 is called NADCON. Another program that is useful is CORPSCON which converts
between coordinates and latitude/longitude from both NAD27 and NAD83 (it has NADCON buili in as a
subroutine)
02/01/96 Project 96E 0001 . Land,5Surveyor •*..._
Region 4 5ite Name Benchmark - 9
City. State Wsatner. Clear. 0.5 mph.61_
SST irater»e pomi« trow property to locate 5 monitoring «H»
Tfi
MCI2 N-02S7.79 1-65SOH
MCI3 N=785176 E=62099fl
IP1 10 LICT2 . 4N= 6322 AEOL2J
c = a • b c = 6b 97
Lan |AH - £h)
'Iiriulh TPItO MCTJ =
V":1-'-
k- I* - i
^,::-,.-:;-^L.._;-J
a.- -. .
JS-J.-S4
L t.Ju
s . *" • V
l.iiii J
Example 5 Figure 15.2 4 Traverse field notation with site map
showing traverse points used to locate monitoring wells.
15 2.5 Procedures for Differential GPS
Differential GPS involves the use of two or more multichannel receivers One or more receivers
are used as the rover receiver(s) and usually only one is used as the base station. The base station and the
rover(s) must be within 200 to 300 miles of each other (accuracy increases as separation between base and
rover decreases) and have an unobstructed view of the sky The base is set up at a control point of known
horizontal location (usually expressed in terms of latitude, longitude, and elevation)
EISOPQAM 15-8 May 1996
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Triangulated coordinate positions from the satellites are recorded at the base, which will be
compared to the actual control point coordinates for the development of a correction factor to be applied
to other roving GPS units. Since the base station receiver and the rover receiver(s) synchronize with the
satellites clocks, data must be recorded or logged by both at the exact same time in order for the correction
factor to be applicable. Often times, base station data will be obtained via modem or disk after the field
data collection by the rovers. It is therefore extremely important to coordinate the logistics and planning
for using GPS techniques before leaving for the field.
All professional staff and field technicians must be trained in the use of the GPS equipment b\
qualified staff before using this equipment Specific procedures on the operation and setup of the GPS
equipment are described in detail in the operations manuals for each of the instruments All instruments
will be used consistent with the instructions contained within these manuals. A copy of each of the manuals
will be maintained by a designated person
32/01/96 "reject 96E-0001 Land* Surveyor -
Region 4 Site Name Ben Chmsrt «
Cit> Stale Weatner ClM,-. 0.5 mphJJ
Coortfinju*
-15 6C; N.6666 95
71966 t .6^2171
AQ'd^ IV '^ *"
es «s jj ^ _, t
|[.6i9ev-.
F.6**? V
ee"J2«S
Example 5 (continued) Figure 15.2.5. Second page of traverse field
notation.
EISOPQAM 15 - 9 May 1996
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15.3 Vertical Location (Elevation) Surveys
1531 Introduction
The Held of surveying that pertains to measuring the relative differences in elevation of two or
more points is called "running levels" or "Leveling". The two most commonly used methods are
Differential Leveling and Trigonometric Leveling. Differential leveling is the most precise and easiest
method because it utilizes "level" measurements with simple addition and subtraction Trigonometric
leveling is slightly less precise and more difficult as it uses vertical angle and distance measurements
combined with the principles of trigonometry Global Positioning System (GPS) equipment can obtain
elevation measurements, however this new technology is less accurate than horizontal measurements and
is not recommended for vertical locations This subsection discusses the standard procedures and
techniques used to obtain differences in elevation and are described in more detail in basic surveying and
Held geology textbooks (See References 1, 2. and 3).
Regardless of the method(s) used, elevation surveys should be based on established control points
A network of vertically (and horizontally) located control data points has been established and is continually
maintained by the National Oceanic and Atmospheric Administration (NOAA) through its National Ocean
Survey (formerly U. S Coast and Geodetic Survey) The system of vertical control points, or Benchmarks
(B Ms ), are referenced to a surface of fixed and precisely known elevation above mean s :a >evel and is
referred to as the datum or datum plane The datum for vertical control (elevation) is called tne National
Geodetic Vertical Datum of 1929 (NGVD29). formerly known as the 1929 sea level datum, or the soon
to be established North American Vertical Datum of 1988 (NAVD88).
Sources of existing information on benchmark data and their locations may be obtamea from local.
state, or federal departments or agencies Typically, engineering or public works departments counties,
cutes. or towns may have data on Hie that is near the particular sue being investigated Sta: ederal
agencies that are good sources of useful data include.
• State highway or transportation departments
• State geodetic or land surveying offices
• State natural or water resources bureaus
• State geological surveys
• NOAA/Nauonal Ocean Survey
• United Suites Geological Survey
• Corps of Engineers. Department of the Army
• Soil Conservation Service
• Tennessee Valley Authority
• Bureau of Land Management
When the exact elevations of sampling locations or other physical features are needed, benchmarKS
of precisely known elevation should be used when leveling If necessary, a registered land surveyor couid
be requested to set at least two third-order accuracy vertical control points or benchmarks The vertic.il
control points should have established elevations referenced to NGVD29 or NAVD88
If no benchmark is located in the site vicinity, an arbitrary temporary benchmark should be
established on a permanent location, e g . bridge wmgwall, foundation, or a nail or spike in a tree or
telephone pole The elevation of the temporary benchmark (and, therefore all other points) could be
determined at a later date As with all field work, the location of benchmarks used should be shown on
the sue sketch map and all field measurements should be recorded in the field logbook as outlined in
Section 3 5
EISOPQAM 15-10 May 1996
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1532 Equipment Available
The following equipment is available for field use in conducting elevation surveys in support of
site investigations.
Differential Leveling
• Sokkia B20 or Lietz B2C, precision automatic level
• tripod
• telescoping level rod
Trigonometric Leveling
• Topcon GTS-2, total station theodolite/electronic distance meter (EDM)
• tnpod(s)
• reflector prism(s)
• prism pole
• cloth or steel tape
• compass
1533 Specific Equipment Quality Control Procedures
Field surveying methods using this equipment should be made only by those personnel who have
been trained to use them. All field investigators must be trained and checked out in surveying procedures
by qualified staff before using this equipment
Each piece of field equipment (as appropriate) should be numbered, and a log book should be kept
containing all maintenance and calibrations made on the equipment The specific maintenance and
calibration procedures found in Section 15.2 3 should be used for all equipment listed above
1534 Procedures for Differential Leveling
The level, or instrument, is set up by the instrument man at a location not more than 250 feet from
the benchmark and at a height above the benchmark and the next point(s). The level is attached to the plate
of the tripod by a fastening screw and the bubble in the bullseye level is centered, or brought level by
adjusting the three-screw leveling heads accordingly Once the bullseye bubble is centered, the level is
rotated 90 degrees at a time and the horizontal level bubble is checked and brought level using the three-
screw leveling heads The level is ready for use when, after repeated rotations, the bubble in the horizontal
level remains exactly in the center or middle of its housing
The rodman holds the rod as plumb (vertical) as possible on the benchmark so that the instrument
man can read where the horizontal cross-hair in the telescope of the level intersects the graduations on the
rod The rodman "rocks" the rod in two planes, when instructed by the instrument man, to obtain a level
reading The rod is white with large red numbers which indicate the foot-marks and smaller black numbers
which indicate the tenths of feet and has black graduations the entire length which indicate hundredths of
feet The instrument man sights through the telescope and takes the first rod reading which is called a
backsight (denoted BS or + in the field log book). The backsight ( + ) reading added to the elevation of
the benchmark gives the height of the level, or instrument, (denoted H.I in the field log book) Next the
rodman holds the rod on a point (called a turning point and denoted TP) of fixed but unknown elevation
such as a nail in the ground, spike in a tree or telephone pole, or the top of a fire hydrant. The instrument
EISOPQAM 15-M May 1996
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man then takes his second rod reading which is called a foresight (denoted FS or - in the field log book)
If the foresight (-) reading is subtracted from the H.I., the result is the elevation of the point That is. the
difference between the first reading obtained from the benchmark and the second reading obtained from
the point is the difference in elevation between the point and the benchmark Note that the distance
between each sighted reading should not ordinarily exceed 250 feet with turning point backsight and
foresight distances deviating no more than 50 feet from one another.
The instrument man then goes ahead of the rodman, sets the level up as stated before and takes a
rod reading (backsight) from the previous turning point. The rodman then moves ahead of the instrumeni
man for a new turning point rod reading (foresight) and so forth until the desired final point is located
vertically Once the final point is located, the instrument man breaks the set up of the level (i.e., changes
the H I) and re-levels the level The instrument man and rodman then run levels from the last or final point
to the first point or benchmark. This is called making a closed circuit or closed level loop
When practical, leveling should be conducted to form a closed circuit. That is, the level circuit
or loop should close back in close agreement to a benchmark by within 0.02 foot of the original reading
or third order accuracy whichever is greater If the level circuit does not close within these limits of
accuracy, then the level circuit must be repeated until this accuracy is attained Third order accuracy is
defined by the formula- 0.05 foot x (/number of miles run), which means for a one-mile level circuit, the
closure should be within five hundredths of a foot Figure 15.3 1 is an example of typical field notations
for differential leveling
02/01/96 Fr0,eci 96E 0001 i
Region 4 Site Nam- C
.Cit> Scale n
5tat io'"/lroi''.: » or B5 HI
S k* £23 6 13 25 69
TPJ 22-: 2162
•r •• •
' ~ "S
'•• r
•";: 739 194-
•S-.-3 959 20 7g
; ••• t22
•
e*ine< Ciea- 0 5 mph (j
19&60
6i 19 b£
\J\: "52
11 '3 969
u <*i e9?
Hi?
62: 11 '9
: 2: 19 K
Remarks
Top of brass cap in concrete mon marked B W 523 EL c!95g;
Scl nail in young
KB spite in telephone pele NWeprner Athens 51 and Ceorj.a *\ve
Ground _»hot at MM/01
Waitr surface of cypress swamp
invert of weir 01 south o>f plant
~- - >- ««~. . _. c.. _ _. _
(Break setup to run levels back]
-*!L*P'*g ]" telephene pole KIW corner Alnens St and CeO'gia /-ve
5ft n»i in ^pakjor^emppraiyjiencn marl 0
C»ecte«» »ito_BM 523 [e** -0 01J
_&rea^setup_^puijnstrument away
Example 1 Figure 15.3.1 Field notation for differential leveling.
EISOPQAM 15 • 12 May 1996
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15.3.5 Procedures for Trigonometric Leveling
The total station theodolite, or instrument, is usually set up above a benchmark and the elevation
of the instrument (H.I.) must be obtained. The theodolite is attached to the plate of the tripod by a fastening
screw and the bubble in the bullseye level is centered, or brought level by adjusting the three-screw
leveling heads accordingly. Once the bullseye bubble is centered, the theodolite is rotated 90 degrees at
a time and the horizontal level bubble is checked and brought level using the three-screw leveling heads.
The instrument is ready for use when, after repeated rotations, the bubble in the horizontal level remains
exactly in the center or middle of its housing.
The rodman has either a range pole equipped with a reflector prism (single or triple) or a tripod
with the reflector prism. The prism is used to reflect the signal from the electronic distance meter in the
total station theodolite. While located over the point(s) whose elevation is desired, the rodman holds the
range pole level by means of centering the bullseye bubble, or sets up the tripod by means of centering the
bullseye bubble with the three-screw leveling heads. The instrument man sights through the telescope on
the theodolite, lines up the horizontal and vertical cross-hairs on the center of the prism, and takes a
reading of both the vertical angle (V<) and the distance to the prism. The difference in elevation between
the theodolite and the prism is determined trigonometrically. A compass with a clinometer and a measuring
tape could also be used for field measurements or as a map reference.
The following three examples graphically depict the distances that must be considered and
accounted for when using the trigonometric leveling method to compute the vertical changes in elevation.
The field notation for trigonometric leveling follows each example.
Example 2: The elevation at point A in Figure 15.3.2 is 100.00 ft. The instrument is set up 5.92
ft. above point A which makes the height of the instrument (H.I.) 105.92 ft. Given a slope distance (Ds)
shot to the prism (distance AB) of 323.88 ft. and a positive vertical angle (V »m
-------
EISOPQAM 15 - 14 May 1996
-------
The method described in Figure 15.3.2 only accounts for the relative difference in elevation
between the theodolite (H.I.) and the center of the prism. The distance that the prism is held above the
point in question must be subtracted from the resulting elevation of the prism to obtain the elevation of the
point. Substituting in the trigonometric formula:
elevation difference = 323.88 ft. x sin(5°30') = 31.04 ft.
The elevation of point B is: 105.92 ft. + 31.04 ft. - 5.23 ft. = 131.73 ft.
Example 3: The elevation at point D in Figure 15.3.3 is 100.00 ft. The instrument is set up 5.92
ft. above point D which makes the height of the instrument (H.I.) 105.92 ft. Given a slope distance (Ds)
shot to the prism (distance DE) of 323.88 ft. and a negative vertical angle (V S'Tyf" . -
Region 4 Site Name Ben Cnmark • f
* o-- &5 Hi -orF5 Elevation Remarks
5 92 105.92 UO 00'
323 SB' 0; H.I. (105.92')
, ,,. _ P:Elev.= 100.00'
•5 3u ./» p
c, »•»• f.a pc V J \ ~-^^ -53O
1 . s ^-^ -^ ,' theodolite eno pr&rr
FE = CE «»in n^tKa.r:t. . isaomc pom:
(523'J
Example 3: Figure 15.3.3. Trigonometric level notation showing side
view when elevation of point desired is below instrument.
EISOPQAM
15- 15
May 1996
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Example 4 When the measurement of
the slope distance is not possible, differences in
elevation can be determined using the law of sines
from trigonometry
sin a _ sin 0 _ sin
a b c
or
sin a
sin
sin
Example 4
elevation
sines.
Figure 15.3.4. Spot
differences using law of
Spot elevation differences can be
determined by taking only three measurements
(shown enclosed in the boxes of Figure 15.3.4) The measurements can be obtained with the total station
theodolite or by using a compass (equipped with a clinometer) and a measuring tape. In Figure 15.3 4 the
vertical angle (V<) is measured at two locations (A and midway between A and C) and the horizontal
distance (Dh) between those two measurements is also measured. Since the sum of the interior angles of
each triangle should equal 180°, all the other interior angles are calculated. Substituting the measurements
into the law of sines and solving for x and y shown in Figure 15.3.4:
1135'
sin 10.5°
kin I.S*M in V
sin 10 5°
161.36'
sin 25.5°
161.36'
sin 90°
= 69.4'
Note that this method above only accounts for the relative difference m elevation between point
A and the point in question, point B If an instrument, such as a compass or theodolite, is used at point
A. the H_L at point A must be added to the resulting elevation of the point in question The field notation
would include the figure drawing, all field measurements, and all of the calculations.
EISOPQAM
is-16
May 1996
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15.4 Bathymetry
1541 Procedures
Recording fathometers are used to provide bathymetric traces of water depths Because water
depths are time dependent (especially in tidal areas), the date and time of all traces should be noted
Operation manuals provide operation and calibration procedures to be followed In particular, tide and
draft adjustments provide datum calibration in regard to the respective tidal amplitude and sensor probe
depth During the initial setup of each survey, the fathometer calibration should be checked against a field
measurement of water depth made using a graduated sounding line. All traces should be noted with
transect description, chart speed, direction of travel, pertinent reference points, and Loran/GPS (if
available) and then indexed to a site map When working in tidal areas, a water stage recorder (see Section
15 5) should be positioned to provide a histogram of water levels to correlate with the bathymetric trace
154.2 Equipment Available
The following equipment is available for bathymetnc surveys-
• recording fathometers,
• water level recorder and/or referenced gaging station(s),
• calibrated sounding hne(s), and
• Loran/GPS instrumentation
1543 Specific Equipment Quality Control Procedures
All equipment used for bathymetnc studies should be numbered and a record should be kept of all
maintenance and calibration procedures The following procedures should be used to maintain and
calibrate bathymetric measurement equipment
Recording Fathometers
These fathometers should be
• Calibrated and maintained according to the manufacturer's instructions before use The chart
speed should be checked against a reliable time source before the instrument is sent to the
field
• Checked in the field against a field measurement of water depth utilizing a calibrated sounding
line
• Cleaned daily after use and prior to being stored.
Sounding Lines
All sounding lines will be calibrated against a steel surveyors tape and should be accurate ±3
percent
E1SOPQAM 15 - 17 May 1996
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15.5 Surface Water Stage/Tape Downs
15 5.1 Procedures
Water level recorders provide a time series record of water levels. When necessary, these
instruments should be referenced to National Geodetic Vertical Datum (NGVD) All water level tracings
should be noted with beginning and ending date and time, site location, stage scale, and time scale and
initialed by the field investigators Standard USGS staff gages should be employed at each water level
recorder sue to provide a reference and check on the recorder trace. Water stage should be recorded to
the nearest 0 01 foot where possible
Tape downs provide instantaneous water stage as referenced to a known elevation. An engineering
tape is fashioned with a plumb bob to measure from a bridge deck or other reference point to the water
surface The plumb bob provides weight for the tape as well as providing a discernible contact with the
water surface All measurements should be to the nearest 0.05 foot accompanied by a date, time, and
station location The exact reference or point from which a tape down is measured should be permanently
marked on the reference (wing wall or bridge rail by etching a reference with a chisel, etc ) and a complete
description of the reference should be made in the field records.
Both of these procedures (water stage and tape downs) are predicated upon accurate references to
established measuring points As mentioned above, the NGVD is an established datum that provides
correlation of water surface recordings to engineering structures (bridge, wing walls, sea wall caps,
clanfier cat walks, etc.) When recording water level dynamics in relation to a particular flow device, the
datum is established in relation to the flow device reference point. The flow through rectangular and V-
notch weirs, for instance, are proportional to the water level referenced to the weir crest or, m the case
of partially filled pipes, the flow rate is proportional to the depth of flow. Therefore, when employing a
water level recorder or tape down on primary flow devices, the reference or datum is the weir crest or in
the case of pipes, the invert (see Section 18. Flow Measurement).
1552 Equipment Available
The following equipment is available for surface water stage/tape down measurements
• Model F Stevens Stage Recorder(s),
• Model A-71 Stevens Stage Recorder(s),
• Stevens Model GS-93 Endcoders and Loggers,
• ISCO flow meter(s) and Recorder!s),
• USGS staff gage(s), and
• Weighted steel measuring tapes.
1553 Specific Equipment Quality Control Procedures
A log book will be kept of all equipment used for making water stage/tape down measurements.
The following maintenance and calibration procedures should be used and recorded in the log book for all
equipment using for water stage and tape down measurements.
EISOPQAM 15 - 18 May 1996
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Stevens Model A-71 and Model F Stage Recorders
These stage recorders should be
• Maintained according to the manufacturer's instructions The time and vertical scale should
be adjusted to read within two percent of full scale.
• Checked in the field by comparison with a staff gage. During field measurements, the vertical
accuracy should check within 0.05 foot
• Cleaned and maintained before storage.
Stevens Model GS-93 Endcoder
This instrument attaches to the A-71 and Model F stage recorders and uses solid state memory
The instrument stores water level data at programmable frequencies onto data cards The Endcoder should
• Be maintained according to manufacturer's instructions and checked in the field by comparison
with a staff gage. The vertical accuracy should check within 0.05 foot
• Be cleaned and maintained before storage.
1SCO 1870. 2870. 3210. and 3230 Flow Meter and Recorder^
See specific quality control procedures for this equipment in Section 18, Flow Measurement
USGS Staff Gapefs)
USGS staff gages should
• Be checked for damage, warpage. legibility, etc . before use Any damaged or illegible staff
gages should be discarded
• Be cleaned after use before being stored
Weighted Steel Measuring Tapes
Weighted steel measuring tapes should
• Be calibrated against the Invar steel surveyor's chain The calibration should be within 0 01
foot per 10 feet of length
• Be checked for damage before use, damaged tapes should be recalibrated or discarded
• Be cleaned after use and prior to being stored.
EISOPQAM 15 - 19 May 1996
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15.6 Time-of-Trave!
15 6 1 Introduction
Three principal methods are used to determine time-of-water-travel time in streams, i e . surface
floats, measurements of cross sectional velocity, and tracers such as dye.
A very rough method for preliminary estimates of time-of-water-travel consists of dropping sticks
or other buoyant objects in the stream reach under observation, and noting the time required for them to
float an estimated 10 feet or some other convenient distance. The velocity estimates are too inaccurate for
use in interpretation of data or final reporting, but can be useful in preliminary planning of studies and in
subsequent more precise measurements of time-of-water-travel.
Stream velocities at gaging stations, measured by the U. S. Geological Survey in developing rating
curves, may be applied to the entire reach under observation to estimate time-of-water travel This is
somewhat more refined than the floating objects estimates, but can still be far from accurate There rarely
are more than one or two gaging stations in most stream reaches being studied. Stream channels generally
are restricted at gaging stations and velocities there are generally higher than average velocities throughout
the reach Cross sectional velocities can also be determined at locations designated for a particular srud\
Tracer dyes provide a direct and highly accurate method of determining time-of-travel This is the
preferred method if resources are available
1562 Procedures
Floats
Surface floats may be followed downstream and timed for known distances to determine time-of-
water-iravel This requires the use of considerable judgment, for floats tend to travel into quiet or edd>
areas, or to become stuck on tree limbs, the stream bank, or other obstacles The floats must frequently
be retrieved and returned to the stream current The principal judgment factors are how long the floats
should be left in quiet areas before retrieval and where they should be placed in the current.
Surface water velocity is greater than the average for the entire stream, and a correction factor
must be applied to the surface velocity An average velocity of about 85 percent of that of the surface
velocity is a reasonable rule-of-thumb value
Cross Section Measurements
The measurement of cross sectional velocities at frequent longitudinal intervals and the calculation
of average velocity m the stream constitutes a time consuming method of obtaining time-of-water-travel
The longitudinal intervals at which cross sections should be measured vary with the characteristics
of the stream channel One cross section per mile may be adequate for streams with reasonably uniform
channels Cross sections at every tenth of a mile may be desirable for streams with irregular channels
Cross section measurement methods are described in detail in Section 18
EISOPQAM 15-20
May 1996
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Tracers
The most accurate method of measuring time-of-travel involves following and measuring a tracer
Some conservative constituents such as salt, or radioisotopes may serve as tracers, however, Rhodamme
WT dye is the most common tracer used Rhodamme WT can be detected at concentrations as low as 0 01
ppb by a fluorometer
Prior to injection into the stream, the concentrated dye is often diluted with stream water This
insures immediate maximum dispersion Addition of concentrated dye without dilution may result in
incomplete dispersion, particularly in shallow streams. Calibration curves should be developed for each
study with particular emphasis on accounting for natural background fluorescence.
The dye should be distributed across the stream at the upstream point, as nearly instantaneously
as possible The ideal distribution produces a narrow band of tracer in a uniform concentration across the
stream The band of tracer mixes with water ahead of and behind it by diffusion, or longitudinal mixing.
as it moves downstream to produce an increasingly wider band. The peak concentration remains near, but
somewhat downstream of, the center line of the band and decreases as longitudinal mixing proceeds. The
times-of-water-travel to downstream points are the differences between the time the dye was added to the
stream and the times the centroid of the dye mass arrives at downstream points The length of the dye
cloud and the peak concentrations produces a measure of mstream dispersion
If Rhodamme WT dye is used as the tracer, peak concentrations from 1 0 to 50 ppb allow
satisfactory definition of the dye concentration curve
Most methods of calculating the dosage of dye needed at the upstream point involve estimates of
one or more stream characteristics, such as flow, velocity, length of reach, volume in the reach, cross-
secnonal area, average depth, or the roughness coefficient "n" of Manning's formula. The USGS has
produced excellent publications regarding time-of-travel techniques, i.e , "Measurement of Time-of-Travel
and Dispersion by Dye Tracing" (5) and "Fluorometnc Procedures for Dye Tracing" (6)
The stream should be sampled frequently as the dye arrives at the downstream point to define the
tracer concentration versus time curve with special emphasis on the peak. The frequency may be varied
from continuously or from once each minute to once every 30 to 60 minutes, depending on how wide the
band of dye has become at the sampling point The dye may be missed altogether by overestimating the
time required for it to travel downstream Much time may be wasted, on the other hand, waiting for it to
arrive if the ume-of-travel is underestimated All information that will contribute to the best possible
preliminary estimate of the time required should be used.
There are two primary methods by which the stream water can be sampled and analyzed for dye
A submersible pump can be used to pump the dye continuously through a fluorometer or the stream
samples can be grabbed (either by hand or by automatic sampler) at specified frequencies and then placed
into the fluorometer individually With the "flow-through" version, a strip chan recorder connected to the
fluorometer can be used to plot the tracer concentration versus time. Some fluorometers have internal data
loggers to provide this function. Readings directly from the fluorometer scale or conversion to dye
concentration can be manually plotted against time when the grab sampling technique is used
A version of the grab sampling technique would be to use an automatic water sampler which
discharges into separate bottles The sampler is pre-set to collect samples at certain intervals, at the end
of the sample collection time, the discrete samples should be analyzed and the concentration determined
for each The concentrations are then plotted against time.
EISOPQAM 15 - 21 May 1996
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For proper determination of travel times, samples should continue to be analyzed until the stream
background concentration following the peak is measured. With a time versus concentration plot from
background level to peak to background level, the centroid, and thus actual travel time, can be determined
The trailing edge of the dye cloud should generally be monitored until the instream tracer concentration
is no more than 2 to 5 % of the peak concentration
Prior to conducting tracer studies in freshwater systems, water supplies should be inventoried to
insure that the dye tracer concentrations will not impart color to downstream public or private water
supplies Rhodamme WT concentrations m the dye cloud should be maintained below 10 ppb at water
supply intakes
1563 Equipment Available
The following equipment is available for time-of-travel studies:
• fluorometers,
• tracer standards,
• automatic samplers,
• pumps,
• recorders,
• flow meters, and
• floats
15.7 Dilution Studies
15 7 1 Procedures
A great deal of the previous section (time-of-travel studies) applies to this section and USGS
publications provide references 10 appropriate techniques, in particular "Measurement of Discharge by
Dye-Dilution Methods" (7)
Dilution studies using tracer dyes evolved from "mass conservation" principles, i.e , a known mass
of tracer is introduced at an upstream point, and after mixing with the water to be traced, this mass should
be accountable at downstream locations Rhodamme WT provides an adequate tracer for most
investigations This dye is slightly photoreactive Decay rates (ekl where k=0.034/day for exposure to
full sunlight) are reported in the literature Due to limited light penetration, actual rates are much lower
than this value and can be established through on-sue bottle tests Other tracers either introduced into an
upstream point or in some instances occurring at the upstream point are often used The high degree of
accuracy and detection ability of fluorometers plus the solubility properties of tracer dyes make them the
technique of choice
In dilution studies, the tracer dye is precisely metered into the waters to be traced and then
monitored after mixing via a fluorometer at downstream stations. This series of events requires highly
controlled metering rates and very accurate fluorometric analyses. State-of-the-art fluorometers make the
dilution study program a valuable assessment tool
Procedure
The principal of superposition as developed by Kilpatrick et al of the USGS is a reliable method
to determine dilution levels of wastewaters in receiving estuaries (8). A tracer dye is metered into the
E1SOPQAM 15 - 22 May 1996
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wastewater stream during a tidal cycle Successive slack tide measurements of dye concentrations in the
estuary at selective distances from the outfall produce a series of concentration curves. By superposition,
the accumulative concentration at each station provides a determination of the ultimate concentrations or
steady-state concentration of a continuous discharge By simple proportioning, with due regard to tracer
photo decay, the dilution levels of the discharge can be produced for selective points in the estuary
Calculation Procedure
Vt
Where
C» = Ultimate concentration of wastewater at point of interest
C, = Ultimate concentration of tracer (by superposition) at point of interest
t = Tidal days to ultimate concentration
ekl = Photo decay of tracer
V, = Wastewater discharge per tidal day
V, = Volume dye released in tidal day
Example
Assume After 5 tidal days the tracer clears to the area of interest and,
C, = 100 ppb
k = 0.005 per tidal day (based on-site bottle tests)
ekl = 1.03 (ultimate concentrations obtained in 5 tidal days)
V. = 100.000 gal/ndal day
V, = 10 gal/for one tidal day
Then C. = 1.030.000 ppb
or
= 0.103% wastewater
Investigations of industrial and municipal facilities for NPDES permit compliance require
measurements of discharge rates Often encountered during these investigations are flow measuring
devices such as orifices and magnetic meters which are inaccessible for measurements of flow by standard
equations relating to hydraulic head and structure size. The following provides a direct technique for
EISOPQAM 15 - 23 May 1996
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measurement of flow through these devices using dye tracers.
Calculation:
The discharge rate through any structure can be defined by the following mass balance equation.
MASS BALANCE EQUATION
q,) = (C,) (Q: + q,)
Q3 = (C,) (q,) - (CJ (q,)
Where:
Q2 = pipe flow rate
C2 = tracer concentration after mixing
q, = tracer injection rate
C, = tracer injection concentration
Assuming a constant discharge rate and complete mixing of the tracer in the waste stream, the task
is (1) to inject into the waste stream a tracer at a constant rate and constant concentration and (2) to
measure the concentration of the tracer after mixing with the waste stream.
It is suggested that at least three injection rates and resulting mixed tracer conceniration
measurements be used to calculate the discharge rate.
15.7.2 Equipment Available
The following field equipment is available for dilution studies:
• fluorometer,
• metering pump,
tracer standards, and
• pumps.
15.7.3 Specific Equipment Quality Control Procedures
See previous section. The metering pump should be calibrated before and during use. Field
calibration data should be recorded in the field records.
E1SOPQAM 15 - 24 May 1996
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15.8 Ground Water Level Measurements
1581 General
The measurement of the ground water level in a well is frequently conducted in conjunction with
ground water sampling to determine the "free" water surface. This potentiometric surface measuremeni
can be used to establish ground water flow direction and gradients Total well depth and ground water
level measurements are needed to determine the volume of water in the well casing prior to purging the
well for sampling purposes
All ground water level and total depth measurements should be made relative to an established
reference point on the well casing and should be documented in the field records. To be useful for
establishing ground water gradient, the reference point should be tied in with the NGVD (National
Geodetic Vertical Datum) or a local datum. For an isolated group of wells, an arbitrary datum common
to all wells in that group may be used if necessary.
1582 Specific Ground Water Level Measuring Techniques
Measuring the depth to the free ground water surface can be accomplished by the following
methods (9). Method accuracies are noted for each of the specific methods described below
• Electronic Water Level Indicators - This instrument consists of a spool of dual conductor
wire, a probe attached to the end. and an indicator When the probe comes in contact with the
water, the circuit is closed and a meter light and/or buzzer attached to the spool will signal the
contact Penlighi or 9-volt batteries are normally used as a power source Measurements
should be made and recorded to the nearest 0 01 foot
• Weighted Tape -- This method is similar to the "bell sounder" method, except that any suitable
weight, not necessarily one designed to create an audible pop, can be used to suspend the tape
The weight should, ideally, be made of a relatively men material and should be easily cleaned
Measurements should be made and recorded to the nearest 0 1 foot.
• Chalked Tape - Chalk rubbed on a weighted steel tape will discolor or be removed when m
contact with water Distance 10 the water surface can be obtained by subtracting the wet
chalked length from the total measured length The tape should be withdrawn quickly from
the well because water has a tendency to rise up the chalk due to capillary action
Measurements should be made and recorded to the nearest 0.01 foot This method is noi
recommended if samples are to be collected for analyses of organic or inorganic contaminants
• Other Methods -- There are other types of water level indicators and recorders available on
the market such as the sliding float method, air line pressure method, and electrical and
automatic recording methods These methods are primarily used for closed systems or
permanent monitoring wells Acoustic water level indicators are also available which measure
water levels based on the measured return of an emitted acoustical impulse Accuracies for
these methods vary and should be evaluated before selection. Any method not capable of
providing measurements to within 0 1 foot should not be used.
EISOPQAM 15 - 25 May 1996
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15 8.3 Total Well Depth Measurement Techniques
The bell sounder, weighted tape, or electronic water level indicators can be used to determine the
total well depth This is accomplished by lowering the tape or cable until the weighted end is felt resting
on the bottom of the well. Because of tape buoyancy and weight effects encountered in deep wells with
long water columns, it may be difficult to determine when the tape end is touching the bottom of (he we!)
Care must be taken in these situations to ensure accurate measurements. All total well depth measurements
must be made and recorded to the nearest 0 1 foot.
1584 Equipment Available
The following equipment is available for ground water level and total well depth measurements
• weighted steel measuring tapes
• electronic water level indicators
1585 Specific Quality Control Procedures
Devices used to measure ground water levels should be calibrated against the Invar steel surveyor's
chain These devices should be calibrated to 0.01 foot per 10 feet length. Before each use, these devices
should be prepared according to the manufacturer's instructions (if appropriate) and checked for obvious
damage These devices should be decontaminated according to the procedures specified in Appendix B
prior to use at the next well. All calibration and maintenance data should be recorded in a log book
EISOPQAM 15 - 26 May 1996
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15.9 References
1 Breed, C. B and G L Hosmer, The Principles and Practices of Surveying Volume I. Elementar\
Surveying. Eleventh Edition, John Wiley and Sons, Inc.: New York, New York
2 Breed, C B , and G L Hosmer, The Principles and Practices of Surveying Volume II. Higher
Surveying. Eighth Edition, John Wiley and Sons, Inc. New York, New York.
3 Compton, R. R , Manual of Field Geology. John Wiley and Sons, Inc.. New York, New York 1
4 United States Environmental Protection Agency, 1992. GIS Technical Memorandum 3 Global
Positioning Systems Technology And Its Application In Environmental Programs US EPA
Document # EPA/600/R-92/036
5 Kilpatnck, F A , L.A Martens, and J.F. Wilson, "Measurement of Time of Travel and Dispersion
by Dye Tracing," Chapter A9, Applications of Hydraulics. Book 3. United States Geological
Survey, Revised 1989
6 Wilson, J.F.. "Fluorometnc Procedures for Dye Tracing," Chapter A12, Applications of
Hydraulics. Book 3. United States Geological Survey, Revised 1989.
7 Cobb. ED and J F Bailey. "Measurement of Discharges by Dye-Dilution Methods. "Chapter 14.
Hydraulic Measurement and Computation. Book 1. United States Geological Survey. 1965
8 Kilpatnck, F A , "Simulation of Soluble Waste Transport and Buildup in Surface Waters Using
Dye Tracers". Open File Report 92-457. United States Geological Survey, 1992
EISOPQAM 15 . 27 May 1996
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SECTION 16
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SECTION 16
FIELD MEASURABLE PHYSICAL/CHEMICAL CHARACTERISTICS
PERFORMANCE OBJECTIVES:
To measure physical/chemical characteristics of a sample that are representative of field
conditions as they exist at the time of sample collection
• By selecting the appropriate meter/instmment(s)
• By properly calibrating each instrument(s)
16.1 Introduction
Temperature, specific conductance (conductivity), hydrogen-ion concentration (pH), turbidity,
dissolved oxygen (DO), chlorine, salinity, flash point, and halogen test will be the parameters discussed
in this section The order in which the measurements are made is very important The sections will be
discussed in the most applicable order. References for each section can be found at the end of the section
listed in order with respect to the meter discussed
Numerous meters/instruments are commercially available. Some meters are capable of numerous
measurements which may include pH, temperature, conductivity, DO, salinity, and turbidity, therefore,
individual meters discussed here are not necessarily the only ones available. However, the setup and use
of all instruments should follow a basic format to imply a consistency of use.
Regardless of the brand of meter used, all meters should be properly maintained and operated in
accordance with the manufacturer's instructions and the calibration should be check prior use
EISOPQAM 16 - 1 May 1996
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16.2 Temperature
Temperature is a measure of hotness or coldness on a defined scale.
Three types of thermometers are available-
• Digital (thermo-couple) thermistor
• Glass bulb mercury Tilled
• Bi-metal strip/dial indicator
Calibration
Whichever type of thermometer is used, it should be calibrated semi-annually against a National
Instrumentation Standards and Technology (NIST) certified thermometer.
Note Thermistors should be checked against a mercury bulb thermometer prior to use and
should agree within ± 0.5 °C.
Inspection
All thermometers should be inspected for leaks, cracks, and/or function prior to use
Note A broken glass bulb-mercury filled thermometer can contaminate samples by the release
of mercury vapors
Procedures (Make measurements m-siru when possible)
1 Clean the probe end with de-iomzed water and immerse into sample
2 Swirl the thermometer in the sample
3 Allow the thermometer to equilibrate with the sample.
4 Suspend the thermometer away from the sides and bottom to observe the reading
5 Record the reading m the log book Report temperatures readings to the nearest 0 5 °C
Note Always clean the thermometer prior to storage and/or use.
Degrees Celsius (°C) or Degrees Fahrenheit ("F)
Conversion Formulas
°F = (9/5 °C) + 32 or 8C = 5/9 (°F - 32)
EISOPQAM 16-2 May 1996
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16.3 Specific Conductance (Conductivity)
Conductivity is defined as the quality or power of conducting or transmitting
Meter(s) available"
• Wheatstone bridge meters are typically used for measuring conductivity.
Calibration
The meter should be calibrated in accordance with the manufacturer's instructions A two-point
standard should be used to insure the accuracy of the meter. Conductivity may be affected by temperature.
therefore, temperature should be read first so that appropriate adjustments can be made in accordance to
the manufactures instructions
1 Check and record the temperature of the standard solutions.
2 Rinse the probe with analyte-free water before immersing it in the standards solution
3 Immerse the probe in the first standard solution and record the results
Note Make sure the meter is "ON".
4 Rinse the probe and immerse it into the second standard solution and record results
Note- If the meter is not accurate to within ± 10% of the standards, correct the problem before
proceeding
Procedures
1 Collect the sample and check and record its temperature.
2 Correct the instruments temperature adjustment to the temperature of the sample (if required)
3 Immerse the probe in the sample keeping it away from the sides and bottom of the container
It is important that the enter portion of the probe be wetted by the sample This will be evident
when some of the sample water is seen coming out of the small weep hole
4. Record the results in a log book
5 Rinse probe.
Units
Conductivity units are measured in micromhos per centimeter (^mohs/cm) at 25°C Results should
be reported to the nearest ten (10) units for readings below 1,000 A
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16.4 Hydrogen Ion Concentration (pH)
The pH is defined as the negative logarithm of the effective hydrogen-ion concentration or
hydrogen-ion activity in grams equivalents per liter used in expressing both acidity and alkalinity on a scale
which ranges from 0 to 14 with 7 representing neutrality.
Meter(s) available
• Orion Model 399A
• Orion SA 250 or 230A
• Hydrolab Surveyor II
• YSI 3530. 3500 Water Quality Monitoring System
Calibration (Follow manufacturer's instructions with the following as a minimum)
Note. The pH of the sample to be tested should be estimated either from historical data or
by using a four-color pH indicator paper or equivalent. Using this information, the
two buffering points for calibration can be determined.
1 Remove the meter from storage and allow it to equilibrate to ambient temperature
2 Use a thermometer and determine the temperature of the buffering solutions and record
3 Select either pH 4 and pH 7 or pH 7 and pH 10 solutions as described above
4 Rinse the probe with analyte-free water and immerse it into the first buffer (pH 7) and
record
5 Rinse the probe with analyte-free water and immerse it into the second buffer and record
6 Rinse and siore the probe in a container filled with analyte-free water
Procedures
1 Collect a sample Measure the temperature prior to measuring the pH
Note If the temperature of the sample differs by more than 2°C or approximately 4°F, refer
to the manufactures instructions on how to adjust for temperature variations
Note When the pH meier response is slow, unstable, or non-reproducible, 11 may be
necessary to check the conductivity. If the conductivity is lower than 20 to 30
^mhos/cm then add 1 ml of 1M potassium chloride solution per 100 mis of sample
Recheck the pH and record
2 Immerse the probe in the sample keeping it away form the sides and bottom of the sample
container. Allow ample time for the probe to equilibrate with the sample
3 While suspending the probe away from the sides and bottom of the sample container,
record the pH
4 Rinse the probe with analyte-free water and store it in a analyte-free water filled container
until the next sample is ready
EISOPQAM 16 - 4 May 1996
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Operational check
1 While in use, periodically check the pH by rinsing the probe with analyte-free water and
immersing it into the pH 7 buffer solution.
2 Preform a post calibration at the end of the day and record all findings.
Units
Units of pH are Standard Units (SU) and should be read in one-hundredths (0.01) and recorded
in tenths (0.1)
Note- If the pH measurements are to be used for RCRA regulatory purposes and when the
pH approaches the alkaline end (pH 2 11.0) of the scale, the pH measurements should
be made by a qualified analyst using laboratory quality equipment to control the
sample at 25°C +.1°C.
EISOPQAM 16 - 5 May 1996
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16.5 Turbidity
A nephelometer/turbidimeter is used in comparing the turbidity of liquids by viewing light through
them and determining how much light is eliminated.
Meter(s) available.
• Hach 21 OOP Turbidimeter
Calibration
1 Turn the meter "ON"
2 Rinse the sample cell 3 times with organic free or deiomzed water.
3 Fill the cell to the fill line with organic free or deionized water and then sap the cell
4 Use a non-abrasive lent-free paper or cloth (preferably lens paper) to wipe o-'f excess water and
streaks
5 Open the cover and insert the cell (arrow to the front) into the unit and close the cover
6 Press "READ" and wait for the 'light bulb1 icon to go off. Record the read ig
7 Using the Gelex standards, repeat steps 4, 5, and 6. Record all findings (no j anomalies)
Procedures
1 Collect a specific sample or use a portion of the sample that is collected for ph temperature,
or conductivity analysis, and pour off enough to fill the cell to the fill line (ap[ roximately 3A
full) and replace the cap on the cell
2 Wipe off excess water and any streaks with non-abrasive lint-free paper or cloth lens paper)
3 Place the cell in chamber of the 2100P with the arrow towards the front and close the cover
4 Press "READ" and wait for the 'light bulb' icon to go off. Record the readm:
5 Rinse the cell with organic-free or analyte-free water.
6 For the next sample, repeal Steps 1-5
Operational check
1 Periodically check the turbidity meter by using the standards provided
2 Preform a post calibration at the end of the day and record all findings
Units
EISOPQAM 16 . 6 May
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Turbidity measurements are reported in nephelometnc turbidity units (NTUs)
EISOPQAM 16 - 7 May 1996
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16.6 Salinitv
Salinity is the measure of salts of the alkali metals or of magnesium found in water This
measuremeni is based on the direct proportionality between the magnitude of an induced electric current
and the electrical conductivity of the water in which it is induced.
Meters available
• Beckman Model RS5-3 Portable Salmometer
• Hydrolab Surveyor II
• Scout
• Datasone Salinometer
Calibration/Maintenance.
• Follow the manufactures instructions
• Routinely check the Beckman meter against a resistor matched to the meter
Procedures
• The Beckman has an accuracy of ± 0.3 parts per thousand (ppt) salinity, ± 0.05 °C
temperature, and ± 0.5 millimhos/cm specific conductance.
• The Hydrolab Surveyor II. Scout, and Datasone Salinometer have an accuracy of ± 0.7 ppt
ai 1% full scale conductance ai ±0.1 °C.
• These meters are suited for use in brackish to saline waters having a salinity range of 0 to 40
ppt
Units
Units are reported as salinity m the nearest tenth of a ppt (0 1 ppt)
EISOPQAM 16 - 8
May 1996
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16.7 Dissolved Oxygen (DO)
Meter available
• Membrane/electrode (ME) DO meter
The most common ME meters for determining the DO in water are dependent upon
electrochemical reactions Under steady-state conditions, the current or potential can be
correlated with DO concentrations Interfacial dynamics at the ME/sample interface are a
factor in probe response and a significant degree or interfacial turbulence is necessary For
precision performance, turbulence should be constant
Inspection
• Prior to field use. the membrane of the DO meter should be inspected for air bubbles and/or
holes If air bubbles or holes exist, replace the membrane.
• The membrane should be checked for dryness. If the membrane is dry, replace and soak it in
analyte-free or analyte-free water prior to calibration of the meter.
Calibration
• Air calibrate according to the manufacturer's instructions, either in air saturated water or in
a water saturated air environment
• The ME meter can be checked and/or calibrated against the Winkler method if desired
Procedures
1 When making measurements, be sure that the ME stirring apparatus is working
2 Adjust the temperature and salinity compensators (if equipped)
3 Read the dial to the nearest 0 1 mg/1 and record the measurement
To Collect a Sample
1 When possible, measure the DO m-situ with a field probe; otherwise.
2 Collect the sample in a 300-m! BOD bottle and measure the DO with a laboratory type
probe
Note Special care should be exercised to avoid entramment of atmospheric oxygen or
loss of DO The sample should be collected with a DO Dunker (APHA-type) for
depths less than five feet below water surface (BWS). A Kemmerer type sampler
is recommended for depths greater than five feet BWS.
3 If an APHA-type DO Dunker is not available and a shallow depth sample is needed, a
bucket may be used to collect a sample of water A siphon tube should be coiled into the
bucket such that the fill end is nearest the bottom Using a 300-ml BOD bottle, allow the
siphoning sample to fill and overflow the bottle for a minimum of three volumes
EISOPQAM 16 - 9 May 1996
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4 If a Kemmerer sampler is used, the BOD sample bonle should be filled to overflowing b>
inserting the outlet tube of the sampler to the bottom of the bottle The tube should be
withdrawn slowly as the bottle is allowed to overflow three times its volume. Care must
be exercised to prevent turbulence or the formation of bubbles when filling the bottle
Duplicate analyses should agree within ± 0.1 mg/1.
Units
Units should be reported in mg/1
Limitations
• Dissolved inorganic salts are a factor with the performance of DO probes
Note The presence of inorganic salts must be determined.
• Reactive gases which pass through the ME probes may interfere with the DO analysis For
example, chlorine will depolarize the cathode and cause a high probe output Long-term
exposures to chlorine will coat the anode with the chloride of the anode metal and eventually
desensitize the probe Hydrogen sulfide will interfere with the ME probes if the applied
potential is greater than the half-wave potential of the sulfide ion.
• Dissolved oxygen ME probes are temperature sensitive, and temperature compensation is
normally provided by the manufacturer (see manufacturers instructions).
EISOPQAM 16 - 10 May 1996
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16.8 Total Residual Chlorine
Meier(s) available
• Pocket colorimeter
• Hach DR-100 Colonmetnc (DPD) kit -- n,n-diethyl-p-phenylenediamine (DPD) may be used
for natural waters or waters treated with chlorine.
Note The Hach reagents and colorimeter or spectrophotometer are accepted by the US-EPA
for NPDES monitoring if used in accordance with approved procedures The pre-
printed calibration scales provided by the manufacturer are based on factors developed
under ideal conditions and are only acceptable if verified. The calibration scale must
be initially verified using multiple standards and a blank. The calibration scale or
curve must be verified at least daily using a blank and one high and one low standard
representative of the linear working range These standard checks must agree within
± 10% of the original scale or a new curve must be prepared Verification data
should be recorded and maintained on file (See Standard Methods)
Use either 1-cm or 2 5-cm cells.
Inspection
• Each meter should be visually inspected before and after each use Report any discrepancies
to the FEC.
• Check the battery strength
• Insure that the reagents are fresh before field trips
Calibration
• The calibration scales must be calibrated onsite with a minimum of three points a blank and
two known standards that bracket the expected sample concentrations
Note If the DPD kit is used, the method must adhere to the requirements set forth in
Standard Methods
Reagents/Standards
• DPD total chlorine powder packets
Note The packets deteriorate in the presence of moisture The packets should be discarded
if they have caked or have turned brown
The DPD oxalate is very toxic DO NOT handle with unprotected hands or ingest
If accidentally spilled on skin or ingested, seek medical attention immediately.
• Chlorine demand-free water (See Standard Methods, Method 4500 Cl for directions in
preparing the ASTM Standard Dl 193 "Consumption of Potassium Permanganate")
EISOPQAM 16-11 May 1996
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Potassium permanganate stock -- Prepare a stock solution containing 891 mgs/1000 mis
Potassium permanganate working stock 10 ppm -- Prepare working stock solution containing
10 mg/1 KMnO4 by diluting 10 mis of D.8.5.4 stock solution to 1 liter
Note The stock should be stable for approximately 5 days if kept cool and away from
light.
Potassium permanganate calibration standards - Prepare calibration standards from the
working stock solution and/or KMnO4 calibration standard solutions for each day of use
Note. KMnO, standards will fade rapidly (within 15 minutes) if chlorine demand-free
water is not used
Calibration Standard (mg/l)
005
0 10
0.5
1.0
2.0
mis of Working Stock/ 100 mis
10 Oof 0.5 mg/1 std
10.0 of 1.0 mg/1
5.0 of 10 mg/1
10.0 of 10 mg/1
20.0 of 10 mg/1
Procedures for total chlorine concentrations ranging between 0 - 2 ug/1
1 Fill a clean 2 5-cm cell to the 10-ml mark with a sample.
Note: The sample should have a pH between 6 and 7 SU. If necessary, adjust with 1N
sulfunc acid or IN sodium hydroxide
2 Open a DPD total chlorine powder packet and add the contents to the sample cell
3 Replace the cap on the cell and swirl to mix
Note It is not necessary for all of the panicles to dissolve to obtain an accurate reading
The pH of the sample containing the DPD buffer packet must be between 6 2 and
6.5 SU.
4 Allow at least 3 minutes but not more than 6 minutes before moving to the next step (see
and follow manufactures instructions for reaction times).
5 Open the light shield, turn the right set knob fully clockwise, and place the 1-cm cell in
the left set position of the sample well holder. Press the cell down firmly to seat it in the
holder.
6. Hold the button down While doing this, adjust the left set knob to align the meter needle
with the arrow at the extreme left of the scale.
EISOPQAM
16- 12
May 1996
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7 Remove the cell from the holder.
8. Fill a clean 2 5-cm sample cell with the sample. Cap the cell and place it into the cell
holder Press it firmly to seat and close the light shield.
9 Set the colorimeter by holding the "ON" button down while adjusting the right set knob
to zero Open the light shield and remove the sample cell
10 Fill a clean 1-cm sample cell with the solution from step 2, cap the cell, and place into the
cell holder.
11 Press the "ON" button down and hold it until the meter stabilizes.
12 Read and record the mg/l of total chlorine from the upper (2.5-cm) scale.
Procedures for total chlorine concentrations ranging between 0 - 3.5 mg/1
1 - 6 Same steps as previously listed.
7 Rotate the cell to the right position
8 Fill a clean 1 -cm sample cell with the sample, cap the cell, and place it into the cell holder
9 Set the colorimeter by holding the "ON" button down while adjusting the right set knob
to zero. Open the light shield and remove the sample cell
10. Fill a clean 1-cm sample cell with the solution from step 2, cap the cell, and place it into
the cell holder
11 Press the "ON" button down and hold it until the meter stabilizes.
12 Read and record the mg/l of total chlorine from the upper (1-cm) scale
Verification
• Duplicate chlorine residual analyses should agree within ± 0.01 mg/l
Units
• mg/l total chlorine
Limitations
• Do not use with or in the presence of any oxidizing agents, e.g., oxidized manganese interferes
with the DPD reagent (1 ng/1 MnO, - ^g/1 CI2)
EISOPQAM 16-13 May 1996
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16.9 Flash Point
The following test method is to determine if a volatile material's flash point is within established
limits
Apparatus
• ERDCO Rapid Tester Model RT-1, Flash Point Analyzer
Calibration
• The repeatability and reproducibihty for this instrument are in accordance with the respective
standards:
• p-xylene 78.0 ± 1.0°F
• n-butanol 97.9 ± 1.7°F
• n-undecane 145 4 ± 2.0°F
• n-hexadecane 270.5 ± 2.0°F
Operational Procedures.
1 Plug in the ERDCO and turn it on
2 Switch the rocker switch adjacent to the display to Fahrenheit or Celsius display.
3 Press the red temperature preset rocker switch and rotate the red temperature preset knob until
the desired temperature appears in the display window (140°F for determining igmtability
characteristics). Release the rocker switch and the actual instrument temperature will appear
in the display window The RED light next to the knob should come on indicating the heater
is "ON"
Note The preset knob for test temperature may have to be reset as the test temperature is
approached
4 If a glass bulb thermometer is used, coat the bulb with a heat transfer compound and insert it
into the well in the left side of the test oven. Carefully secure the top of the thermometer in
the channel
5 Open the control valve on the butane cylinder approximately 5 turns and install Close the
control valve and place the cylinder into the instrument's receptacle. Hook the hose to the
valve
6 Open the control valve approximately one turn and light the pilot light located over the square
hole in shutter lid Adjust the pilot light for the minimum flame that will light test the jet.
Adjust the test jet for the flame to 4 mm width using the pinch valve knob
EISOPQAM 16 . 14 May 1996
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Note Immediately above the shutter is a 4 mm referenced milled lid.
7 Make sure that the shutter lid is latched (Closed). Inject 2 cc of the sample into the port
between the shutter and the latch handle Press the 1-minute timer rocker switch until the light
goes on, then return the switch to center.
8 When the timer sounds, slide the shutter back slowly (taking about 2 seconds to do this) The
material under test will either flash or not flash.
Note If a halo develops around the flame, this does not constitute a flash
9 Lift the lid Clean out any material which was being tested with Chem-wipes Also clean the
injection port with a pipe cleaner.
Shut Down Procedures
1 Close the control valve on the butane cylinder.
2 Disconnect the hose
3 Open the control valve on the butane cylinder approximately 5 turns.
4 Turn the instrument off
5 IMPORTANT - Clean the instrument (See step 9 above) Allow ample time for the instrument
to cool down before storing
EISOPQAM 16-15 May 1996
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16.10 Halogen Test
This method is used to qualitatively screen wastes for the presence of halogenated compounds
Tesi using copper wire and flame
Equipment-
• Propane fuel cylinder with a torch
• Igniter source (matches, flint/bar striker, etc.)
• Stainless steel rod approximately 1 foot long and VB to '/z inch in diameter
Note. The smaller diameter rods cool down more quickly.
• Thermally resistant handle or thermally resistant gloves
• 16 or 18 gauge copper wire
• Wire cutters
Procedure
1 Wrap approximately 4 feet of copper wire around the tip of the rod
2 Clean the wire and rod tip using the flame of the propane torch.
Note When a blue flame with small yellow-orange streaks appears, the wire and rod are
clean Allow the copper wire to become "red" hot during the cleaning process
(this takes from Vi to 1 minute)
3 Allow the rod and wire to cool for a minimum of 15 minutes.
Note- The wire and rod can be immersed in water to speed up the cool down time This
will not bias the results Allow the water to evaporate completely and the rod tip
should be cool to the touch before using it in the test
CAUTION!
DO NOT IMMERSE A HOT ROD INTO A POTENTIALLY FLAMMABLE MATERIAL
4 Immerse the cooled wire and rod up into the test material for approximately 10 seconds
5 Remove the wetted wire/tip from the test material and allow the excess material to drip
back into the container
Note. Highly viscous material which sticks to the tip may produce a large flame
6 Place wetted wire into the flame and observe the color produced.
EISOPQAM 16 - 16 May 1996
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Note A bright green flame indicates the presence of halogenated material
E1SOPQAM 16 - 17 May 1996
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16.11 References
Temperature
1 Standard Methods for the Examination of Water and Wastewater. 18th Edition p 2-59. Method
25508(1992)
2 Methods for Chemical Analyses of Water and Wastes US-EPA, 170.1 (1983)
Specific Conductance (Conductivity)
3 Standard Methods for the Examination of Water and Wastewater. 18th Edition, p 2-42 Method
25108(1992).
4 Annual Book of ASTM Standard*, Vnl 11.1, "Water," Standard Dl 125-91 A, P 202
5 Methods for Chemical Analysis of Water and Wastes. US-EPA, 120.1 (1983).
6 Instruction Manual. SoluBridge* RB-5/RB-6. Beckman Instruments, Inc., Rev. January 1982
7 Surveyor II Operating Manual Hydrolab Corporation. Rev. A February 1985
8 YS1 Model 3560 Water Quality Monitoring System Insimcnnns. July, 1988
H> drogen Ion Concentration (pH)
9 Standard Methods for the Examination of Wastewater. 16th Edition, p. 429, Method 423 (1985)
10 Instruction Manual for Models 399 A/F, 399 AIL Analog nH Meter, and SA 250 and 230A, Orion
Research Incorporated
11
Instruction Manual for Surveyor II. Hydrolab Corporation
12 Instruction Manual for YSI Water Quality Monitoring Sysiem for the Model 3530 pH Electrode
Assembly
'3 Annual Book of ASTM Standards. Part 31, "Water". Standard D 1293-78(8).
'4 Methods for Chemical Analysis of Water and Wastes. US-EPA ISO l
15 Procedure No 501. pH Measurement in Low Ionic Strength Solutions Orion Application
Information. Orion Research Incorporated.
16 Federal Register. Vol. 60. No 64. Tuesday, April 4, 1995 - Rules and Regulations, 17001-17003
EISOPQAM 16 - 18 May 1996
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Turbidity
17 Operating procedures for the Hach 2100P Turbidimeter
Dissolved Oxygen
18 Standard Methods for the Examination of Water and Wastewater. 18th Edition, p 4-100. Method
4500-OC(1992)
19 Annual Book of ASTM Standards. Part 31, "Water," Standard D888-92(A)
20 Methods for Chemical Analysis of Water and Wastes. US-EPA, 360 1 (1983)
21 Methods for Chemical Analysis of Water and Wastes. US-EPA, 360 2 (1983)
22 Instruction Manual YSI Model 57. Dissolved Oxygen Meter. Science Division. Yellow Sprincs
Instrument Company.
Chlorine - (DPT Colorimetric)
23 Annual Book of ASTM Standards. "Water." Standard D 1253-86(92)
2-4 Methods for Chemical Analysis of Water and Wastes. US-EPA. 330 1 (1983)
25 Methods for Chemical Analysis of Water and Wastes. US-EPA, 330 5 (1983)
26 Standard Methods for the Examination of Water and Wastewater. 18th Edition. Method 4500-CL
D(1992)
27 Standard Methods for the Examination of Water and Wastewater. 18th Edition, p 4-100, Method
4500-CLG( 1992)
28 Instruction Manual PR 100 Colorimeter Model 41100-02. DPP Method for Chlorine Hach
Company. June 1983
Salinity
29 Standard Methods for the Examination of Water and Wastewaier. 18th Edition, p 2-47 Method
25208(1992).
30 Instruction Manual. RS5-3 Portable Salmometer. Beckman Instruments, Inc.. Revised March 1973
Flash Point
31 Rapid Tester Model RT-1 Technical Manual. Operations and Service, November 1, 1989
EISOPQAM 16 - 19 May 1996
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SECTION IT
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SECTION 17
AIR MONITORING SAFETY EQUIPMENT
CALIBRATION PROCEDURES
17.1 Introduction
This section gives specific procedures to be followed when calibrating air moniiorinc
instrumentation Calibrations defined in these procedures will result in instrument response accuracy
within the capabilities of the instruments The following practices shall be followed with calibration gases
• Calibrations should demonstrate proper operation of the monitor and insure that results give
an acceptably accurate indication of conditions upon which to base safety decisions and
actions
• Calibration gases shall be certified by their supplier 10 be of a specified and known
concentration
• Concentrations of calibration gases shall be within a relevant range of response for the air
monitors, but will not exceed any flammability or toxic exposure limits
• Gas cylinders will not be sent to the field if they contain less than one-fifth of their full
capacirj Cylinders below the required volume will be utilized in the warehouse for equipment
check-oui and maintenance
Calibration mixtures and approximate concentrations for specific air monitors will be as follows
MONITOR
Combustible Gas
Flame lomzation
Phoio-lomzation Detector
CALIBRATION GASES
GAS MIXTURE
Pentane in Air
Methane in Air
Toluene in Air
CONCENTRATION
075%
75 ppm
lOOppm
Calibrauon Equipment
All calibrations will consist of introducing a gas of known concentration into the monitor at
atmospheric pressure Under no circumstances will n be acceptable to attempt calibration when the
monitor is measuring gas concentrations below or above atmospheric pressure
EISOPQAM 17.
May 19%
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To insure a stable pressure of the calibration gas. a calibration manifold system will be used The
manifold will consist of a "T" fitting, a Teflon* bag. Teflon* tubing, and finings The Teflon* bag iv
omitted for calibration of the OVA
The calibration gas cylinder will be connected to the "T" fining with Teflon* tubing so that the gas
will flow directly through the lop of the "T" into a Teflon* bag
The "T fitting and cubing will be purged with calibration gas prior to connection of the Teflon*
bag The bouom or side port of the "T" will be connected with Teflon* tubing to a stainless steel quick
disconnect Once the Teflon* bag has been filled with gas, the gas flow will be turned off The monitor's
probe will be connected to the manifold via the quick disconnect and allowed to sample the contents of the
Teflon" bag
Calibration Frequency
li is required that the monitors be calibrated each time they are turned on More frequent
calibrations are encouraged if the field investigators determine that field conditions and hazards are
warranted Frequent checking of monitor response or proper setting and operation of alarms is
encouraged
Prior to turning off the monitor, a post calibration check shall be performed This check will
follow the same procedures as the initial calibration except that no adjustments will be made to the monitor
Instead, the response will simply be logged in the field book
Documentation
Calibrations should be documented in the field log book The entry needs to include the following
information
CALIBRATION DOCUMENTATION
Monitor's Identification Number
Date of Calibration
Time of Calibration
Bjiien Check Response
Alarm Response
Instrumem Response
Calibration Gas Concentration
Fuel Level (FID)
Operator's Initials
EISOPQAM 17 - 2 May 19%
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17.2 MSA Model 260 Combustible Gas and Oxygen Alarm
Introduction
The MSA Model 260 Combustible Gas and Oxygen Alarm is a hand-carried, battery operated
instrument
• It is used to sample atmospheres for combustible gases or vapors and oxygen content and w^rn
the user when pre-determmed concentrations of either are reached
• The monitor will only detect combustible gases and vapors in air It will not indicate the
presence of combustible airborne mists or dusts such as lubricating oils, coal dust, or gram
dust
- THE LACK OF A RESPONSE ON THIS METER DOES NOT GUARANTEE THAT
THE ENVIRONMENT IS SAFE.
Operational Checks
1 Connect the probe line to the monitor's water drop-out bottle Check the probe fining and the
water drop-out bottle fitting for tightness
2 Place the monitor's "ON-OFF" switch in the "HORN OFF" position
• Note thai the monitor s "£ OXYGEN" and "% LEL" meters respond upscale, and then
stabilize
• Note that the oxygen alarm and LEL alarm lights are illuminated, the green flow indicator
is flashing, and the "FLOW indicator float is vibrating audibly.
3 Press the "RESET" button and observe that both "ALARM" lights go out
4 Press the "CHECK" burton and record the battery reading from the "% LEL" meter
5 Set the "5 OXYGEN1 meter to read 20 8% using the "CALIBRATE O:" knob Set the "%
LEL' meter to read zero using the "ZERO LEL" knob
6 Place the monitor's function switch to the "ON" position
7 Leak check the monitor b\ placing your thumb tightly over the probe line inlet Observe that
the monitor's pump stops Observe also that when the "% OXYGEN" meter falls to
approximately 19£. the "ALARM" light illuminates and the alarm horn sounds
8 Remove your thumb from probe inlet line When "% OXYGEN" meter returns to 20.8%.
press "RESET" button
9 Rotate the "ZERO LEL" knob clockwise until the "ALARM" light illuminates and the alarm
horn sounds This should occur at about 25% of LEL Return the LEL meter to a reading
of zero and reset the alarms
EISOPQAM ,7-3 May,996
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Calibration
1 Assemble a calibration manifold as described in Section 17.1 Upon introduction of the
calibration gas to the monitor, the LEL response should be approximately 50% Record the
response.
2 Disconnect the monitor from the calibration manifold and reset the alarms
3 Insure thai the function switch is in the "ON" position and thai the green flow indicator iv
steadily illuminated
4 Attach the probe 10 the probe line
EISOiQAM ,7.4 May 19%
-------
17.3 Photovac Microtip Photoionization Detector
Note: Some microtips are NOT iastrinsciaUy safe
Introduction
The Photovac Microtip is a microprocessor controlled photoiomzation detector The mstrumem
normally operates with a 10 6 eV lamp, however 9.5 and 11 7 eV lamps are available as options The
detector is capable of measuring concentrations down to about 1 ppm sensitivity for certain compounds
It is important to realize that this sensitivity is not achievable for all compounds Some materials
will result in a very low response on the PID in relation to their actual concentrations, while others will
noi respond at all to the detector's lomzation energy. It can not be used to identify unknown substances.
it can only quantify them Winds and high humidity will affect measurement readings Foggy or high
humidity conditions can cause condensation on the lamp, thus affecting measurements
As a general rule, the PID should not be used to monitor for low molecular weight hydrocarbon
compounds whose structures contain only single bonds (methane, ethane, pentane, hexane, heptane, carbon
tetrachlonde. and hydrogen sulfide) The PID should be used to detect- aromatics such as benzene.
loluene. and styrene. aliphatic amines such as diethylamme; and chlorinated unsaturated compounds such
as vinyl chloride and tnchloroethylene
• THE LACK OF A RESPONSE ON THIS METER DOES NOT GUARANTEE THAT
THE ENVIRONMENT IS SAFE.
• THE MICROTIP MODEL MP100 IS NOT INTRINSICALLY SAFE
• DO NOT USE A NOMNTRINSICALLY SAFE MICROTIP IN CONFINED SPACES
LTsLESS CLEARED WITH AN EXPLOSIMETER
Operanonal Information
Turn the instrument on b\ pressing the back of the power switch The pump will start and the
message "Warming up now, please wait" will be displayed Within three minutes the following
intormanon will appear on the display
Current Detected
Instrument Status Concentration
Ready 2000 ppm
008 10.15 Feb 15
Event Number Time Date
The Microtip then operates automatical!) The user reads the concentration directly from the
display The display updates itself each half second
OSOPQAM 17 . 5 May 1996
-------
The minimum, maximum, and average concentrations measured in each 15-second period JT-J
automatically recorded in memory The memory holds the last 12 hours of data The concentration datd
can be retrieved from memory1 on the instrument's display or sent to a printer or computer in either tabular
or a graphical format Data are recorded by date, time, and by a user-entered event number Data arc
played back by the user specifying a start and a stop event number
The keypad is used to set up and calibrate the Microtip. and it allows the user to manipulate the
concentrations measured and recorded by the instrument in various ways The Microtip has 16 labelled
keys for direct numeric entry and for using the instrument's functions All information entered from the
keypad and stored in data logging memory is retained when the instrument is switched off The clock and
calendar continue to operate and do not need to be reset the next time the instrument is used If there are
no options to the function then the key acts immediately If there are options, then the display will indicate
these The currently selected option is displayed on the lower line. The user is prompted to display the
other options by pressing the up arrow or down arrow keys. Pressing ENTER confirms that the displayed
option is correct If the function requires numeric input then the current value is displayed on the lower
line The user can change it on the display by pressing the numeric keys. Pressing ENTER confirms that
the displayed value is correct Some functions have multiple steps for options and/or numeric inputs
These are arranged so that the most frequently changed inputs are displayed first. Once the desired
changes have been made the user can bypass the rest of the steps by pressing EXIT.
Following is a list of the keys and a description of their functions:
TUTOR
To assist the user in learning the ke\ functions, the instrument has a built-in tutorial session which
displays a two-line description of the function of each key Pressing the TUTOR ke\ begins a
tutorial session and pressing the EXIT key twice ends the session While in the tutorial session key
presses have no effect on the instrument s operation
If a numerical display is shown, pressing DISPLAY will change it to a bar graph If the bar graph
is shown, pressing DISPLAY changes it to a numerical display. The bar graph range ts selected
with the SETUP ke\
Backlighting can be of one of two micnsines The brighter lighting consumes more power and is
recommended for use onl> in \en dark locations Pressing the LIGHT key switches the backlight
on to high intensity, pressing n again decreases the intensity, and pressing it once more turns the
backlighting off Backlighting is noi available on intrinsically safe instruments
EISOPQAM 17-6 May 1996
-------
Pressing the BATT key displays the current battery level The battery voltage will be shown fur
15 seconds and then the display reverts to normal The normal operating voltage range is 9 to 16
volts When LoBat is displayed there is approximately 10 minutes of operation left The batier>
pack must be replaced by a fully charged pack and the discharged pack should be recharged
If operation is continued with a low battery pack, another message will appear indicating thai the
batteries are critically low The Microtip will then turn off the detector lamp, the pump, and the
backlighting (if activated) This reduces deep discharging of the banery pack and possible memor>
loss
MAX
When pressed, the maximum concentration, the event during which it was encountered, the time
and the date of the occurrence will be displayed This is shown for 15 seconds and then the display
reverts to normal Pressing MAX and then CLEAR will reset the Max register "Max Cleared"
will be displayed with the current date and time. After 15 seconds the display reverts to normal
Recording of real time data is not interrupted when the MAX key is pressed or when the Max
register is cleared
CLEAR
CLEAR erases the lasi numerical entr> If a number is entered in error press CLEAR to erase the
entr> and re-enter the correct number CLEAR used m conjunction with the MAX ke> resets the
Max recister
EVENT
Each press of the EVENT ke> advances the Event number by one unit on the display Press
EVENT to help identif> a particular sample or sampling location in memory After Event 255.
the E\ em counter resets to zero Each lime the instrument is turned on the Event number is
automatically advanced b> one unii Recorded data are played and printed by specifying a start
and stop Event number
The instrument will record continuous!} for a period of 12 hours After 12 hours it begins to
overwrite existing data one event at a time If a printed copy of the data is required, it should be
downloaded at least once every 12 hours of operation
EISOPQAM 17-7
May 1996
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The EXIT key terminates all functions except DISPLAY, LIGHT, and EVENT When EXIT i-
pressed the display reverts 10 normal Most functions exit automatically if no key is pressed for
IS seconds When EXIT is pressed during printing or graphing, the instrument stops sending
information to the printer or computer The printer will continue to print until its buffer is ernpn
The SETUP key allows the insirument to be set up for a specific application The current dale and
time are also set with the SETUP key Press SETUP and step through the options Press ENTER
to accept the displayed data or enter a numerical value using the keypad and then press ENTER
If no values are entered, the display reverts to normal
To set up the instrument
1 Press SETUP.
2 The first step sets the full scale range for the bar graph display, the graph output, the audio
output, and the 1 volt analog ourpui Use the up and down arrow keys to select the 20.200 or
2.000 parts per million (ppm) ranee
3 Nexi the Cal memory is selected The instrument has five Cal Memories for regular operation
and one for High 5ensinvir\ operation Only one Cal memory can be used at a time Select
Cal Memory 1 with the up and down arrow keys and press ENTER
4 Next, enter the correct \alue* for the cunem time Press ENTER after each value
5 Enier the numencal values for the da\. month, and year Again press ENTER after each
selection
The instrumem is now sei for operation
To connect the headset, remove the dustcover from the I/O connector and plug in the headset If
a headset is being used, pres<. AUDIO and use the arrow keys to select one of three options for
audio output and press ENTER The audio output can be turned off altogether. It can be set so
there is audio output during an alarm condition only The last option is a continuous audio signal
with trie tone being proportional to the detected concentration
EJSOPQAM 17 - 8 May 1996
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ALARM
The ALARM key displays ihe current alarm level and allows a new alarm level to be eniered
1 Press ALARM.
2 The current alarm is displayed If the value is correct (5 ppm) wait for the displas to revert
to normal in 15 seconds or press EXIT.
3 If a new value is to be set, enter the value, and press ENTER
When an alarm condition is detected the instrument status changes to "Alarm" and remains on until
the alarm condition has passed
PLAY
The PLAY key plays back previously recorded data
1 Press PLAY Two options are available Pressing ENTER begins playback where u was last
stopped Press the SETUP (•) key to set the playback options
2 Select the start Event If the selected Event is not available, the instrument begins at the
closesi higher Event An Event may not be available if the EVENT key was pressed more
than once in 15 seconds, or if the selected Event has been overwritten in the memory by more
recent information
3 Next select which value is to be displayed, either the Minimum, the Averace. or the
Maximum, with the arrow keys and press ENTER
4 The data can be played back m either numerical or graphical display by pressmc the DISPLAY
ke\
When the instrument is playing back recorded data it is also measuring and recording real time
concentrations even thouch the instrument status is "Play" If. during playback, an instrument
status with a prioni\ higher than that of "Play" is encountered in real time operation u will be
displayed, but the pla\ back will continue The playback speed and direction can be selected using
the arrow keys The speed can be increased or decreased and the information can be viewed in
the opposite direction as well A forv. ard arrow {>) appears in the display if data are being played
forward or a backward arrow « ) if the data are being played in reverse Press ENTER to freeze
the display at an> time and use the arrow keys to resume playback. Press EXIT to return to the
normal display The PLAY function provides a speed search to find the desired start and stop
Event numbers for printing or graphing
EISOPQAM |7.9
May 1996
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CAL |
The instrument must be calibrated against a dynamic standard in order to display concentration*.
in units equivalent to ppm Clean outdoor air is suitable as Zero Gas Assemble a calibration
manifold as described in Section 17.1 using toluene as the calibration gas
1 Press SETUP and check all display information Select a Cal Memory (usually # 1 > w, uh UK
arrow keys and press ENTER Press EXIT to leave the Setup
2 Press BATT and record battery voltage.
3 Press ALARM and set the alarm level to 5.0 and then press enter.
4 Press CAL and expose the instrument to Zero Gas Press ENTER and the zero point is set
5 The instrument then asks for the Span Gas concentration Enter the known concentration from
the span gas cylinder and press ENTER.
6 Connect the span gas fitting to the sample inlet.
7 Press ENTER and the sensitivity is set
8 When the display reverts to normal, the instrument is calibrated and ready for use
When the instrument is turned on. it will automatically calibrate itself to the data stored in the CAL
Memor\ (usualK #1) selected in Step 1 This instrument calibration is acceptable provided
• The site is not a level C or B sue. and that no "hits" have been detected or are expected to be
detected
• The instrument responds to some lomzable material introduced to the sample inlet (i e . a felt
tip pen check)
EISOPQAM I7.,0
May 19%
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17.4 Toxic Vapor Analyzer (TVA 1000A)
Introduction
The Toxic Vapor Analyzer (TVA IOOOA) is a portable inorganic/organic vapor monitor This
analyzer uses both a flame lomzauon detector (FID) and a photoionizanon detector (PID) to sample and
measure concentrations of gases
Hydrogen Tank for the FID
When the TVA IOOOA leaves the Field Equipment Center (FEC), the hydrogen tank will be full
and the battery will be charged
If the hydrogen tank (used to run the FID) has to be refilled during the field exercise remember
that the threads on the hydrogen tank are left-handed Follow the same procedures for refilling
this hydrogen tank as you would for refilling the hydrogen (used to run the FID) on the OVA
Note that you must always screw the hydrogen tank into the unit when taking the TVA ou: of the
carrying box The TVA will not fit back in the box without taking the hydrogen tank out of the
unit Extra hydrogen tanks are available
Operating Procedures
1 After you have recharged the battery and filled the hydrogen tank, install it in the instrument
(left handed ihread. turn counter-clockwise until resistance is felt)
2 Connect the sample probe, and turn the unn on
3 If you want to use the FID turn on the red HYDROGEN ON/OFF valve
J The TVA-IOOOA is user fnendlymenu driven To operate the TVA IOOOA. follow the
procedures listed in the next two tables The instrument takes a few minute to warm up
EISOPQAM 17.11 May 1996
-------
To displa\ a measuremeni on a PID unit, use the procedure below
TV A 1000A - PID DISPLAY
ACTION
Press On
Wan 15 Seconds
Press Conirol
Press 1
Press 1
DISPLAY
Battery OK
NV RAM OK
Date/Time OK
Self Test OK
Main Menu
l=Run 2 = Setup 3 = Info
4 = PC Link/Memorv
Control Menu
1 =Tum Pump On
2 = Turn PID On
Mam Menu
l=Run 2= Setup 3 = Info
4 = PC Link/Memory
PID 00255
DESCRIPTION
The TVA 1000A performs selftesi diagnostics
for approximately IS seconds.
The mam menu is displayed When starling
the instrument for survey, be sure to turn the
pump on before selecting the run mode
The mam menu prompts you to make a
selection
The mam menu is displayed again, but this
time the pump is on Since the pump is on.
you can make a measurement Note the
prompt selections
The TVA 1000 A presents the measurement
information Refer to the setup procedure in
the Display Menus
To power down the instrument, press and hold trie OFF button
EISOPQAM
17- 12
May 1996
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To displax a measurement on a FID-only or FID/PID unit, execute the following procedure
TVA 1000A - FID DISPLAY
ACTION
DISPLAY
DESCRIPTION
Press On
Battery OK
NV RAM OK
Date/Time OK
Self Test OK
The TVA 1000A performs selftesi diagnostics
for approximately 15 seconds
\\ait 15 Seconds
Mam Menu
l=Run 2 = Setup 3 = Info
4 = PC Lmk/Memor\
The mam menu is displayed When starting
the instrument for survey, turn on the pump
and ignite the FID before selecting 1 for run
Press Conirol
Control Menu
1 =Turn Pump On
2=TurnPIDOn
The main menu prompts you to make a
selection. To turn the pump on. press 1
NOTE Choice "3" available only on FID/PID
unit
Press 1
Mam Menu
1= Run 2 = Setup 3 = Info
4 = PC Lmk/Memon
The mam menu is displayed again, but this
time the pump is on With the pump on, press
the CONTROL key again to ignite the FID
Press CONTROL
Conirol Menu
1 =Turn pump on
2 = Ignite
3= Turn PID on
Now that the pump is on. select 2 to ignite the
FID Before pressing the 2 key, turn on the
gas valve and let the instrument run for at least
30 seconds
Press 2
Mam Menu
I =Run
2 = Setup
3 = Info
4 = PCLmk/Memor\
The mam menu is displayed again This time
the pump is on and the FID is ignited To
make a measurement, select 1 for RUN
Press I
PID 0025S
FID 00 259:
The TVA 1000A presents the measurements
information Refer to the setup procedure in
the Display Menus
To power down this instrument, press and hold the OFF key You must also shut the gas valve to
avoid depleting the tank suppU
EISOPQAM
17- 13
May 1996
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Calibration
To provide the specified accuracj. the instrument must be calibrated at the beginning of each
workda\
The four steps involved in calibrating the TVA 1000A are.
1 Calibrate a Zero pomi using either a zero gas or clean ambient air. The Zero and
BACKGROUND terms are used only for reference. Only one ZERO value is stored
Menu item 1 = Zero refers 10 a zero gas being used
Menu item 2 = Background refers to clean ambient air used for the zero
2 Calibrate a reference point, using a known span gas.
Menu item 3 = Span
3 Define to the instrument the actual concentration of gas provided in Step 2
Menu item 4 = Gas Concentration
4 Define the response sensnivii). using a response factor
Menu item 5 = Response Factor
Calibrate the TVA 1000A by taking an actual gas sample for ZERO and another actual gas sample
for SPAN The ZERO sample may come from either clean ambient air (display reads Backgndl or from
a calibration zero gas tank (display reads Zero) The SPAN sample must be a known concentration of
calibration gas Enier the concentration of span gas (display reads GasConc) and then assign a sensmvm
level for the gas to be measured (displax reads Response Factor).
Performing an accurate calibranon requires the necessary calibration gas source, a clean zero
source, and execution of the following procedures
Note Prior 10 performing calibration, the instrument must be ON and warmed up for
approximately 30 mmuies The pump must also be ON and, if the instrument is equipped
with a FID. the flame must he ignited throughout the warmup period
E1SOPQAM 17-14 May 1996
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•\ccessmp the Calibration Menu
1 From the MAIN menu display, press 2 = Setup
2 Seleci 5 = Other Settings, then 4 = User Options, and then select 3 = Cal Mode
The calibration modes are
AUTO Instrument analyzes the gas sample until values stabilize arid then stores the final
value There is no measurement display during this process The factor)' setting
is AUTO
MANUAL User monitors gas sample measurements (in counts) and presses ENTER to store
the value
The following steps assume the AUTO calibration mode
3 From the SETUP menu display, press 1 = Calibration and follow the procedures for the
appropriate calibration
CALIBRATION MENU (For FID only, PID only. PID/FID)
l=Zero 2-Background
3 = Span 4=GasConc
5 = Response
Zero or Background Zero Reference Poini
1 From the CALIBRATION menu displav. press J = Zero if zero is to be used for calibrating
zero Press 2 = Background if clean ambient air is to be used for zero (Select one or the
other)
Note If you have selected the MANUAL calibration option, the display will show the
unsealed detecior output values of the zero gas (expressed in counts) as of the last
calibration If you select the AUTO option, the coum is not displayed
If the instrumem is a dual detecior rvpe (P1D and FID), you can zero the PID and FID
separated . bovh iogevh«. o: ont in ICTO gas and one in clean ambient air To do so. follow
the same procedure However. K n suggested that you zero both detectors together
If \ou press 1 = Zero, the diipla> uill show
FID-onh PID-onlv PID/FID
Zero Cal Zero Cal Zero cal l=Both
Enter = Stan Enter = Stan 2 = PID 3= FID
EISOPQAM 17 - 15 May 1996
-------
2 To perform the actual ZERO procedure for
FID-only or PID-only or PID/FID
»ress ENTER Press ENTER Press 1. 2. or 3
Apply Zero Gas Apply Zero Gas Apply Zero Gas
FID PID PID/FID
Ei:ter = Stari Enter = Start Enter = Start
E>. i = Cancel Exit=Cancel Exit=Cancel
3 Apj ly the zero gas to ihe probe at ambient pressure (using a clean and labeled gas sampling
bagi and then press ENTER
Calib-atmg Calibrating... Calibrating
FID PID FID/PID
Zero Cias Zero Gas Zero Gas
Exii = Cancel Exit = Cancel Exit=Cancel
The mst-ument analyzes the zero sample
Calibrating . Calibrating.. Calibrating
FID PID FID/PID
ACCEPTEl ACCEPTED ACCEPTED
The ACCEPTED message appears for a brief time and is then replaced by the normal
CALIBRATION menu
When the ACC EPTED message disappears and the CALIBRATION menu appears, the ZERO
reference value is in non-volatile memory' until the next calibration is performed The date and
lime of this calnration are sieved and accessed through the INFO menu
Noie For opti num accuracy, re-zero the FID every time the hydrogen supply valve is
turned 01
EISOPQAM 17 - 16
May 1996
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Span Reference Point
To set the span reference pomi. execute the procedure described below Note that the procedure
is the same as that for setting [he zero reference except that a span gas is used instead of a zero Cds Trie
procedure is
1 From ihe CALIBRATION MENU display, press 3 =Span
Note If you have selected the MANUAL option for the calibration mode, the displa> will
show the unsealed detector output values of the span media (expressed in counts) as
of the last calibration If you select the AUTO option, the count is not displayed
If your instrument is a dual detector type (PID and FID), you can set the span reference for
the PID and FID separate!}, both together, or one in one type of calibration gas and one in
another rype of gas To do so. follow the same procedure
When you press 3 = Span. the display will show.
FID-only PID-only PID/FID
Span Cal Span Cat Span Cal
Enter = 5urt Emer = Start Emer=Start
2 To perform the actual SPAN calibration for a
FID-only or PID-only or PID/FID
Press ENTER Press ENTER Press Enter
Appl\ Span Gas Appl> Span Gas Apply Span Gas
FID PID PID/FID
Enter = Start Enter = Start Emer=Start
Exit = Cancel Extt = Cancel Exit = Cancel
3 Apply the span gas to the probe at ambient pressure (using a clean and labeled gas bag) and
then press ENTER
Calibrating Calibrating Calibrating
FID PID FID/PID
Span Gas Span Gas Span Gas
Exn=Cancel Exn=Cancel Exn = Cancel
The instrument analyzes the span sample
Calibrating . Calibrating Calibrating. .
FID PID FID/PID
ACCEPTED ACCEPTED ACCEPTED
DSOPQAM 17-17 May 1996
-------
The ACCEPTED message appears for a brief time and is then replaced by the normal
CALIBRATION menu
When the ACCEPTED message disappears and the CALIBRATION menu appears the SPAN
reference value is stored This value is stored in non-volatile memory The date and time ol
this calibration are stored and can be accessed through the INFO menu
Define the Gas Concentration
1 From the CALIBRATION menu display, press 4 = Gas Cone.
Note At this time, the upper display (or two displays if unit has both FID and PID detectors)
reads the concentration value of the span gas (expressed as %, PPM, or PPB) as of the
last calibration If this is the first time that the unit has been turned ON. the displa\
reads 1 St With duel detector units, the lower displays prompt you to select the
detector type to be calibrated, i.e.. l=Both, 2 = PID, and 3=FID
Since this instrument has dual detectors you may choose to calibrate the PID and FID
separately or together The gas concentration values refer to the known concentration of
the calibration span gases used
FID-onK PID-onl> FID/PID
FID 100% PID 1 005 PID 1.00%
FID- 1.00%
Span Gas Cone Span Gas Cone Span Gas Cone 1 = Both
Enter = New Calib Enter = New Cahb 2 = PID 3=FID
2 To change the gas concentration to a new value, press 1. 2. or 3 (The value that you enter
must be the concentration of the actual span gas used for the span reference point) You will
see
FID-only PID-only FID/PID
Enter Span Cone Enter Span Cone Enter Span Cone
F1DOOOOS PID 00 00$ F&P 00 DOS
Lp-Dn=Next Unn Lp Dn = Nexi Una L)p/Dn = Next Unit
Enter = Accept
Use the up and down keys to select Z. PPM. PPB. and decimal point position, and then enter
the numeric value for the known concentration
3 Press ENTER to store the new values into the instrument memory.
4 Press EXIT to return to the CALIBRATION menu Gas concentration ranges are defined in
the following table on the next page
EISOPQAM 17-18 May 1996
-------
GAS CONCENTRATION RANGES
RANGE
5
4
3
2
1
UNITS
%
PPM
PPM
PPM
PPB
DISPLAY
DDDD
DDDDDD
DDDD D
DDD.DDD
DDDDDD
The range of the instrument is determined by the manner in which you enter the numeric value of
the cas concentration (how you select the measurement units and place the decimal)
After you have entered the value for the gas concentration, enter the RUN mode The msirumeni
w ill auto-range (upward only) to select optimum range for displaying the measurement information
For example, if you entered a value in Range 3 and measured value changes to a high, the
instrument will automatically switch to range 4 If it increases further, it will switch to Range 5
Noie thai the auto-ranging will noi switch ranges in the down direction
Define the Response Factor
Response Factor is the means b\ which the TV A 1000A automatically corrects for the direct
readme of a single concentration of an> cas other than 1 Refer to Foxboro for this response factor
1 From the CALIBRATION menu displaj . press 5 = Response Factor
Noie
If the cas to be measured is noi the same compound for which the respective deiector was
calibrated, the response factor ma\ be something other than 1 Refer to Foxboro for this
response factor
At this time, two displays read the response factor (expressed as a ratio) as of the last
calibration Response Facior is a measure of sensitivity of the TVA to any compound
referenced against the calibration span gas used for each detector
Response Factor = (Response to Gas 10 be Measured )/(Response to Cal Gas)
For example PID= 1 00 or FID = I 00 are displayed simultaneously with dual detector
units Vnih dual detector units, the lower two displays prompt you 10
select the detector type to be calibrated, i.e., l=Both, 2 = PID and
EISOPQAM
17- 19
May 1996
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FID-only PID-only FID/PID
FID 100 PID 100 FID- 1.00
PID. 1 00
Response Facior Response Factor Resp FCT l=Both
2=PID3 = FID
2 To change the response facior to a new value, press 1, 2, or 3 and see
FID-only PID-only FID/PID
Emer Resp Fact Enter Resp. Fact. Enter Resp Fact
FID 00.00 PID 0000 F&P: 00.00
Enier = Accept Enter = Accept Enter=Accept
Enter the appropriate response factor for your specific gas Refer to Foxboro for values for
specific gases
3 Press ENTER to store the new values into the instrument memory.
4 Press EXIT to return to the CALIBRATION menu.
EISOPQAM p - 20 May 1996
-------
Alarm Levels
The TVA-1000 is supplied with three user-configurable alarms - HI Ceiling, Low Ceiling anil
STEL (short icrrn exposure limit) When any one of these alarms is exceeded, an alarm message i^
displayed on ihe sidepack display only and an alarm tone is generated Press EXIT to acknowledge; the
alarm message and sounder Once acknowledged, the display returns to the live measurement with . press 2 = Setup
2 From the SETUP menu displa>. press 2 = Alarms and follow the procedures for the appropriate
alarm settings
EISOPQAM
17-21
May 1996
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STEL Level Alarm
1 From the ALARM LEVELS display, press 1 =STEL The previous alarm settings for STEL
alarm are then displayed as follows
FID-only PID-only PID/FID
FID 80 00 ppm P!D 80 00 ppm PID 80.00 ppm
STEL Alarm STEL Alarm FID 80 00 ppm
Enter = Ne\v Value Enter = New Value STEL'l=Both 2 = PID 3 = FID
2 To change the alarm level 10 a new value, press ENTER on a single detector instrument or I.
2. or 3 on a dual detector instrument and see:
FID-only PID-only PID/FID
Enter STEL Enter STEL: Enter STEL-
FID 000.00 ppm PID 000.00 ppm P&F: 000.00 ppm
UP/Dn = Next Unit UP/Dn = Next Unit UP/Dn = Next Unit
Emer = Accept Emer=Accept Emer=Accept
Use the up and down arrow keys to select %, PPM, PPB. and decimal point position, then
enter the numeric value for the alarm level desired.
3 Press ENTER to store new values into the instruments memory
4 Press EXIT to return to the ALARM LEVELS
Lo" Ceiling Alarm
1 From the ALARM LEVEL displav. press 2 = Low Ceiling The previous alarm settings for
ihe Low Ceiling alarm are then displayed, as follows
FID-only PID-onl> PID/FID
Low Ceiling Alarm Low Ceiling Alarm
FID 80 00 ppm PID 80 00 ppm P&F 80 00 ppm
Emer = New Value Emer = New Value Low Ceiling 1 = Both 2 = PID 3 = FID
2 To chance the alarm level to a new value, press ENTER on a single detector instrument or 1.
2. or 3 on a dual detector instrument and see
FID-only PID-onl> PID/FID
Enter Low Ceil Emer Low Ceil Enter Low Ceil
FID 000 00 ppm PID 000 00 ppm P&F 000 00 ppm
UP/Dn = Next Unit UP/Dn = Nexi Unit UP/Dn = Next Unit
Enter = Accept Emer = Accept Emer = Accept
Use the up and down keys to select £. PPM. PPB. and decimal point position, and then enter
the numeric value for the alarm level desired
EISOPQAM 17-22
May 1996
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3 Press ENTER 10 store the new values into the instruments memory
4 Press EXIT to return to the ALARM LEVELS
High Ceiling Alarm
1 From the ALARM LEVEL display, press 3 = High Ceiling The previous alarm settings tor
the High Ceiling alarm are then displayed, as follows
FID-only PID-only PID/FID
High Ceiling Alarm High Ceiling Alarm
FID 80 00 ppm PID 80.00 ppm P&.F 80 00 ppm
Emer=New Value Enter = New Value High Ceiling 1 =Both 2 = PID 3 = FID
2 To change the alarm level to a new value, press ENTER on a single detector instrument or 1.
2. or 3 on a dual detector instrument and see
FID-only PID-only PID/FID
Emer High Ceil Enter High Ceil Enter High Ceil
FID 000 00 ppm PID 000.00 ppm P&F. 000 00 ppm
UP/Dn = Next Una UP/Dn = Next Unit UP/Dn = Next Umi
Enter = Accept Enter = Accept Enter=Accept
Use the up and down keys to select %. PPM, PPB, and decimal point position, and then type
the numeric value for the alarm level desired
3 Press ENTER to store the new values into the instruments memory'
4 Press EXIT to return to the ALARM LEVELS
E1SOPQAM 17-23 May 1996
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17.5 Centun Model OVA-128 Organic Vapor Analyzer
Introduction
The Century Model OVA-128 Organic Vapor Analyzer (OVA) is designed to detect organs
compounds in air
• h uses a hydrogen flame lomzation detector (FID) as its detection principle This detector
allows the monitor 10 respond to a wide variety of organic compounds, bui limits its sensitive
to around 10 ppm under ideal circumstances The OVA's best response is to single-bonded
hydrocarbons such as methane and dichloroethane
- THE LACK OF A RESPONSE ON THIS METER DOES NOT GUARANTEE THAT THE
ENVIRONMENT IS SAFE
Operational Checks
1 Connect the hand readout unit's electrical and pneumatic finings to the side pack assembly
2 Connect probe to the hand readout unit
3 Place the "PUMP" switch in the ON position Check the battery's condition b> placing the
"INSTR" switch to the BATT position and observe the response on the hand readout unit
4 Place the "INSTR" switch in the ON position.
5 Set the "Calibration Switch' to the "XlO" position
6 Use the "CALIBRATE" knob to set the readout to a reading of 6 Using the Alarm Level
Adiustment Knob on the back of the readout, obtain an audible response 10 ihe reading of 6
T Set the "Calibration Switch"
10 Open the "H, TANK VALVE' and the "H: SUPPLY VALVE" one turn each Allow fuel to flo*
for aboui 1 minute
I! Press ignitor button and hold until readout unit indicates ignition
12 Use "CALIBRATE" knob 10 set readout to a reading of 0
• Note a small positive offset above 0 may be necessary to prevent activation of the
flame-out alarm
EISOPQAM 17-24 Mav 1996
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Calibration
1 Assemble a calibration manifold as described in Section 17 1 using methane as the calibration
gas (Remember to omit the use of a Teflon* bag )
2 Set the "CALIBRATION SWITCH" to the appropriate position for the concentration of the
calibration gas (usually X10)
3 Connect the instrument's probe to the calibration manifold and allow it to sample the
calibration gas
4 The readout should indicate a value which is close to the concentration of the calibration gas
plus any offset which may have been added.
5 Place the "CALIBRATION SWITCH" in the "XI11 position before entering the sue
EISOPQAM 17.2s May 1996
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17.6 HNu Model PI 101 Pholoionization Detector
Introduction
The HNu model PI 101 is designed 10 detect primarily organic compounds in air It uses a
photoionizanon detector (PID) as us method of operation. The instrument is capable of measuring
concentrations down to about 1 ppm sensitivity for certain compounds
• h is important to realize thai this sensitivity is not achievable for all compounds Some
materials will result in a very low response on the PID in relation to their actual
concentrations, while others will not respond at all to the detector's lomzation energ\
• As a general rule, the PID should not be used to monitor for low molecular weight
hydrocarbon compounds whose structures contain only single bonds (methane, ethane.
pentane, hexane, heptane, carbon tetrachloride, and hydrogen sulfide) The PID should be
used to detect aromatics such as benzene, toluene, and styrene, aliphatic amines such as
diethylamine. and chlorinated unsaturated compounds such as vinyl chloride, and
tnchloroethylene
- THE LACK OF A RESPONSE ON THIS METER DOES NOT GUARANTEE THAT THF
ENVIRONMENT IS SAFE
Operational Checks
1 Connect the probe to the meter case of the instrument
2 Place the function/range switch in the "BATT" position and note the meter's response
3 Place the function/range switch in am of the three range positions Listen closely to the probe
for a humming sound which indicates that the sample fan is operating
Calibration
1 Place the function/ranee
-------
17.7 Ludlum Model 3 Radiation Survey Meter
Introduction
The Ludlum Model 3 is a portable radiation survey meter. The instrument is set for 900 voli
Gejger-Mueller Tube (GMT) measurement of beia and gamma radiation. The range of the meter is from
0 (o 200 milliroemgen per hour It is important that the operator realizes that this meter will not respond
(o most alpha radiation
- THE LACK OF A RESPONSE QN THIS METER DOES NOT GUARANTEE THAT THF.
ENVtRONMENT IS SAFE
Operational Checks
1 Place the multifunction switch m the "BAT" position and note the meter's reading
2 Place the multifunction swuch in the "XO.l" position, the F/S switch in the "S" position, and
the "AUDIO" switch in the "ON" position Note that an audible clicking sound can be heard
while the meter is counting After a few seconds, press the "RES" button and note that the
meter returns to zero
Calibration
1 Read and record the background radiation level
2 Place the GMT probe flai aeamst the casing of a certified Sr90 standard
3 Adjust the multifunction switch unnl the meter reading remains on scale
4 Read and record the meter s response
5 Calculate the detector's effkienc\ as follows
E = Meier Reading - Background
Activity
6 Check to insure that the calculated efficiency is within ± 0 1 of the efficiency rating placarded
on the meter
1 Set the multifunction switch to "XO 1' before entering the sue
E1SOPQAM 17 - 27 May 1996
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17.8 MiniRAE
Introduction
The MiniRAE (RAE) is a programriable pbotoionization detector (PID) that measures organic
vapors in hazardous environments It incorporates a sampling pump and data download capabilities for
continuous loxic monitoring, site survey, and leak detection. The RAE can measure double-bonded
organic vapors with its supplied 10 6 eV gai discharge lamp The RAE is calibrated with toluene
• The RAE is intrinsically safe
• Only key steps are listed below Almost all set-up functions on the RAE have been pre-sej
The keys you will need to press will generally deal with calibration
• The battery on the RAE drams slow -y even when turned off If the unit has not been charged
for 4-5 days, the battery voltage v, II be low If the unit is left to charge overnight, n will
automatically shut itself off when fuily charged.
• Only operate the RAE in the survey mode The RAE has been pre-set to automatically Stan
in the survey mode.
Operating Procedures
1 Power On/Off
To Turn On the RAE oress the [on| ke\ The audio buzzer will beep once and the displas
will show "HG-x x\" or "Su-x xx 10 indicate the operating mode and software version
number The unit will then go through a self-diagnostic routine to check the kev
components of the unu A ' diac ' message will be displayed with a red back light turned
on while the self-diagnostic routine :< execu-.ing The red LED and back light will flash once
and the buzzer will beep once to ensure thai they are functional. The sampling pump will be
turned on and start 10 draw air sample
To turn Off the RAE press the lonl key The message "off will flash on the LED displaj.
press the I enter I ke\ to connrm anc1 the unit -vill be turned off Pressing any other key will
return the unit to normal operation
2 The RAE can display five different T adings instantaneous gas concentration. STEL. TWA.
and peak and batter> voltace Mosi u: these functions have either been pre-set or do not apply
10 most Branch surveys Onl\ press (enter] 10 «-croll through each display
3 Alarm Signal - The buili-in microcomputer corstamly updates and monitors real ume gas
concentrations and compares it will) the programmed alarm limits Whenever the
concentration exceeds an> of the preset limits (5 ppm), the alarm buzzer and red flashing
LED will be activated immediate!} 10 warn the user of the alarm condition
Whenever the banen voltage falls below 5.5 volt (6 3v or higher is normal) or the UV lamp
or sensor module fails, the unit will also activate the buzzer and red LED alarm signal
ElSOPQ^M ]--28 May 1996
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In the Survey Mode, the alarm signal is proportional to the level of the gas concenirjtion
Therefore, when the gas concentration exceeds preset limits (5 ppm), the alarm signal ITU\
very from a single beep and a single flash per second to a rapid 7 beeps and 7 flashes per
second when the high threshold level has been exceeded The higher frequency of alarm sitinj!
indicates higher gas concentrations.
4 Back Light - The LCD display is equipped with a red LED back light to assist the readings
under poor lighting conditions This back light can be turned on by pressing the |up] ke>
When the back lighi is already on. pressing the [up] key will turn it off
5 Charging the RAE - On the back side of ihe RAE is a battery charging jack which is normall)
covered by a protective rubber cover Open the rubber cover and connect the AC adapter tor
the automotive DC charging adapter, depending on the power source to the charging jack)
There is a bi-colored LED inside the LED window which will provide an indication of the
charging status
Red - banery is being charged
Green - charging is completed
No light - bad connection or defective battery
Plug in the AC (or DC) adapter which will turn on the red charge status LED first If ihe
battery is fully charged, it will turn to green quickly A completely discharged battery will be
charged to its full capacity within 10 hours
Calibration
In the survey mode, the user ma> re-calibrate the RAE This is a two-point calibration process
using Zero Gas and a Standard Reference Gas
t First, a zero gas which contains no detectable organic vapors is used to set the zero pomi
(CO)
2 Second, a standard reference gas is used to set the second point of reference (Cl)
Zero ga«^ Calibration
Use a gas bag (I liter) and zero concentration gas from your air box
I Fill the gas bag with zero concentration gas Zero gas calibration option is the 5th menu
option Display shows CO xxx x where x xxx is the gas reading based on current calibration
of the instrument
2 Attach the gas bag to the inlet rube and open the bag so that the instrument can begin pumping
the zero concentranon gas The display should be reading zero
3 If this reading is not zero, press the lenterj ke> to zero it If the reading still shows a small
\alue after a few seconds, press the |emer] key again to zero it Repeat this process until the
reading is stabilized around zero or 0 1 ppm This completes ihe zero gas calibration Press
the [menu] key to exit zero gas calibration while the bag is still on the instrument
EISOPQAM n . 29 May 1996
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Enier Siandard Calibration Gas Value
I Enter standard gas value option is the 6th menu option
2 If the concentration of the standard calibration gas to be used is the same as the displaced
value, press (enter] ke> 4 times to accept the displayed calibration value one digit at a time
and move to the next step
3 If the concentration of the standard calibration gas to be used is different from the displaved
value, the user needs to enter the new value Starting from the left most digit of the displaved
value, use the |up] or (down) arrow key to change the digit value and [enter] to confirm the
digit
4 Now the standard calibration gas value is entered.
Display shows a flashing message of "GAS ON" to remind the user to turn on the standard
calibration gas bottle no* After the gas bottle is turned on, press (enter] key to continue the
standard calibration procedure
Standard Gas Calibration Procedure
1 Insert the instrument probe into the calibration gas bag (bag should be at least 1 liter) that is
filled with toluene.
2 Display shows a flashing message of "GAS ON".
Press the [enter] kev. the display should show CAL.. for about 30 seconds while the
instrument performs calibration Afterwards, the display shows Cl xxx x where Cl indicates
that this is the standard calibration gas and xxx x is the actual gas reading in ppm based on the
new calibration data
Note The readme should be ver> close to the value of the calibration gas If the reading is
higher or lower than the standard gas value and continues to rise slowly, it means thai
the calibration gas has not yet stabilized Wait a few seconds until the reading
stabilizes and then press the [enter] key again Every time the [enter] is pressed, the
instrument measures the current gas concentration and calibrate according!)
3 Press the [menu] ke\ to exit the standard gas calibration procedure and move 10 next menu
item
•4 Disconnect the calibration ga«. bag
EISOPQAM 17-30 May 1996
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SECTION 18
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SECTION 18
FLOW MEASUREMENT
18.1 Introduction
The measurement of flow with surface water and wastewater sampling is essential to almosi all
water pollution control activities Activities such as water quality enforcement studies. NPDES permn
compliance monitoring, water quality monitoring, municipal operation and maintenance investigations.
planning, and research rely on accurate flow measurements. The importance of obtaining accurate flow
data cannot be overemphasized, particularly with respect to enforcement investigations since these data will
be used as evidence in enforcement cases NPDES permits often limit the quantity (mass loading) of a
particular pollutant that may be discharged, and the calculation of mass loadings are also frequentlx
necessary for water quality studies and other purposes. As much attention and care should be given 10 flow
measurement in the design of a sampling program as to the collection of samples and their subsequent
laboratory analysis
The basic objectives of this section are to-
• outline standard practices with respect to wastewater flow measurements during water
enforcement and NPDES compliance monitoring activities and other studies where wastewater
flow measurements are required.
• outline standard practices for obtaining surface water flow measurements during water qualm-
surveys,
• present acceptable, commonlj used flow measurement techniques: and
• present general and specific quality assurance procedures for flow measurement equipment and
techniques
A complete discussion of all available flow measurement techniques and the theory behind them
is ne\ond the scope of this seciton However, most of the commonly used techniques are covered in
general terms A comprehensi\e IIM of references is included at the end of this section and a detailed
discussion of flow measurement techniques may be found in the references
EISOPQAM 18-1
May 1996
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18.2 \\astewater Flow Measurement
1821 Introduction
The USD1 Water Measurement Manual (I) is a standard reference for details on checking the
installation of primary open channel flow devices Basic guidance for making wastewater flow
measurements and a basic description of all acceptable wastewater flow measurement systems are given
in the NPDES Compliance Inspection Manual. September 1984 (2) This manual shall be used as Branch
guidance for such measurements
1822 Site Selection
It is the field investigator's responsibility to insure that the wastewater flow measuremem system
or technique used measures the total wastewater discharged (described by the NPDES permit if
applicable) All recycled wastewaters must be accounted for so that any reported flows accurately reflect
the volume of wastewaters discharged The location of the wastewater flow measurement equipment
should satisfy these criteria, be consistent with NPDES permit requirements, and measure the actual flow
1823 Flow.1 Measurement Systems
Flow may be measured on an instantaneous or a continuous basis A typical continuous system
consists of a primary flow device, a flow sensor, transmitting equipment, a recorder, and a totalizer
Instantaneous flow measurements can be obtained without using such a system.
The heari of a typical continuous flow measuremem system is the primary flow device This device
is constructed to produce predictable hydraulic responses which are related to the flow rate of water or
wasiewater through it Examples of such devices include weirs and flumes which relate water depth (head)
to flow. \ enrun and orifice type meters which relate the differential pressure to flow, and magnetic flow
meters which relate induced electric voltage to flow Standard primary flow devices have undergone
detailed testing and experimentation, and their accuracy has been verified.
A flow sensor is required to measure the particular hydraulic responses of the primary flow
mejsurement device and transmit them to the recording system Typically, sensors include ultra-sonic
transmitters, floats, pressure transducers, capacitance probes, differential pressure cells, electromagnetic
cells, etc The sensor signal is generalK converted using mechanical, electromechanical, or electronic
s> stems into units of flow which are recorded directK on a chart or transmitted into a data system Systems
which utilize a recorder are general!) equipped with a flow totalizer which displays the total flow on a real
time basis
Srudies thai need continuous flow measurements require a complete system Instantaneous flow
measurements do not necessanK dictate the use of any portion of such a system Techniques which are
described laier m this Section are available for measuring instantaneous flows with portable equipment
An important consideration during wastewater studies is that the investigator may want to obtain
continuous flow data at a facility- where only instantaneous flow data are being measured If an open
channel pnman flow device is utilized for making instantaneous measurements, only the installation of a
portable Held sensor and recorder is necessary If, on the other hand, the facility being investigated does
not utilize a pnman flow device, and a continuous flow record is desired, a portable primary flow device
will have to be installed Field investigators have both open channel equipment and closed conduit flow
meters available for field use These devices should be installed according to the manufacturers
E1SOPQAM |g.2 May 1996
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specifications
Wasiewaier flow measurcrmen systems are generally very accurate Any system thai cannoi
measure the wastewater flow within _± 1< percent of the actual flow is considered unacceptable for use in
measuring wastewaier flow
1824 Use of Existing Flow Measurement Systems
The installation of systems 10 measure wastewater flows can be a lime consuming task, pariicularh
if a primary device is not available Therefore, field personnel can use existing facility primarx flow
devices and flow measurement systems when the accuracy of these devices and the system can be verified
The objective of this section is to outline the responsibilities of field personnel in verifying the accuracj
of existing primary flow devices and systems
The field investigator must verify that jny existing facility flow measurement system (including
primary flow device) utilized to measure wasiew.ier flows conforms with recognized design and installation
standards, and any deviation from standard cono.tions shall be thoroughly documented The accuracy of
the primary flow device should be checked by making an independent flow measurement If there is no
usable or existing primary flow measjring device or if the device has been mislocated. the investigator shall
attempt to install a portable pnman How. device
If the discharger's flow measurement system is accurate within ±10 percent of the actual flow, the
investigator can use the installed sv5-=m The accuracy of flow sensors and recorders for open channel
fl
the investigator and the discharger should be informed th.it the equipment should be calibrated as soon as
possible
1825 Specific Techniques
This section outlines and famih.irues the field investigator with the most commonly used methods
for uasieuater flow measurements anc nc primary devices ihat will be encountered during field studies
Volumetric and dilution techniques are : -estnted at the beginning of this section, since they are applicable
to both open channel and closed conujii flow situations The remaining methods are grouped under
categories dealing with open channels jnd closed conduits The general method of checking individual
primary flo* devices is given, where applicable Several estimation techniques are presented However.
it Miould be recognized that flow estimates do not satisfy NPDES permit monitoring requirements unless
ilis permu specifically states that this is permissible The following methods are included only to enable
the field investigator to make accurate 1> >* estimates when necessary
V olumetric Techniques
Volumetric flow measurement techniques are among the simplest and most accurate methods for
measuring flow These techniques basically involve the measurement of volume and/or the measurement
EISOPQAM 18-3 May 1996
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of time required to Till a container of known size
Vessel Volumes
The measurement of vessel volumes to obtain flow data is particularly applicable to batch
wastewater discharges Accurate measurements of the vessel volumes and the frequency that the> arc
dumped are all lhai is required An accurate tape to verify vessel dimensions and a stop waich are the onK
required field equipment The NPDES Compliance Inspection Manual (2) is a useful reference on the
equations for calculating volumes of various containers
Sump Pumps
This measurement is made by observing the sump levels when the pumps cut on and off and
calculating the volume contained between these levels. This volume, along with the number of pump
cycles, will give a good estimate of the daily wastewater flow. The inspector must also account for the
quantiry of wastewater that flows into the sump during the pumping cycle
Bucket and Stop Watch
The bucket and stop watch technique is particularly useful for the measurement of small wastewater
flows It is accurate and easy to use The only equipment required to make this measurement is a
calibrated container (bucket, drum. lanL etc ) and a stop watch A minimum of 10 seconds to fill the
container is recommended Three consecutive measurements should be made, and the results should be
averaged
Dilution Methods
Dilution methods for water and wasiewaier flow measurements are based on the color.
conductivity, fluorescence, or other quantifiable property of an injected tracer The dilution methods
require specialized equipment, special attention to detail by the investigator, and are time consuming
However, these techniques offer the investigator
• a method for making instantaneous flow measurements where other methods are inappropriate
or impossible to use.
• a reference procedure of high accuracv to check m-situ those primary flow devices and flow
measurement systems thai are non-standard or are improperly installed, and
• a procedure to verify the accurac> of closed conduit flow measuring systems
The Turner Designs nomograph (3). the NPDES Compliance Inspection Manual (2). and the U S
Geological Survey publication (4) outline recommended reference procedures. The dilution method
utilizing Rhodamme \VT dye is the preferred reference procedure to be utilized by inspectors when
verihmc the accuracy of flow measurement systems
IS 2 6 Open Channel Flow Measurements
The measurement of wastewater flow m open channels is the most frequently encountered situation
during field investigations An open channel is defined as any open conduit, such as a channel or flume.
E1SOPQAM 18-4 May 1996
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or any closed conduit, such as a pipe, which is noi (lowing full The most commonly encountered methixh
in measuring open channel wastewater flows are described in this section Several flow estimation
techniques are also presented
The measurement accuracies quoted in this section apply only to the specific method or to the
primary flow device being discussed The total error involved in a continuous flow measurement system.
which is the sum of the errors of each component, is beyond the scope of this discussion The reader is
referred 10 the list of references at the end of this chapter for such a discussion
Weirs
A weir is basically defined as an overflow structure built according to specific design standards
across an open channel to measure the flow of water. The theory of flow measurements utilizing weirs
involves the release of potential static energy 10 kinetic energy. Equations can be derived for weirs of
specific geometry which relate static head to water flow (discharge). Weirs are generally classified into
two general categories, broad crested and sharp crested.
Broad crested weirs take the following form. Q=CLtHJ/:. Values for the coefficient C are given
in hydraulic handbooks (5. 6) Unless such weirs have been independently calibrated, they are usually not
accurate enough for wastewater flow measurements
Sharp crested weirs are constructed in a wide variety of shapes and the most commonly
encountered are V-notch, rectangular, and Cipolletti weirs If such weirs are constructed as outlined in
the USDI Water Measurement Manual (1). they are considered standard primary flow devices
All weirs should be inspected to determine if the weir installation and construction conform to the
conditions given m the USDI ^ater Measurement Manual (1). and provide a uniform influent flow
distribution and that the weir is placed squareh across the channel perpendicular to the direction of flow
Useful tools for checking weir construction and installation include a carpenter's level, a framing square
a measuring tape, a staff gage, or surveyors level and rod Problems observed during the inspection or
studs should be noted in the Held records or log book
A set of weir tables is necessar> for calculating flows The USDI Water Measurement Manual (1).
the Steven* V>ater Resource Data Book (7). and the 1SCO Open Channel Flow Measurement Handbook
(8) contain a complete set of tables
Flume*
The conditions that must be met in a flume are similar to those that occur at a weir or spillway crest
since uaier passinc through the tJiroat should not be impeded by downstream conditions (e.g .
constrictions, bends in channel, obstructions) There are several types of flumes (e g., Palmer-Bowlus.
Cutthroat. H. and Trapezoidal) but the most widely used is the Parshall flume The Parshall flume is
considered a standard primary flow device when constructed and installed as outlined in the USDI Water
Mcdsuremcni Manual (1) A complete discussion of other types of flumes is given in references 9. 10, II.
and 12
All flumes should be inspected to determine if entrance conditions provide a uniform influent flow
distribution, the flume dimensions conform to those given in the USDI Water Measurement Manual (1),
the floor of the flume at the throat section is level, and the throat section walls are vertical Useful tools
for checking the construction and installation of Parshall (and other) flumes include a carpenter's level, a
EISOPQ4M 18-5 May 1996
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framing square, and a measuring tape The flume should be closely examined to determine if n i^
discharging freely If there is any question about free discharge, the downstream head (Hbi should he
measured and compared to the head at the proper location (Ha) in the converging section A staff gdt!e
is useful for making head measurements Any problems observed during the inspection or stud> should
be noted in the field log book
A set of flume tables is necessary for calculating flows. The USDI Water Measurement Manual
(I). the Stevens Water Resources Data Book (7), and the ISCO Open Channel Flow Measurement
Handbook (8) contain a complete sei of tables The explanatory material accompanying these tables should
be read and understood before they are used In many cases, tabulated flow values are given for measured
heads thai are not within the usable measurement range
Open Flov. Nozzles
Open flow nozzles such as parabolic or Kennison nozzles are factory calibrated and are ordinarily
supplied as part of a flow measurement system Calibration and installation information for each nozzle
should be supplied by or obtained from the manufacturer The accuracy of these devices is reported to be
often beuer than ± 5 percent of the indicated flow (10) A framing square is useful for checking the
installation A volumetric flow measurement may be used to check accuracy of this device if flow volumes
are noi excessive
Velocitv-Area Method
The basic principal of this method is thai the flow m a channel (cubic feet/second) is equal to the
average velocin (feet/second) times the cross sectional area (square feet) of the channel The velocity of
the water or wastewater is determined w ith a current meter The area of the channel is either measured
or calculated using an approximation technique The USGS mid-section method and the stream gaging
techniques described in the USGS publication. Discharge Measurements at Gaging Stations (9) is standard
practice This technique shall be used (where appropriate) as an independent flow measurement to venf\
the accuracy of existing flow measurement systems
Slope-Area Method
The slope-area method consists of using the slope of the water surface, in a uniform reach of
channel, and the average cross-sectional area of that reach, to estimate the flow rate of an open channel
The flow rate is estimated from the Manning formula (5. 6)
1827 Closed Conduit Flow Measurements
The accurac> of closed conduit flou measuring devices shall be checked when necessary, by
rrukinc an independent flow measurement, preferably using a dilution technique
\ cmuri Meter
The Venturi meter employs a comersion of static head to velocity head whereby a differential is
created that is proportional to flow The typical accuracy of a Venturi meter is at 1 to 2 percent (10 11
12. and 13)
Orifice Meter
EISOPQAM 18-6 May 1996
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The orifice meter is a pressure differential device that measures flow by the difference in static
head Orifice meters require from 40 to 60 pipe diameters of straight pipe upstream of the installation
They can be accurate, e.g . within 0 5 percent, although their usable range is limited (10)
Flow Nozzle
The basic principle of operation is the same as that of the Ventun meter The flow nozzle has an
entrance section and a throat, but lacks the diverging section of the Ventun meter Flow nozzle accuracies
can approach those of Venrun meters (lOj
Electromagnetic Flow Meter
The electromagnetic flow meter operates according to Faraday's Law of Induction where the
conductor is the liquid stream, and the field is produced by a set of electromagnetic coils The accuracy
of the device is within +.1 percent of full scale (10).
Other Closed Conduct Devices
References for other closed conduit flow measurement methods such as acoustic flow meters.
iraiecton methods, pump curves, and water meters can be found in the NPDES Compliance Inspection
Manual (2)
18.3 Surface V\aler Flow Measurements
IS 3 1 Introduction
Surface waters are considered to be open channels for flow measurement purposes All of the
technique? utilized b> field investigators to measure open channel flows have been discussed in the
wasiewater flow measurement portion of this section Except for very small surface streams, the
installation of primary flow devices is not practical Most surface water flow measurements are made
utilizing classical stream gaging techniques These techniques involve the use of the velocity-area open
channel technique which was discussed in the waste water portion of this section Branch personnel shall
use the techniques outlined in the USGS publication Discharge Measurements at Gaging Stations (9) to
• select the flow measurmc sue
• perform stream gaging, and
• calculate flow
1852 Techniques
Whenever possible, stream studies shall be conducted utilizing existing permanent stream gaging
stations operated b> the USGS. the t! S Army COE. or other federal or state agencies These permanent
cacmg stations have established v.ater stage-discharge relationships that permit the flow to be obtained from
water stage measurements Staff gage or recorder readings of water stage at these stations may be
converted to flow, by using the rating curve for that gaging station The rating curve is generally available
EISOPQAM IB -7 May 1996
-------
from the operator of the permanent gaping station An additional benefit of utilizing these
gaging stations is that long-term flow records are generally available These long-term flow records art-
invaluable in planning water quality studies and assessing data trends
Where permanent gaging stations do not exist, surface water flow will have to be measured
utilizing classical stream gaging techniques If a station is to be used more than one time during a water
quality survey, a rating curve should be developed for that station This may be done by making a series
of independent flow measurements and simultaneous tape down or staff gage measurements for thai station
at different water levels The rating curve is developed utilizing the same measurement section each time
ai least two (preferably three) flow, measurement-tape downs should be made The flow measurements
used to develop the rating curve must bracket the lowest and highest flows encountered during the studv
A tape-down rating curve is constructed b> plotting the tape-down measurements verses flows on a piece
of semi-log graph paper
18.4 General Quality Assurance Procedures
Techniques and procedures for making wastewater and surface water flow measurements are
outlined in this section The USDI Water Measurement Manual (1), the USGS publication Discharge
Measurements at Gaping Stations f9l. the EPA NPDES Compliance Inspection Manual (2) and a set of weir
and flume tables shall be supplied 10 all field investigators However, the measurements of waste water and
water flows require considerable experience Therefore, no field investigator shall make flow
measurements until they have had at least six months of actual field experience and has performed these
measurements under the supervision of a senior field investigator
\Vasiewaier flow shall be expressed in million gallons per day (mgd) or the metric equivalent
im'/dav) Stream flow shall be expressed in cubic feet per second (second feel) or the metric equivaleni
im'/sec) Time records associated with flow measurements shall be kept in local time, shall be made in
ihe 2400 hour military time format, and shall be recorded to the nearest five minutes
All flow measurements conducted shall be thoroughly documented in field records All
measurement shall be traceable both to the individual making the measurements and the equipment
utilized
A log of all maintenance, calibrations, and repairs for each piece of flow measuring equipment
shall be established The log shall be kept in such a manner that all maintenance and calibrations
performed on the equipment are traceable to the person performing them and to the calibration standard
utilized All equipment shall be numbered, or the US-EPA property or serial number shall be used to
facilitate identification
18.5 Equipment
The equipment available for the measurement of surface water or wastewater flows is categorized
as follows water level/stage hardware and recorders, velocity- measuring equipment and assemblies, and
direct flow measurement equipment and insirumentation
The hardware available to determine the rise and fall of a water surface with time (the water stage)
includes the following recording devices Stevens Model F horizontal drum recorders. Stevens Model A-
71 continuous strip chart recorders. Stevens Encoder Recorders, and ISCO Model 2870. 3210. and 3230
flow meters Non-recording equipment available includes vertical staff gages and tape-down systems (see
Section 15)
EISOPQ4M 18 - 8 May 1996
-------
Instruments and equipment available to make velocity cross-sectional area measurements include
current meters and sounding (depth) equipment The current meters available are the vertical-axis mounted
Price AA and Price pygmy meters (including direct readout meters), and ENDECO solid state memorv
current meters Sounding (determination of depth) is accomplished using Ratheon or Lorance recording
fathometers or with a standard top setting wading rod Width measurements are made using a Lee-Au
galvanized steel tag line which is segmented into equal divisions of length by metal beads or steel tapes
The equipment available for direct flow measurement includes the following priman devices
available for installation. V-riotch weir plates and rectangular weir plates The corresponding conversion
of water level to flow rate can be accomplished instantaneously from stage/staff gage reading*
corresponding 10 the primary flow device in use. or by instantaneous readings of the available recording
flow meter systems The continuous recording systems presently available are the ISCO Model 2870.
3210. and 3230 recording flow meiers
The Polysomcs Ultrasonic Flowmeter (Model UFM84P) is available for measuring flows m closed
pipes The largest size pipe that can be measured is a 90-inch pipe. The pipe must be flowing complete!)
full and not contain large amounts of air pockets A coupling jelly is spread on the face of two transducers.
and the transducers are mounted opposite each other on the outside of the pipe The meter must then be
calibrated according to the manufacturer's instructions.
18.6 Specific Equipment Qualit> Control Procedures
A log book shall be kept of all equipment utilized for measuring water flows, water stage/tape
downs. velocit\ measurements, flow recordings, etc The following maintenance and calibration
procedures shall be implemented
Steven* Model A-71 and Model F Stag'.- Recorders
See specific equipment and qualiu control procedures in Section 15 5
ISCO Model 1870 and 2870 Recording Flow Meters
The recording flow meiers shall be thoroughly tested annually to insure that the accuracy.
resolution, and precision are within the technical specifications as established by the manufacturer This
shall be accomplished by operating the instruments in a controlled test environment for a period not less
than 24 hours The test environment shall consist of a controlled atmospheric temperature, power source.
and water level/head Operation during the lesung period shall be according to the manufacturer's
instruction manual The functions thai shall be lesied include flow meter totalizer accuracy, flow recorder
tracing accuracy, and chart speed accurac\
In addition to the above annual testing program, an abbreviated testing procedure shall be
Londucied on the flow meters and recorders which will include a check of the following functions flow
meter and recorder response to chancing heads as shown on the meter's liquid level indicator and the
recorder s firm indicator, and bubble rate adiusi response The flow meters and recorders shall be checked
through the abbreviated procedure prior to field use
The following routine maintenance procedures shall apply whenever the equipment is returned from
the field the exterior of the meter and recorder case should be cleaned with soapy water (Appendix B).
the front panel desiccant and external desiccant cartridges should be reactivated (only if needed), the bubble
line should be inspected and cleaned, and sensors shall be cleaned
EISOPQAM IS. 9 May 1996
-------
Vertical Siaff Gages and Tape Down Systems
See specific equipment and quality control procedures in Section 15.5.
E1SOPQAM IS . 10 May 1996
-------
Price A A and Price Pvpmv Current Meters
All meters shall be examined before and after each discharge measurement The examination shall
include the meter cups or vanes, pivot and bearing, and shaft for damage, wear, or faulty alignment
Meter balance and alignment shall be checked prior to each use in the field (9) Meters shall be cleaned
and oiled daily when in use Surfaces that shall be cleaned and oiled on a yearly basis are the pivot
bearing, pentagear teeth and shaft, cylindrical shaft bearing, and thrust bearing at the cap
Top Setting Wading Rod
This equipment shall be cleaned and examined before and after each discharge measurement The
examination shall include a check on the sliding rod and lock set mechanism.
Lee-Au Tap Line
This equipment shall be inspected for damage and cleaned before and after each discharge
measurement The accuracy of the tag line will be checked initially and then once per year utilizing the
Invar steel surveyors chain The tag Ime(s) shall be accurate to 0.1 foot per 100 feet Any tag lines that
do not conform to this accurac> specification shall be repaired, recalibrated, or discarded Yearl\
maintenance shall include an inspection for potential breaks, a thorough washing, and a finish oiling
V-Notch and Rectangular Weir Plaies
These plates shall be cleaned and examined before and after each field installation Construction
and condition of weir plates shall conform to recognized standards (2) The plates shall be cleaned with
a soap\ wash water, followed b> a distilled water rinse The weir plates will be inspected to insure thai
the upstream edge of the plate remains sharp
EISOPQAM ,g.,|
May 1996
-------
18.6 REFERENCES
1 Water Measurement Manual. Second Edition. Revised, United States Departmeni of Interior
Bureau of Reclamation, 198 1 Available from the United States Government Pnnimc Office D C
20402
2 NPDES Compliance Inspection Manual. United States Environmental Protection Acenc\
September. 1984
3 Fluorometric Facts. Flow Measurements. Nomograph, Turner Designs Company Mountain V ieu
California, 1976
4 "Measurement of Discharge by Dye Dilution Methods," Hydraulic Measurement and Computation
Book I. Chapter 14. United States Department of the Interior, Geological Survey. 1965
5 Kmc H W . and E F Braier. Handbook of Hydraulics. Sixth Edition McGraw-Hill New York
1976
6 Davis. C V . and K E Sorenson. Handbook of Applied Hydraulics. Third Edition. McGraw-Hill
New York, 1969
7 Steven? Water Resource Data Book. Third Edition. Leopold Stevens, Inc. Beaverton Oregon
1978
S ISCO Open Channel Flow Measurement Handbook. Second Edition, Second Printing.
Instrumentation Specialists Compan> Lincoln. Nebraska. 1985
9 "Discharge Measurements ai Gating Stations." Hydraulic Measurement and Computation. Book
1. Chapter 11, United States Department of Interior. Geological Survey, 1965
10 "Sewer Flow Measuiemeni A State-of-the-An Assessment." Municipal Environmental Research
Laboraior) . Office of Research and Development, U S Environmental Protection Agenc\
Cincinnati. Ohio, 600-275027
1 1 A Guide 10 Methods and Standard* for the Measurement of Water Flow United States Department
of Commerce. National Bureau of Standards. NBS Special Publication 421. 1975
12 Wells. E A and H B Gotaas. 'Design of Venruri Flumes in Circular Conduits," American
Sociei\ of Civil Engineers. 82. Proc Paper 928, April 1956
13 American Society of Testing Materials. 1985 Annual Book of ASTM Sumriaifo Volume II -
ttaier. American Society of Testing Materials Philadelphia. Pennsylvania. 1985
EISOPQAM 18-12
May 1996
-------
APPENDIX A
-------
APPENDIX A
RECOMMENDED CONTAINERS, HOLDING TIMES, & PRESERVATION
ANALYTICAL GROUP
Soil/Sediment
Com
Pres
Hold
Water/Wastewater1 V\ aste
Cant
Pres
Hold j] Com
Pres
Hold
BIOLOGICAL
Bacteriological'
Toxiciiy. Acute
ToMcm . Chronic
--
--
-•
--
--
-
-
--
-
B
CU
CU
I
I
I
6hr
2
2
--
-•
--
--
--
--
--
--
--
INORGANICS
pH'
Dermal Corrosion
Flashpoint
BTL1 Comem
Ash Conient
Residual Chlorine'
Turbidir\
Conducmit)
Temperature'
BOD5
Solids Series
Settleable Solids
Nutrients (S.P)
Chloride
Ormo-P
Dissolved P
COD
Alkalimts
Color
Oil <5L Grease'
Metals
8G
-•
--
-•
--
--
-•
--
--
•-
--
•-
8G
-•
8G
--
8G
--
--
--
8G
NA
-•
--
--
--
--
--
--
--
--
--
--
I
-•
I
--
1
•-
-
-
I
--
--
--
-
-
--
--
--
--
--
--
--
NS
--
NS
••
NS
--
--
--
180
--
--
-
--
--
SM
SM
SM
SM
HP:
HP
HP
HP
LP
LP
LP
LP
LP
GP
LG
LP
--
--
--
--
--
NA
I
1
NA
1
I
I
S/l
NA
I'
SVF
S/I
S/l
I
S/I
N
-
--
--
--
-
F
2
28"
I
2
7
2
28
28
2
28
28
28
2
28
180
8G
8G
8G
8G
8G
--
--
--
--
--
-•
--
--
--
--
--
--
-
--
-
8G
NA
NA
NA
NA
NA
--
--
--
--
--
--
-•
--
--
--
--
--
--
--
--
NA
N
N
N
N
N
--
--
--
--
--
--
--
-
--
--
•-
--
~
--
--
180
ElBSOPQAM
A- 1
May 1996
-------
ANALYTICAL GROUP
Mercury
Metals - TCLP
Mcials - EP
Crormum V]
Cyanide
Sulfides
Sul fates
Nitrite
Nil rate
Hardness
Fluoride
Soil/Sediment
Com
8G
8G
8G
--
--
•-
--
--
--
--
--
Pres
I
I
J
-
--
--
--
--
--
--
-•
Hold
180
36012
3601:
--
-
-
--
-•
-
--
--
Water/Wastewater1
Com
LP
LP
LP
LP
LP
LP
LP
LP
HP
LP
LP
Pres
N
I
1
1
AVC'/I
Z/C'/I
I
I
I
N
NA
Hold
28
360''
360' :
1
14
7
28
2
2
180
28
Waste
Com
8G
8G
8G
--
8G
-
-
--
--
-
--
Pres
NA
NA
NA
-•
NA
--
--
--
--
--
--
Hold
180
360 ;
360-
--
14
--
--
-
-
--
--
ORGANICS
VOCs'
VOCs - TCLP'
Eviractables"
E\tractable^ - TCLP
Dicum*-"
Perceni Alcohol
Phenols
Ore HjhdiMTOXi
2G
2G
8G
8G
A
8G
--
8G
I
1
I
I
I
J
--
1
14
28'1
54"
61"
75"
NS
--
28
V
V
GO
GG
LA1
GG
LA
LA
Be/l
1
I9
1
I10
I
S/I
S/I
14/7"
28'3
47"
61"
7515
NS
28
28
8G
8G
8G
8G
A
8G
--
-•
NA
NA
NA
NA
1
NA
-•
--
14
28!i
54"
61"
75"
NS
--
-
General Footnotes:
Com - Container
Pres - Preservation
Hold - Holding Time (days)
- Grab sample only, unless indicated a grab or composite is acceptable.
1 - Consult 40 CFR Pan 136 Table II - Required Containers, Preservation Techniques, and Holding Times
for latest requirements
19 - Including pesticides, herbicides and PCBs
20 - Consult local laboratory- for most recent dioxin container and preservation requirements.
C1BSOPQAM
A-2
May 1996
-------
Containers:
B - Batenolocical container
CD - Cubitamer one gallon or 2 gallon
8G - 8 oz widemouih glass (Teflon lid)
20 - 2 oz widemouih glass (Teflon septum lid)
LP - One liter polyethylene
GG - One gallon amber glass (Teflon lid)
V - 40 ml glass (Teflon septum lid)
SM - Siormore 500 ml polyethylene
LG - One liier widemouth glass (Teflon lid)
GP - Gallon polyethylene
HP - Half-gallon polyethylene
LA - One liter amber glass (Teflon lid)
A - 500 ml widemouih amber glass (Teflon lid)
2 - Use GP for BOD with multiple parameters
3 - Collect 2 sample containers (LA) per sample plus 4 at one location for matrix spike
Preservatives:
A - Ascorbic acid
B - Sodium bisulfite
C - NaOH
H - HC1
I - Ice (4"C)
N - 507c HNOjlpH < 2 OS U )
N A - Noi applicable
S - 505L H,SO3 with residual CL
ft - TopH > 12.0 S U
7 - To pH > 9 0 S U
8 - V\ ith residual CL? mix sample in 8 oz glass container with 8 drops 25% ascorbic acid
9 • With residual CL, mix sample with 0 0089c sodium thiosulfate
10 • V\ uh residual CL. mix sample w tin 80 mg of sodium thiosutfaie per liter
Holding Times: in days unless noted other* ise
NS • Not Specified
N - Indefinate
1 - Immediate (within 15 minutes 40 CFR 136 Table II)
11 • Determine on-site if possible
12 -360da\s 180 days to extraction plus 180 days to analysis
13 - 28 days 14 days 10 TCLP extraction plus 14 days to analysis (7 days if not preserved following
extraction)
14 - 61 daj-s 14 days to TCLP extraction. 7 days to solvent extraction, 40 days to analysis
15 - Method 8290 specifies 30 days to extraction plus 45 days to analysis
16 - 7 days if not preserved
17 - 47 days 7 days to extraction. 40 days to analysis
EIBSOPQAM A - 3 May 1996
-------
18 - 54 days 14 days 10 exinction. 40 days to analysts
EIBSOPQAM A - 4 May 1996
-------
Shipping Note:
When samples are to be shipped by common carrier or sent through the United States mail, it must compK
with the Departmem of Transportation Hazardous Materials Regulations (49 CFR 172) The person oftennt;
such material for transportation is responsible for ensuring such compliance For the preservation
requirements of 40 CFR. Pan 136. Table II. the Office of Hazardous Materials, Materials Transportation
Bureau. Department of Transportation has determined that the Hazardous Materials Regulations do not appl\
10 the following materials Hydrochloric Acid (HCL) in water solutions at concentrations of 0 045 b> weight
or less (pH about 1 96 or greater). Nunc acid (HN03) in water solutions at concentrations of 0 15£ h> weight
or less (pH aboui I 62 or greaier). Sulfunc acid (H:SO4) in water solutions at concentrations of 0 35SJ b\
weight or less
-------
APPENDIX B
-------
APPENDIX BSTANDARD FIELD CLEANING PROCEDURES
PERFORMANCE OBJECTIVE:
• To remove contaminants of concern from sampling, drilling and other field equipment 10
concentrations Uiat do not impact study objectives using a standard cleaning procedure.
B.I Introduction
Cleaning procedures in this appendix are intended for use by field personnel for cleaning sampling
and other equipment in the field. Emergency field sample container cleaning procedures are also included;
however, they should not be used unless absolutely necessary. Cleaning procedures for use at the Field
Equipment Center (FEC) are in Appendix C
Sampling and field equipment cleaned in accordance with these procedures must meet the minimum
requirements for Data Quality Objectives (DQO) definitive data collection. Alternative field
decontamination procedures may be substituted as outlined in Section 5.12 when samples are to be analyzed
for data uses ai a lower DQO level. Deviations from these procedures should be documented in the
approved study plan, field records, and investigative reports.
These are the materials, methods, and procedures to be used when cleaning sampling and other
equipment in the field.
B. 1.1 Specifications for Cleaning Materials
Specifications for standard cleaning materials referred to in this appendix are as follows:
• Soap shall be a standard brand of phosphate-free laboratory detergent such as Liquinox*. Use
of other detergent must be justified and documented in the field logbooks and inspection or
investigative reports.
• Solvent shall be pesticide-grade isopropanol. Use of a solvent other than pesticide-grade
isopropanol for equipment cleaning purposes must be justified in the study plan. Otherwise its
use must be documented tn field logbooks and inspection or investigation reports.
• Tap water may be used from any municipal water treatment system. Use of an untreated
potable water supply is not an acceptable substitute for tap water.
• Analvte free water (deiomzed water) is tap water that has been treated by passing through a
standard deionizing resin column. At a minimum, the finished water should contain no
delectable heavy metals or other inorganic compounds (i.e., at or above analytical detection
limits) as defined by a standard inductively coupled Argon Plasma Spectrophotometer (ICP) (or
equivalent) scan. Analvte free water obtained by other methods is acceptable, as long as it
meets the above analytical criteria.
E1BSOPQA.M B - I May 1996
-------
• Orpamc/analvte free water is defined as tap water that has been treated with actuated carbon
and deiomzmg units A portable system to produce orgamc/analyte free water under field
conditions is available At a minimum, the finished water must meet the analytical criteria of
analyie free water and should contain no detectable pesticides, herbicides, or extractable organic
compounds, and no volatile organic compounds above minimum detectable levels as determined
by the Region 4 laboratory for a given set of analyses Orgamc/analyie free water obtained b\
other methods is acceptable, as long as it meets the above analytical criteria
• Other solvents may be substituted for a particular purpose if required For example, removal
of concentrated waste materials may require the use of either pesticide-grade hexane or
petroleum ether After the waste material is removed, the equipment must be subjected to the
standard cleaning procedure Because these solvents are not miscible with water, the equipment
must be completely dry prior to use
Solvents, laboratory detergent, and rinse waters used to clean equipment shall not be reused dunnc
field decontamination
B 1 2 Handling and Containers for Cleaning Solutions
Improperly handled cleaning solutions may easily become contaminated. Storage and application
containers must be constructed of the proper materials to ensure their integrity Following are acceptable
materials used for containing the specified cleaning solutions'
• Soap must be kept m clean plastic, metal, or glass containers until used It should be poured
directly from the container during use
• Solvent must be stored m the unopened original containers until used They ma\ be applied
usmc the low pressure nitrogen system fitted with a Teflon* nozzle, or using Teflon* squeeze
bottles
• Tap water ma\ be kepi m clean tanks, hand pressure sprayers, squeeze bottles, or applied
directly from a hose
• Analvte free water must be stored in clean glass, stainless steel, or plastic containers that can
be closed prior to use It can be applied from plastic squeeze bottles
* Organic-analvte free water must be stored m clean glass. Teflon*, or stainless steel containers
prior to use It ma> be applied using Teflon* squeeze bottles, or with the portable system
Noie Hand pump sprayers generalK are noj acceptable storage or application containers for the above
mjierMls i w ith the exception of up u aier) "Dm also applies to stainless steel sprayers All hand sprayers
hd\e internal oil coated gaskets and black rubber seals that may contaminate the solutions
B 1 3 Disposal of Solvent Cleaning Solutions
Procedures for ihe safe handling and disposition of investigation derived waste (IDW). including
used wash water, rinse water, and speni solvents are m Section 5 15
B 1 4 Equipment Contaminated with Concentrated Wastes
Equipment used to collect samples of hazardous materials or toxic wastes or materials from
hazardous waste sites. RCRA facilities, or in-process waste streams should be field cleaned before
returning irom the study Ai a minimum, this should consist of washing with soap and rinsing with tap
DBSOPQAM B.; May 19%
-------
water
More stringent procedures may be required at the discretion of the field investigators
EIBSOPQAM B-3 May 1996
-------
B 1 5 Safet\ Procedures for Field Cleaning Operations
Some of the materials used to implement the cleaning procedures outlined in this appendix can he
harmful if used improperly Caution should be exercised by all field investigators and all applicable safeu
procedures should be followed Ai a minimum, the following precautions should be taken in the field
during these cleaning operations
• Safety glasses with splash shields or goggles, and latex gloves will be worn during all cleaning
operations
• Solvent rinsing operations will be conducted in the open (never in a closed room)
• No eating, smoking, drinking, chewing, or any hand to mouth contact should be permitted
during cleaning operations
B 1 6 Handling of Cleaned Equipment
After field cleaning, equipment should be handled only by personnel wearing clean gloves to
prevent re-contamination In addition, the equipment should be moved away (preferably upwind) from the
cleaning area to prevent recontammation If the equipment is not to be immediately re-used it should be
covered with plastic sheeting or wrapped m aluminum foil to prevent re-comamination The area where
the equipment is kept prior 10 re-use must be free of contaminants
B.2 Field Equipment Cleaning Procedures
Sufficient clean equipment should be transported to the field so that an enure study can be
conducted without the need for field cleaning However, this is not possible for some specialized items
such as ponable power augers (Lutle Beaver*), well drilling rigs, soil coring rigs, and other large pieces
of Held equipment In addition, particular!} during large scale studies, it is not practical or possible to
transpon all of the precleaned field equipmem required imo the field. In these instances, sufficient pre-
cleaned equipment should be transported 10 the field to perform at least one days work The following
procedures are to be utilized when equipmem must be cleaned m the field
B 2 I Specifications for Decontamination Pads
Decontamination pads constructed for field cleaning of sampling and drilling equipment should
meei the following minimum specifications
• The pad should be construcied in an area known or believed to be free of surface
contamination
• The pad should not leak excessive!}
• If possible, the pad should be construcied on a level, paved surface and should facilitate the
removal of wasiewater This may be accomplished by either constructing the pad with one
comer lower than the rest, or b> creating a sump or pit in one corner or along one side Any
sump or pu should also be lined
• Sawhorses or racks constructed to hold equipment while being cleaned should be high enough
EIBSOPQAM B-4 May I996
-------
above ground to prevent equipment from being splashed
EIBSOPQ^M B - 5 May 19%
-------
• Water should be removed from the decontamination pad frequently.
• A temporary pad should be lined with a water impermeable material with no seams within the-
pad This material should be either easily replaced (disposable) or repairable
AI the completion of sue activities, the decontamination pad should be deactivated The pn or
sump should be backfilled with the appropriate material designated by the sue project leader, but only after
all waste/rinse water has been pumped into containers for disposal. No solvent nnsates will be placed in
the pit Solvent nnsates should be collected in separate containers for proper disposal See Section 5 15
of this SOP for proper handling and disposal of these materials If the decontamination pad has leaked
excessively, soil sampling may be required
B 2 2 "Classic Parameter" Sampling Equipment
"Classic Parameters" are analyses such as oxygen demand, nutrients, certain inorganics, sulfide.
flow, measurements, etc For routine operations involving classic parameter analyses, water quality
sampling equipment such as Kemrnerers. buckets, dissolved oxygen dunkers, dredges, etc . may be cleaned
with the sample or analyte-free water between sampling locations. A brush may be used to remove
deposits of material or sediment, if necessary If analyte-free water is samplers should be flushed at the
ne\i sampling location with the substance (water) to be sampled, but before the sample is collected
Flow measuring equipment such as weirs, staff gages, velocity meters, and other stream gaging
equipment may be cleaned with tap water between measuring locations, if necessary
The previous!} described procedures are not to be used for cleaning field equipment to be
used for the collection of samples undergoing trace organic or inorganic constituent analyses.
B 2 3 Sampling Equipment used for the Collection of Trace Organic and Inorganic Compounds
The following procedures are 10 be used for all sampling equipment used to collect routine samples
undergoing trace organic or inorganic constituent analyses
I Clean with tap water and soap using a brush if necessary to remove paniculate matter and
surface films Equipment ma> be steam cleaned (soap and high pressure hot water) as an
alternative to brushing Sampling equipment that is steam cleaned should be placed on racks
or sau horses at least two feet above the floor of the decontamination pad PVC or plastic items
should not be sieam cleaned
2 Rinse thorough!) wiih tap v>ater
3 Rinse thoroughly with analue frer uaicr
4 Rmse thoroughly with solvent Do not solvent rinse PVC or plastic items
5 Rinse thoroughly with orgamc/analyte free water If orgamc/analyte free water is not available.
equipment should be allowed to completely dry Do noj apply a final rinse with analyte water
Orgamc/analyte free water can be generated on-site utilizing the portable system.
6 Remove the equipment from the decontamination area and cover with plastic. Equipment stored
overnight should be wrapped in aluminum foil and covered with clean, unused plastic.
EIBSOPQAM B - 6 May 1996
-------
B 2 -4 Well Sounders or Tapes
1 Wash with soap and up water
2 Rinse with tap water
3 Rinse with analyte free water
B 2 5 Fuliz* Pump Cleaning Procedure
CAUTION - To avoid damaging the Fuliz* pump:
• Never run pump when dry
• Never switch directly from the forward to the reverse mode without pausing in the "OFF"
position
The Fultz* pump should be cleaned prior to use and between each monitoring well The folio wine
procedure is required
1 Pump a sufficient amouni of soapy water through the hose to flush out any residual purge water
2 Using a brush, scrub the exterior of the contaminated hose and pump with soapy water Rinse
the soap from the outside of the hose with up water Rinse the hose with analyte-free water
and recoil onto the spool
3 Pump a sufficient amount of tap water through the hose to flush out all the soapy water
(approximately one gallon)
4 Pump a sufficient amount of analyte-free water through the hose to flush out the tap water, then
purge with the pump in the reverse mode
5 Rinse the outside of the pump housing and hose with analyte-free water (approximately 1/4
gal )
6 Place pump and reel in clean plastic bag
B 2 6 Goulds* Pump Cleaning Procedure
CAUTION - During cleaning always disconnect the pump from the generator.
The Gouldsc pump should be cleaned prior to use and between each monitoring well
The following, procedure is required
1 Using a brush, scrub the exterior of the contaminated hose and pump with soap and tap water
2 Rinse the soap from the outside of the pump and hose with tap water
3 Rinse the tap water residue from the outside of pump and hose with analyte-free water
4 Place the pump and hose in a clean plastic bag
EIBSOPQAM B - 7 May 1996
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B 2 7 Redi-Flo2* Pump
The Redi-Flo2* pump should be cleaned prior to use and between each monitoring well The
following procedure is required
CAUTION - Make sure the pump is not plugged in.
I Using a brush, scrub the exterior of the pump, electrical cord and garden hose with soap and
tap water Do not wet the electrical plug.
2 Rinse with tap water
3 Rinse with analyte free water
4 Place the equipment in a clean plastic bag.
To clean the Redi-Flo2* ball check valve
1 Completely dismantle ball check valve Check for wear and/or corrosion, and replace as
needed
2 Using a brush, scrub all components with soap and tap water.
3 Rinse with analyte free water
4 Reassemble and re-atiach the ball check valve to the Redi-Flo2* pump head
B 2 8 Auiomanc Sampler Tubing
The Silastic* and Tygon* tubing previously used in the automatic samplers may be field cleaned
as follows
I Flush tubing with tap water and soap
2 Rinse rubing thorough!} with up water
3 Rinse tubing with analue free uater
B.3 Dounhole Drilling Equipment
These procedures are to be used for drilling activities involving the collection of soil samples for
trjcc organic and inorganic constituent anal\ses. and for the construction of monitoring wells to be used
lor the collecnon of groundwater samples for trace organic and inorganic constituent analyses
B 3 I Introduction
Cleaning and decontamination of all equipment should occur at a designated area (decontamination
pad) on the sue The decontamination pad should meet the specifications of Section B.2.1
EIBSOPQAM B - 8
May 1996
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Tap water (potable) brouehi on ihe sue for drilling and cleaning purposes should be comaimrd H,
a pre-cleaned tank of sufficient size so that drilling activities can proceed without having to scop and obuin
additional water
A sieam cleaner and/or high pressure hoi water washer capable of generating a pressure of ai least
2500 PS1 and producing hot water and/or steam (200'f plus), with a soap compartmeni. should be
obtained
B 3 2 Preliminary Cleaning and Inspection
The drill rig should be clean of any contaminants that may have been transported from another
hazardous waste site, to minimize the potential for cross-contamination Further, the drill rig itself should
nut serve as a source of contaminants In addition, associated drilling and decontamination equipment udl
construction materials, and equipment handling procedures should meet these minimum specified criteria
• All downhole augenng. drilling, and sampling equipment should be sandblasted before use it
painted, and/or there is a buildup of rust, hard or caked matter, etc , that cannot be removed
by steam cleaning (soap and high pressure hoi water), or wire brushing Sandblasting should
be performed prior 10 arrival on sue, or well away from the decontamination pad and areas 10
be sampled
• Any portion of the drill rig. backhoe. etc , that is over the borehole fkelly bar or mast, backhoe
buckets, drilling platform hoist or chain pulldowns, spindles, cathead, etc ) should be steam
cleaned (soap and high pressure hot water) and wire brushed (as needed) to remove all rust.
soil, and other material which mav have come from other hazardous waste sites before being
brought on sue
• Printing and/or writing on well casing, tremie tubing, etc , should be removed beiore use
Emer> cloth or sand paper can be used to remove the priming and/or wruing Most well
material suppliers can supplv materials wuhout ihe printing and/or wruing if specified when
ordered
• The drill ng and other equipment associated with the drilling and sampling activities should be
inspected to insure that all oils, greases, hydraulic fluids, etc . have been removed and all seals
and gaskets are intact with no fluid leaks
• PVC or plastic materials such as tremie rubes should be inspected Items that cannot be cleaned
are not acceptable and should be discarded
B 3 ? Drill Rig Field Cleaning Procedure
Am portion of the drill rig. backhoe. eic . that is over the borehole (kelly bar or mast, backhoe
buckets, drilling platform, hoisi or chain pulldouns. spindles, cathead, etc ) should be steam cleaned (soap
and hich pressure hot water) between boreholes
EIBSOPQAM B-9 May 1996
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B 3 4 Field Cleaning Procedure for Drilling Equipment
The following is the standard procedure for field cleaning augers, drill stems, rods, tools, and
associated equipment This procedure does not apply to well casings, well screens, or split-spoon samplers
used (o obtain samples for chemical analyses, which should be cleaned as outlined in Section B 2 3
1 Clean with tap water and soap, using a brush if necessary, to remove paniculate matter and
surface films Steam cleaning (high pressure hot water with soap) may be necessar\ to remove
matter that is difficult to remove with the brush. Drilling equipment that is steam cleaned
should be placed on racks or saw horses at least two feet above the floor of the decontamination
pad Hollow-stem augers, drill rods, etc., that are hollow or have holes that transmit water or
drilling fluids, should be cleaned on the inside with vigorous brushing
2 Rinse thoroughly with tap water
3 Remove from the decontamination pad and cover with clean, unused plastic If stored
overnight, the plastic should be secured to ensure that it stays in place.
When there is concern for low level contaminants it may be necessary to clean this equipment
between borehole drilling and/or monitoring well installation using the procedure outlined in Section B.2 3
B.4 Emergency Disposable Sample Container Cleaning
Nev. one-pint or one-quart mason jars may be used to collect samples for analyses of organic
compoui ds and metals in waste and soil samples during an emergency These containers would also be
acceptable on an emergency basis for the collection of water samples for extractable organic compounds.
pesticides and metals analyses These jars cannot be used for the collection of water samples for volatile
organic cc ipuund analyses
The rubber sealing rinc should not be m contact with the jar and aluminum foil should be used.
il possible, i ?iween the jar and the sealing rmc If possible, the jar and aluminum foil should be rinsed
u ith pesticidi crade isopropanol and allowed to air dry before use Several empty bottles and lids should
be submitted > the laboratory as blanks for qualit) control purposes
EIBSOPQAM B - 10 May 1996
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APPENDIX C
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APPENDIX C
FIELD EQUIPMENT CENTER STANDARD CLEANING PROCEDURES
PERFORMANCE OBJECTIVE:
• To remove contaminants of concern from sampling, drilling and other Held equipment
to concentrations that do not impact study objectives using a standard cleaning
procedure
C.I Introduction
Cleaning procedures outlined tn this appendix are intended for use at the Field Equipment Center
(FEC) for cleaning sampling and other field equipment prior to field use These procedures are not
intended to be used in the field Cleaning procedures for use in the field may be found in Appendix B
Sampling and other field equipment cleaned in accordance with these procedures will meet the
minimum requirements for Data Quality Objective (DQO) Definitive Data Collection Alternative cleaning
procedures may be substituted as outlined in Section 5 12 when samples are to be analyzed for data to be
used at a lower DQO level Deviations from these procedures should be documented in the approved study
plan, field records, and investigative reports
C I I Specifications For Cleaning Materials
The specifications for standard cleaning materials referred to in this appendix are as follows
• Soap shall be a standard brand of phosphate-free laboratory detergent such as Liqumox*
• Disinfectant soap shall be a standard brand of disinfectant cleaner
• Solvent shall be pesticide grade isopropanol
• Tap water may be obtained from any spigot at the FEC
• Nitric acid solution (105» shall be made from reagent-grade nitric acid and deiomzed water
• Analvtc free water (deiomzcd water) is tap water that has been treated by passing it through a
standard deiomzmg resin column At a minimum, it should contain no detectable heavy metals
or other inorganic compounds (i e . at or above analytical detection limits) as defined by a
standard Inductively Coupled Argon Plasma Spectrophotometer (ICP) (or equivalent) scan
• Orpanic/analvie free water is defined as tap water that has been treated with activated carbon
and deionizing units Ai a minimum, it must meet the analytical criteria of analyte free water
and should contain no detectable pesticides, herbicides, or extractable organic compounds, and
no volatile organic compounds above minimum detectable levels determined by the Region 4
laboratory for a given set of analyses Orgamc/analyte free water obtained by other methods
is acceptable, as long as it meets the above analytical criteria
EIBSOPQAM C • 1 May 1996
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• Other solvents may be substituted for a particular investigation if needed Pesucide-L'rack
acetone or methanol are acceptable However, it should be noted that if pesticide-grade aceione
is used, the detection of acetone in samples collected with acetone rinsed equipment is
considered suspect Pesticide-grade methanol is much more hazardous to use than either
pesticide-grade acetone or isopropanol, therefore its use is discouraged
Solvents, nitric acid solution, laboratory detergent, and rinse waters used to clean equipment cannot
be reused
C 1 2 Handling and Containers for Cleaning Solutions
Improperly handled cleaning solutions may easily become contaminated. Containers should be
constructed of the proper materials to ensure their integrity Following are the materials to be used for
storing the specified cleaning maienals
• Soap should be kept in clean containers until use. It should be poured direct!) from the
container.
• Disinfectant soap should be kept in clean containers until use. Il should be poured directly from
the container
• Solvents should be stored in the unopened original containers until used Solvents may be
applied using the low pressure nitrogen system fitted with a Teflon* nozzle, or by using
Teflon* squeeze bottles
• Tap water may be kept in clean tanks, hand pressure sprayers, squeeze bottles, or applied
directly from a hose
vte free water should be stored in cleaned containers that can be closed when not being
used li may be applied from squeeze bottles.
• Organic/analvte free water should be stored in cleaned glass. Teflon*, or stainless steel
containers prior to use It ma> be applied using Teflon* squeeze bottles, or directly from the
system
• Nitric acid should be kepi in the glass container it is received in. and placed in squeeze bottles
prior 10 application
C I 3 Disposal of Spent Cleaning Solution^
Procedures for safe handling and disposition of speni cleaning solutions, including washwater, rinse
*;iier. spent acid solutions, and spent solvent.1, are as follows
\\asrmaier
Since equipment is decontaminated before its return 10 the FEC. the washwater may be disposed
in the sanitary dram m the washroom When large equipment (vehicles, augers, etc.) is washed outside.
ii ma> wash onto the ground without recovery of the washwaier.
E1BSOPQAM C - 2 May 1996
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Rmseuaier
Since equipment is decontaminated before its return to the FEC, the nnsewater may be disposed
in the sanitary dram in the washroom When large equipment (vehicles, augers, etc.) is rinsed outside n
may go onio the ground without recovery
Nitric Acid
Nitric acid cleaning solutions are to be diluted to a pH greater than 2.0. and flushed down the
samtarv dram in the washroom If used outdoors, this material should be captured and diluted to a pH
greater than 2 0. and flushed down the sanitary dram in the washroom
Solvent
All solvents used should be captured, properly labeled, and stored on the premises of the FEC until
arrangements for proper disposal are made Used solvents can be classified as either "solvent for
recover\" or "solvent for disposal" Solvent for recovery is that which was used in the standard field
cleaning or FEC cleaning of equipment Solvent used for cleaning badly contaminated equipment
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C 1 6 Initial Processing of Returned Equipment
Field or sampling equipment that needs to be repaired will be identified with a "repair" tag An\
problems encountered with the equipment and specific required repairs shall be noted on this tag. as well
as the date and the initials of the investigator Field equipment or reusable sample containers needing
cleaning or repairs will not be stored with clean equipment, sample tubing, or sample containers
All plastic wrapped equipment, containers, and tubing not used in the field may be placed buck miu
stock after the following precautions are taken
• Soap and hot water rinse plastic containers. Allow to air dry.
• If plastic wrapping leaks after soap/water rinse, remove the equipment and place it into the
standard cleaning process
C.2 Trace Organic and Inorganic Constituent Sampling Equipment
Sampling equipment used to collect samples undergoing trace organic and/or inorganic constituent
analyses should be thoroughly cleaned The following procedures are to be used
C 2 1 Tenon* and Glass
1 Wash equipment thorough!) with soap and hot up water using a brush or scrub pad to remove
an\ paniculate matter or surface Him
2 Rinse equipment thorough!) with hot tap water
3 Rinse equipment with 10 percent nitric acid solution Small and awkward equipment such as
vacuum bortle inserts and well bailer ends may be soaked in the nitric acid solution instead of
being rinsed with n Fresh nitric acid solution should be prepared for each cleaning session
4 Rinse equipment thorough!} vuih anaKte free water
5 Rinse equipment thorough!) with solvent and allow to air dry for at least 24 hours
6 V> rap equipment in one layer of aluminum foil Roll edges of foil into a "tab" to allow for eas\
removal Seal the foil * rapped equipment in plastic and label.
W hen this sampling equipmeni is used to collect samples that contain oil, grease, or other hard to
remove materials, it may be necessary to rinse the equipmeni several limes with pesticide-grade acetone.
hc\ane. or petroleum ether to remove the materials before proceeding with the first step In extreme cases.
n ma> be necessary to steam clean the field equipment before proceeding with Step 1 If the equipment
cjnnnt be cleaned utilizing these procedures n should be discarded
EIBSOPQAM C • 4 May 1996
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C.2.2 Stainless Steel or Steel
1. Wash equipment thoroughly with soap and hot tap water using a brush or scrub pad to remove
any paniculate matter or surface film.
2. Rinse equipment thoroughly with hot tap water.
3. Rinse equipment thoroughly with analyte free water.
4. Rinse equipment thoroughly with solvent and allow to air dry for at least 24 hours.
5. Wrap equipment in one layer of aluminum foil. Roll edges of foil into a "tab" to allow for easy
removal. Seal the foil wrapped equipment in plastic and label.
When this sampling equipment is used to collect samples that contain oil, grease, or other hard to
remove materials, it may be necessary to rinse the equipment several times with pesticide-grade acetone.
hexane. or petroleum ether to remove the materials before proceeding with the first step. In extreme cases,
it may be necessary to steam clean the field equipment before proceeding with Step 1. If the equipment
cannot be cleaned utilizing these procedures, it should be discarded.
C.2.3 Reusable Composite Sample and Organic/Analyte Free Water Containers
These containers will be rinsed with organic/analyte free water and the rinse water will be
submitted to the Region 4 laboratory outlined in Appendix B.2.3. Approximately one percent of all such —**•""
containers cleaned will be subjected to this procedure. Y
»
C.3 Automatic \Vastewaler Sampling Equipment
C.3.1 ISCOE and Other Automatic Samplers
• The exterior and accessible interior (excluding the waterproof timing mechanism) portions of
the automatic samplers will be washed with soap and tap water then rinsed with tap water.
• Desiccant in the flow meters should be checked and replaced, if necessary, each time the
equipment is cleaned
• The face of the timing case mechanism will be cleaned with a clean damp cloth.
• Tubing (sample intake and pump tubing) will be discarded after each use.
• New precleaned, Silastic pump tubing (see Appendix C.4.1) will be installed.
C.3.2 !SCOr 1680, 2700, and 3700 Rotary Funnel, Distributor, and Metal Tube
1. Clean with hot tap water, soap, and a brush.
2. Rinse thoroughly with analyte free water.
EIBSOPQAM C - 5 May 1996
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3 Replace in sampler
EIBSOPQAM C • 6 May 1996
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C 3 3 All Automatic Sampler Headers
1 Disassemble header and using a bottle brush, wash with hot tap water and soap
2 Rinse thoroughly with analyte free water
3 Dry thoroughly, then reassemble header and wrap with aluminum foil
4 Seal in Plastic
C 3 4 Reusable Glass Composue Sample Containers
1 Wash containers thoroughly with hot tap water and laboratory detergent, using a bottle brush
to remove paniculate matter and surface film
2 Rinse containers thoroughly with hot tap water
3 Rinse containers with at least 10 percent nitric acid
4 Rinse containers ihoroughK with tap water
5 Rinse containers thoroughly with analyte free water
6 Rinse twice with solvent and allow to air dry for at leasi 24 hours
7 Cap with aluminum foil or Teflon* film
When these containers are used 10 colleci samples thai contain oil. grease, or other hard to remove
materials, it ma\ be necessan to rinse the containers several times with pesticide-grade acetone, hexane
or petroleum ether to remove the materials before proceeding with Step 1 Any bottles that have a visible
film, scale, or discoloration remaining after this cleaning procedure shall also be discarded
C 3 5 Plastic Reusable Composue Sample Containers (2700 - 5 gal., 3700 - 4 gal )
1 Wash containers thoroughly wuh hot tap water and laboratory detergent, using a bottle brush
10 remove paniculate matter and surface film
2 Rinse containers ihoroughK \uth hoi tap water
3 Rinse containers with at least 10 percent nitric acid
4 Rinse containers thoroughly u nh tap water
5 Rinse containers thoroughly with analyte free water
6 Cap with aluminum foil or Teflon* film
Am plastic composite sample containers that have a visible film, scale, or other discoloration
remaining after this cleaning procedure will be discarded
EIBSOPQAM C - 7 May 1996
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C 3 6 ISCO£ 1680 Glass Sequential Sample Bottles
I Rinse with 10 percent mine acid
2 Rinse thoroughly with tap water
3 Wash in dishwasher at wash cycle, using laboratory detergent cycle, followed b> tap and
analyie free waier rinse cycles
4 Replace bottles m covered, automatic sampler base and cover with aluminum foil for storage
These ISCO® 1680 glass sequential sample bottles are not to be used for collecting samples for
GC/MS (or equivalent) analyses The ISCO1 1680 bottles may be used for collecting samples for GC/MS
(or equivalent) analyses if the cleaning procedures outlined in Section C.3.7 are used.
C 3 7 ISCOC 1680, 2700. and 3700 Glass Sequential Bottles for GC/MS Analyses
1 Rinse with 10 percent nitric acid
2 Rinse thoroughly with lap water
3 Wash in dishwasher at wash cycle, using laboratory detergent cycle, followed by tap and
analyte free water rinse cycles
4 Rinse twice with solvent and allow to air dry for at least 24 hours.
5 Replace in covered, automatic sampler base, cover with aluminum foil for storage and mark
the base as follows "Cleaned for organic analyses "
C 3 8 Bottle Siphons for Composite Containers
Tubing should be rinsed with solvent and dried m the drying oven overnight before use The ends
of the siphon should be capped with aluminum foil and/or Teflon* film for storage The tubing will be
sealed m plastic and labeled The siphon should be flushed with sample thoroughly before use
C 3 9 Reusable Teflon* Composite Mixer Rods
I U ash equipment thorough!) u ith soap and hot tap water using a brush or scrub pad to remove
am paniculate matter or surface film
2 Rinse equipment thorough!) with hot tap water
3 Rinse equipment with at least a 10 percent nitric acid solution.
•4 Rinse equipment thorough!) with tap water
5 Rinse equipment thorough!) with analyte free water
6 Rinse equipment thoroughly with solvent and allow to air dry for at least 24 hours
7 Wrap equipment in one layer of aluminum foil Roll edges of foil into a "tab" to allow for easy
EtBSOPQAM C - 8 May 1996
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removal Seal the foil wrapped equipment in plastic and label.
EIBSOPQAM C - 9 May 1996
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When this sampling equipmeni is used 10 collect samples that contain oil. grease, or other hard u>
remove materials, it may be necessary to rinse the equipment several times with pesticide-grade acetone
hexane. or petroleum ether to remove the materials before proceeding with Step 1. In extreme cases, it ma>
he necessary to steam clean the field equipment before proceeding with Step 1 If the equipment cannoi
be cleaned utilizing these procedures, it should be discarded
C.4 Cleaning Procedures for Tubing
C 4 1 Silasiic* Pump Tubing
The Silasiic* pump tubing in the automatic samplers and peristaltic pumps should be replaced after
each stud\ Afier installation, the exposed ends should be capped with clean, unused aluminum foil
C 4 2 Teflon* Sample Tubing
Use only new Teflon* tubing which has been precleaned as follows for the collection of samples
for trace organic compound or 1CP analyses
1 Teflon* tubing shall be precui in 10. 15 or 25-foot lengths before cleaning
2 Rinse outside of tubing with solvent
3 Flush interior of tubing with solvent
4 Dry overnight in the drying oven
5 Coil Cap ends with aluminum foil \Vrap tubing in one layer of aluminum foil Roll edges
of foil into a "tab" to allow for eas> removal Seal ihe foil wrapped tubing in plastic and label
C 4 3 Stainless Sieel Tubing
1 Vtash vuth soap and hoi tap uaier using a long, narrow, bottle brush
2 Rinse equipment thoroughly with hot tap water
3 Rinse equipmeni thoroughK with anahie free water
4 Rinse equipment thoroughK with solvent and allow to air dry for at least 24 hours
5 Cap ends with aluminum foil U rap rubing in one layer of aluminum foil Roll edges of foil
into a ' tab" to allow, for eas> remma) Seal the foil wrapped tubing in plastic and date
When this sampling equipment is used to collect samples that contain oil, grease, or other hard to
remove materials, it may be necessan to rinse the equipmeni several times with pesticide-grade acetone.
hexanc. or petroleum ether to remove the materials before proceeding with Step 1 If the equipment cannot
be cleaned utilizing ihese procedures, it should be discarded
E1BSOPQAM C - 10 May 1996
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C 4 4 Glass Tubing
New glass tubing should be cleaned as follows
1 Rinse thoroughly with solvent
2 Air dry for at least 24 hours
3 Wrap tubing completely with aluminum foil and seal in plastic (one rube/pack) 10 prevent
contamination during storage
C.5 Cleaning Procedures Tor Miscellaneous Equipment
C 5 1 Well Sounders and Tapes
1 Wash with soap and tap water
2 Rinse with hot tap water
3 Rinse with analyte free water
4 Allow 10 air dry overnight
5 Wrap equipment in aluminum foil (with tab for easy removal) seal in plastic, and date
C 5 2 Fultz* Pump
CAUTION: To avoid damaging the Fultz pump:
• Never run pump when dr\
• Never switch directly from forward 10 reverse mode without pausing in the "OFF" position
Cleaning
1 Pump a sufficient amount of hot soap> water through the hose to flush out any residual purge
water
2 Using a brush or scrub pad. scrub the exterior of the contaminated hose and pump with hot soapy
waier Rinse hose with analyie free water and recoil onto the spool
3 Pump a sufficient amount of up uaier through the hose to flush out soapy water (approximately
one gallon)
4 Pump a sufficient amount of analue-free water through the hose to flush out the tap water, then
empty pump and hose by placing pump in reverse Do not allow pump to run dry
5 Rinse the pump housing and hose with analyie free water
6 Place pump and reel in clean polyethylene bag or wrap in clean polyethylene film Ensure that
EIBSOPQAM C - 11 May 1996
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a complete set of new. rotors, two fuses and a set of cables are attached to the reel
E1BSOPQAM C-12 May 1996
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C 5 3 Goulds* Pump
CAUTION - Never plug the pump in while cleaning.
Cleaning
1 Remove garden hose (if attached), and clean separately.
2 Using a brush or scrub pad. scrub the exterior of the hose, electrical cord and pump with soap
and tap water Do not wet the electrical plug.
3 Rinse with analyte free water
4 Air dry
5 Place pump and hose in clean plastic bag and label
C 5 4 Redi-Flo2* Pump
CAUTION - Make sure that the controller is not plugged in.
CAUTION - Do not wet the controller.
Controller Box Cleaning
1 V, jpe the controller box with a damp cloth Immediately remove any excess water
2 Lei the controller box dry completely
Pump Cleaning
CALTION - Make sure that the pump is not plugged in.
1 Remove garden hose (if attached) and ball check valve Clean these items separately
2 Using a brush or scrub pad scrub the exterior of the electrical cord and pump with soap and tap
water Do not wet the electrical plug
3 Rinse wuh tap water
4 Rinse with analyte free water
5 Completely air dry
6 Place equipment in clean plastic bag
E1BSOPQAM C • 13 May 1996
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To clean the Redi-Fk>2" ball check valve
! Completely dismantle ball check valve Check for wear and/or corrosion, and replace as needed
2 Using a brush, scrub all components with soap and hot tap water
3 Rinse with analyte-free water
4 Completely air dry
5 Reassemble the ball check valve and re-attach to Redi-Flo2* pump head
Note The analyte-free water within the Redi-Flo2« pump head should be changed at the FEC upon return
from the field according to the manufacturer's instructions
C 5 5 Little Beaver*
The engine and power head should be cleaned with a power washer, steam jenny, or hand washed
w, iih a brush using soap to remove oil, grease, and hydraulic fluid from the exterior of the unit Do not use
degreasers Rinse thoroughly with lap water
Auger flights and bits should be cleaned as follows
1 Inspect thoroughly If severe rust, corrosion, paint, or hardened grout is present, the equipment
will require sandblasting prior 10 cleaning
2 Clean with tap water and soap, using a brush if necessary, to remove paniculate matter and
surface films Steam cleaning (high pressure hot water with soap) may be necessary to remove
matter that is difficult to remove with the brush Augers that are steam cleaned should be placed
on racks or saw horses ai least two feet aboveground
3 Rinse thoroughly with tap water
4 Completely air dry Remove and wrap with clean, unused plastic Return to storage
At the direction of the proiect leader or the Quality Assurance Officer, this equipment may be
cleaned as specified in Section C 2 2 prior IP use
C 5 6 Drill Rig. Grout Mixet. and Associated Equipment
• A thorough interior and exterior cleaning of the drill rig is required at the end of each study.
The exterior (including undercarriage) should be washed with soap and tap water and ihen rinsed
vuih tap water The steam jenn> may be used
• The pump and tank on the drill rig should be flushed with tap water until clear, and then drained
• The pump on the grout mixer should be flushed with tap water until clear, then drained
• The grout mixer should be washed with soap and tap water The steam jenny may be used
EIBSOPQAM C - l« May 1996
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Drilling equipment (tools, rods, augers, etc ) should be cleaned as follows
1 Inspect thoroughly If severe rust, corrosion, paint, or hardened grout is present the equipment
may require sandblasting prior to cleaning
2 Clean with tap water and soap, using a brush if necessary, to remove paniculate matter and
surface films Steam cleaning (high pressure hot water with soap) may be necessary to remove
matier thai is difficult to remove with the brush. Drilling equipment that has been sieam cleaned
should be placed on racks or saw horses at least two feet above ground Hollow-stem augers.
drill rods, etc . that are hollow or have holes that transmit water or drilling fluids, should be
cleaned on the inside and outside
3 Rinse thoroughly with tap waier
4 Let completely air dry Remove and cover with clean, unused plastic and label
At the direction of the project leader. Quality Assurance Officer, or drill rig operator, this equipment
may be cleaned as specified in Section C 22 prior to use.
C 5 7 Miscellaneous Sampling and Flow. Measuring Equipment
Flow measuring equipment such as weirs, staff gages, velocity meters, and other stream gaging
equipment, and other miscellaneous sampling equipment shall be washed with soap and hot tap water, rinsed
with hot tap water, rinsed thoroughly with analyte free water, and completely air dried before being stored
This procedure is not to be used for equipment utilized for the collection of samples for trace organic or
inorganic constituent analyses
CSS Field Analytical Equipmeni
Field instruments for in-situ water analysis should be wiped with a clean, damp cloth The probes
on these msiruments (pH. conductivity, DO. etc ). should be rinsed with analyte-free water and air dried
An> desiccant in these instruments should be checked and replaced, if necessary, each time the
equipment is cleaned
C 5 9 ke Chests and Shipping Containers
Ice chests and reusable containers shall be washed with soap (interior and exterior) and rinsed with
uip water and air dried before storage If in the opinion of the field investigators the container is severely
conuiminjieb with concentrated waste or other toxic material, it shall be cleaned as thoroughly as possible,
rendered unusable, and properly disposed
C 5 10 Pressure Field Filtration Apparatus
1 N* ash equipment thoroughly with soap and hot tap water using a brush to remove any paniculate
matter or surface film
2 Rinse equipment thoroughly with hot tap water
3 Rinse equipment with 10 percent nitric acid solution
ELBSOPQAM C • 15 May 1996
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4 Rinse equipment thoroughly with analyte free water
5 Rinse equipment thoroughly with solvent and allow to air dry for at least 24 hours
6 Assemble the apparatus and cap both the pressure inlet and sample discharge lines with aluminum
foil 10 prevent contamination during storage
7 Wrap equipment in one layer of aluminum foil Roll edges of foil into a "tab" to allou for eas\
removal. Seal the foil wrapped equipment in plastic and date.
During steps 1 through 5 as outlined above and immediately after assembling, pressure should be
applied to the apparatus after each rinse step (water and acid) to drive the rinse material through the porous
glass filter holder in the bottom of the apparatus
When this sampling equipment is used to collect samples that contain oil, grease, or other hard to
remove materials, it may be necessary 10 rinse the equipment several times with pesticide-grade acetone.
hexane. or petroleum ether to remove the materials before proceeding with the first step In extreme cases.
it mav be necessary to steam clean the field equipment before proceeding with Step 1 If the equipment
cannot be cleaned utilizing these procedures, it should be discarded
C 5 11 Orcamc/Analyte Free Water Siorage Containers
NOTE: These containers will be used onh for transporting organic/analyse free water.
1 Wash containers thorough!) (interior and exterior) with hot tap water and laboratory detergent.
using a bottle brush to remove paniculate matter and surface film.
2 Rinse containers thorouchK with hot lap water
3 Rinse containers with at least 10 percent nitric acid
4 Rinse containers thorough!) with tap water
5 Rinse containers thoroughK with analyie free water
6 Rinse containers thorouphlv with solvent and allow to air dry for at least 24 hours
7 Cap with aluminum foil or Tenon* film
8 Store in plastic bags
When transporting orgamc/analue free water to the field, use only containers cleaned as specified
above Thorouchlv rinse the interior of the container with orgamc/analyte free water prior to filling. Cap
with one laver of Teflon* film, one layer of aluminum foil, and label the container as "orgamc/analyte free
water and include the date it was prepared Do not store the orgamc/analyte free water at the FEC for more
than three davs
EIBSOPQ^M C • 16 May 1996
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C 5 12 Ponable Solvent Rinse Sysiem
1 Replace Teflon* tubing if necessary Wash nozzle and tubing fittings with hot. soaps water
2 Rinse with analyte-free water
3 Wrap nozzle and tubing ends with aluminum foil
C 5 13 Splash Suits
CAUTION: Splash suits should be inspected for wear or damage. If, after consultation with the
Branch Safety Officer, the suil cannot be repaired, it should be discarded.
1 Wash and brush sun thoroughly inside and out with a brush in hot tap water and soap
2 Rinse suit thoroughly inside and out with tap water.
3 Hang suit up until completely dry.
4 Fold suit and place in clean, clear plastic bag and tap shut. Mark the suit's size on the bag
C 5 14 SCBA Facemasks
CAUTION: Facemasks should be inspected for wear or damage. If, after consultation with the Safet\
Officer, the facemask cannot be repaired, it should be discarded.
1 Wash facemask thorouchK inside and out with hot tap water and disinfectant soap Use only soft
brushes Do not use scouring pads of any type
2 Rinse facemask thoroughly inside and out with tap water
3 Hang facemask up until completely dry
4 Place facemask in plastic bag and return to SCBA case.
C 5 15 Garden Hose
1 Brush exterior uith soap and lap water
2 Rinse with tap water
3 Flush interior with tap water until clear (minimum of one gallon)
4 Lei completely air dry
5 Coil and place in clean plastic bag
EIBSOPQ-U1 C • 17 May 1996
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C 5 16 Ponable Tanks for Tap Water
1 Scrub interior and exterior with soap and tap water
2 Rinse with tap water
3 Lei completely air dry
4 Close
C 5 17 Vehicles
Vehicles utilized by field investigators should be washed (if possible) at the conclusion of each field
trip This should minimize contamination of equipment or samples due to contamination of vehicles
When vehicles are used in conjunction with hazardous waste site inspections, or on studies where
pesticides, herbicides, organic compounds, or other toxic materials are known or suspected to be present.
a thorough interior and exterior cleaning (using soapy tap water) is mandatory at the conclusion of such
investigations It shall be the responsibility of the field investigators to see that this procedure is followed
Personnel involved will use appropriate safety measures
Vehicles shall be equipped with trash bags and/or trash containers to facilitate vehicle cleaning
Field investigators are responsible for keeping field vehicles clean by removing trash and other debris
Contaminated trash and equipment should be kept separate from ordinary trash and should be proper!)
disposed on-site or upon return (Section 5 15)
C.6 Preparation of Disposable Sample Containers
C 6 1 Introduction
No disposable sample container (with the exception of the glass and plastic compositing containers)
ma> be reused All disposable sample containers *ill be stored in their original packing containers When
packages of uncapped sample containers are opened, they will be placed m new plastic garbage bags and
sealed to prevent contamination during storage
Specific precleanmg instructions for disposable sample containers are given in the following sections
C t> 2 Plasiic Containers used for "Classical" Parameters
Plasuc containers used for oxspen demand, nutrients, classical inorganics, and suI fides have no
precleanmg requirement However. onl> new containers may be used
ElBSOPQAM C - 18 May 1996
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C 6 3 Glass Bottles for Semi-Volatile GC/MS Analyies
These procedures are to be used only if the supply of precleaned, certified sample boitk"- i^
disrupted The Quality Assurance Officer will instruct personnel in the proper implementation of thesi-
procedures
If desired, pesticide-grade meihylene chloride may be substituted for pesticide-grade isopropanoi
In addition. 1 1 nitric acid may be substituted for the 10% mine acid solution
When these sample containers are cleaned and prepared, they should be cleaned in standard sized
lots of 100 to facilitate the qualit) control procedures outlined in Section 5 14
1 Wash bottles and jars. Teflon* liners, and caps in hot tap water and soap
2 Rinse three limes with tap water
3 Rinse with 10% nitric acid solution
4 Rinse three times with analyie free water
5 Rinse bottles, jars, and liners (not caps) with solvent
6 Oven dr\ bottles, jars, and liners ai 125°C Allow to cool
7 Place liners in caps and close containers
8 Store in contammani-free area
C 6 4 Glass Bottles for Volatile GC/MS and TOX Analyses
These procedures are to be used onl> if the suppl> of precleaned, certified sample bottles is
disrupted The Qua!it\ Assurance Officer will instruct personnel in the proper implementation of these
procedures
When these sample containers are cleaned and prepared, they should be cleaned in standard sized
lots of 100 to facilitate the qualitx control procedures outlined in Section 5.14
1 VA ash vials, bottles and tars Teflon' liners and sepia, and caps in hot tap water and laboratorv
detergent
2 Rinse all items with analue free «.aier
3 Oxen dry at 125°C and allow to cool
4 Seal vials, bottles, and jars with liners or septa as appropriate and cap
5 Store in a contaminant free area
ElBSOPQ*kM C - 19 May 1996
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C 6 5 Plastic Bottles for ICP Analytes
These procedures are 10 be used only if the supply of precleaned, certified sample bottles i^
disrupted The Qualify Assurance Officer will instruct personnel in the proper implementation of these;
procedures
When these sample containers are cleaned and prepared, they should be cleaned in standard sized
lots of 100 10 facilitate the quality control procedures outlined in Section 5 14
1 Wash bottles and caps in hot tap water with soap.
2 Rinse both with 10% nitric acid solution.
3 Rinse three times with analyte-free water.
4 Invert bottles and dry in contaminant free environment.
5 Cap bottles
6 Store in contaminant free area
E1BSOPQAM C - 20 May 1996
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APPENDIX D
-------
APPENDIX D
SAMPLE SHIPPING PROCEDURES
D.I Introduction
Samples collected during field investigations or in response to a hazardous materials incident
must be classified prior 10 shipment, as either environmental or hazardous materials samples In general.
environmental samples include drinking water, most groundwater and ambient surface water soil
sediment, treated municipal and industrial wasiewater effluent, biological specimens, or any samples not
expected to be contaminated with high levels of hazardous materials.
Samples collected from process wasiewater streams, drums, bulk storage tanks, soil, sediment.
or water samples from areas suspected of being highly contaminated may require shipment as dangerous
goods Regulations for packing, marking, labeling, and shipping of dangerous goods by air transport are
promulgated by the International Air Transport Authority (1ATA), which is equivalent to United Nations
International Civil Aviation Organization (UN/ICAO) (1) Transportation of hazardous materials
(dangerous goods) by EPA personnel is covered by EPA Order 1000. 18 (2)
D.2 Shipment of Dangerous Goods
The project leader is responsible for determining if samples collected during a specific field
investigation meet the definitions for dangerous goods. If a sample is collected of a material that is listed
in the Dangerous Goods List. Section 4 2. 1ATA, then that sample must be identified, packaged, marked.
labeled, and shipped according to the instructions given for that material If the composition of the
collected sample(s) is unknown, and the project leader knows or suspects that it is a regulated material
(dangerous goods), the sample ma\ not be offered for air transport If the composition and properties of
the waste sample or highly contaminated soil, sediment, or water sample are unknown, or only partial!)
known the sample may not be offered for air transport
In addition, the shipment of prepreserved sample containers or bottles of preservatives (e.g .
NaOH pellets. HCL, etc ) which are designated as dangerous goods by 1ATA is regulated Shipment of
nitric acid is forbidden on all aircraft Dangerous goods must not be offered for air transport without
contacting the Division dangerous goods shipment destgnee
D.3 Shipment of Environmental Laboratory Samples
Guidance for the shipment of environmental laboratory samples by personnel is provided in a
memorandum dated March 6. 1981. subiect "Final National Guidance Package for Compliance with
Department of Transportation Regulations in the Shipment of Laboratory Samples" (3) By this
memorandum, the shipment of the following unpreserved samples is not regulated
• Drinking water
• Treated effluent
• Biological specimens
• Sediment
• Water treatment plant sludge
• POTW sludge
EIBSOPQAM D-l May 19%
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In addition, the shipment of the following preserved samples is not regulated, prouded thu-
amount of preservative used does not exceed the amounts found in 40 CFR 136.3 (4) (see Appendix Ai
It is the shippers' (individual signing the air waybill) responsibility to ensure that proper amounis oi
presen auve are used
• Drinking water
• Ambient water
Treated effluent
Biological specimens
• Sediment
• Wastewater treatment plant sludge
• Waier treatment plant sludge
Samples determined by the project leader to be in these categories are to be shipped using the
following protocol, developed jointly between US-EPA, OSHA. and DOT This procedure is documented
in the "Final National Guidance Package for Compliance with Department of Transportation Regulations
in the Shipment of Environmental Laboratory1 Samples" (3)
Untreated wastewater and sludge from POTW's are considered to be "diagnostic specimens" (not
environmental laboratory samples) However, because they are not considered to be etiologic agents
(infectious) they are not restricted and ma\ be shipped using the procedures outlined below
Environmental samples should be packed prior to shipment by air using the following procedures
1 Allow sufficient headspace (ullage) in all bottles (except VOC containers with a septum
seal) 10 compensate for any pressure and temperature changes (approximately 10 percent
of the volume of the container)
2 Be sure the lids on all bottles are light (will not leak)
3 Place bottles in separate and appropriately sized polyethylene bags and seal the bags with
tape (preferably plastic electrical tape) Up to three VOC bottles may be packed in one
Whirl-Pak container
4 Optionally, place three to six VOC vials in a quart metal can and then fill the can with
vermiculite
5 Select a sturdv cooler in pood repair Secure and tape the drain plug with Tiber or duct
tape Line the cooler w iih a large heavy duty plastic bag
6 Place two to four inches of vermiculite tn the bottom of the cooler and then place the
bottles and cans in the cooler with sufficient space to allow for the addition of vermiculite
between the bottles and cans
7 Put "blue ice"
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EIBSOPQAM D - 3 May 1996
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APPENDIX E
-------
APPENDIX E
PUMP OPERATING PROCEDURES
E.I Peristaltic Pump
E I 1 Introduction
When relatively small volumes or water are required for purging and sampling, and the water level
is within the limn of suction (generally around 25 feet vertical separation between the pump and water
surface) peristaltic pumps can be used These pumps are generally small, light-weight, and portable and
are powered by 12-volt batteries
The application of these pumps differs with respect to purging and sampling The following
sections detail the use of peristaltic pumps for both purposes
E 1 2 Purging with a Peristaltic Pump
1 Place a coil of standard-cleaned (Appendix B) Teflon* tubing, equal to the well depth plus
an additional five to ten feei. in a standard cleaned bucket or box which has been lined with
clean plastic sheeting or a garbage bag Enough tubing is needed to run from the ground
surface up to the top of the well casing and back down to the bottom of the well This will
allow for operation of the pump at all possible water level conditions in the well
2 Place one end of the tubing into the vacuum side of the peristaltic pump head Proper sizing
of the Teflon* and Silastic* or Tygon* tubing should allow for a snug fit of the Teflon*
tubing inside the flexible tubing mounted in the pump head
3 Run a short section of tubing (does not have to be Teflon*) from the discharge side of the
pump head to a graduated bucket
4 Place the free end of the coil of Teflon* tubing into the well until the end of the tubing is just
below the top of the water column
5 Secure the Teflon* tubing to the well casing or other secure object using electrician's tape or
other suitable means This will prevent the tubing from being lost in the well should all of
the tubing be deployed and come loose from the pump head
6 Turn on the pump to produce a vacuum on the well side of the pump head and begin the
puree Observe pump direcnon to ensure that a vacuum is being applied to the purge line
If the purge line is being pressurized, either switch the tubing at the pump head or reverse
the polarity of the cables on the pump or on the battery
7 Purge the well according to the criteria described in Section 7.2 of this manual If the
pumping rate exceeds the recovery rate of the well, continue to lower the tubing into the well
several feet at a time, as needed, until the drawdown stabilizes or the well is evacuated to
dryness If the pump is a variable speed peristaltic pump, and the water level in the well is
being drawn down, reduce the speed of the pump in an attempt to stabilize the drawdown
If the well can be purged without evacuating the well to dryness, a sample with greater
integrity can be obtained
EIBSOPQAM E - 1 May 1996
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E1BSOPQAM E - 2 May 1996
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8 For welts which are not evacuated to dry ness, particularly (hose with recovery rates equal m
or very nearly equal 10 the purge rate, there may no: be a complete exchange and removal
of stagnant water in that portion of the water column above the cubing intake For ihi<-
reason. it is important that the tubing intake be placed m the very uppermost ponion of thi:
water column while purging Standard field measurements should frequently be taken during
this process to verify adequacy of the purge (See Section 7 2 for specific details regarding
purge adequacy measurements)
E 1 3 Sampling with a Peristaltic Pump
Flexible tubing used in peristaltic pump heads ts not acceptable for collecting samples for organic
compounds analyses and cannot easily be field cleaned between sampling locations prior to collecting
samples for oUier parameters For these reasons. 11 is necessary to use a vacuum container, placed between
the pump and the well for sample collection with a pensiakic pump. However, if (he flexible pump rubinc
is decontaminated according to Appendix C of (his SOP. samples for analyses of some inorganic
constituents may be collected through the tubing if blanks are collected. This method is detailed in the
following steps
NOTE Samples for volatile organic compound analyses cannot be collected using this method If
samples for VOC analyses are required, they must be collected with a Teflon* or stainless
steel bailer or by other approved methods, such as the straw method The straw method
involves allowing the rubmg to fill, by either lowering it into the water column or filling it
via suction applied by the pump head Upon filling, the tubing is removed from the well and
allowed to drain into the sample vial This is repeated, as necessary', until all vials are filled
I Disconneci the purge rubmc from the pump Make sure the tubing is securely attached 10 the
protective casing or other secure object
2 Insert the rubmg into one of the ferrule nut fittings of a Teflon* vacuum container transfer
cap assembK
3 Place a suitable length of Teflon* tubing berween the remaining transfer cap assembly ferrule
nut fining and the vacuum side of the flexible tubing m the peristaltic pump head SecureK
hand lighten both fittings
J Turn the pump on V ater should begin to collect m the transfer container (typically a 4-luer
or 1-gallon sample containeri within a few minutes If water does not begin to flow into the
container within five minutes, check the transfer cap fittings and make sure the assembly is
tightly attached to the container It may be necessary to tighten the ferrule nuts with a wrench
or pliers to achieve a vacuum in the system, particularly when approaching the maximum
head difference between the pump and water table
5 When the transfer container is nearly full, turn off the pump, remove the transfer cap
assembly, and pour the sample into the appropriate containers Samples to be analyzed for
exiractable organic compounds, metals, and cyanide can be collected using this system
Because the one-gallon (4-luer) containers used by the Branch are rinsed with nitric acid
during cleaning. the\ cannot be used for collecting samples to be analyzed for nitrogen
sensitive parameters
E1BSOPQAM E - 3 May 1996
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6 If additional sample volume is needed, replace the transfer cap assembly, turn the pump on
and collect additional volume The use of Teflon* valves or ball check devices to retain ihc
water column in the sample delivery tubing during the transfer phase, when large volume*-
of sample are required, is acceptable These devices, however, must be constructed so thai
they may be completely disassembled and cleaned according to the procedures in Appendix
C2 1
7 When sampling is completed, all Teflon* tubing should be discarded
E.2 Fultz* Pump
E 2 1 Introduction
The Fultz* pump is a small 24-volt DC submersible pump suitable for purging most 2-mch and
some 4-mch wells and is available in two different diameters, 1.75 inches and 2.5 inches Operating depths
tor these pumps range from approximately 135 feet to 150 feet Maximum pump rates range from approxi-
mately 1 5 gallons per minute, at shallower depths, to less than 0.5 gallon per minute at the maximum
operating depth For a given depth, the 2 5-inch pump has a slightly higher pumping rate, than smaller
diameter pump The pump housing for each pump is constructed of 304 stainless steel and houses a high
efficiency electric motor and Teflon* gears trotors). Water is pulled through a fine-mesh stainless steel
screen on the pump head by the meshing rotors and is positively displaced through the discharge hose
As supplied from the manufacturer, power for the pump is supplied by an internal power pack
comprised of four 6-volt gel cell batteries The manufacturer also offers an external power pack.
containing the same array of batteries as the internal supply, and a 24-volt DC generator as optional power
sources li has been found thai the pumps operate at higher rates and for longer periods of time when
powered either with the generator or with two 12-volt car or motorcycle batteries connected to provide 24
volts
E 2 2 Operation
Control Panel Switch Functions
The following is a list of switch functions found on the control panel of the Fultz* pump
• ON Supplies power from selected power source to pump motor
• OFF Turns pump off
INTERNAL Selects the internal battery array as the power source for the pump
Note Because the external sources are more reliable and provide longer
service, the internal batteries have been removed from all pumps
EXTERNAL Selects an external power source Source must be plugged mio the front
panel at exterior source plug
FORWARD Selects forward operating mode, used to pump water from the source
• REVERSE Selects reverse operating mode, used to empty water from hose through
pump head and to flush silt from pump screen, when clogged
CAUTION: Always turn the power off before changing direction of pump to prevent damage to unit
or fuse failure.
EIBSOPQAM £ • 4 May 1996
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Purging Procedures
The following steps detail the operation of the Fultz* pump when used for purging monitoring
wells This pump is no: used for sampling
1 Select external power source to be used If a generator is used, plug in to external source
jack and place generator as far from the well as possible m the downwind direction If 12-
volt batteries are used, connect batteries with provided cables to provide 24 volts Bridge the
positive posi of one battery to the negative post of the other. Next, place the red clip from
the main supply cable (the long cable which plugs into the face of the control panel of the
pump) on the remaining positive post and place the black clip on the remaining negative post
2 Check pump head to make sure pump and electrical connections are secure
3 Lower pump into well, placing pump head no more than one or two feet below the top of the
water column
4 Turn pump on and make sure REVERSE/FORWARD switch is in FORWARD position If
the polanry of the power connection is reversed, the amp meter will deflect to the left and the
pump will be running opposite of the selected direction Make the appropriate change
5 During normal operating conditions, the pump should pull no more than 1 5 to 2 0 amps
Newl) replaced rotors may temporarily pull slightly more amps. Check amp meter on
control panel to make sure that the pump is operating in this normal range
6 Listen to the pump, as this is an indication of the amount of water over the pump As the
water level is pulled down, the pitch of the sound will increase and become louder If the
water level is pulled down, lower the pump another one or two feet and continue to listen to
the sound of the pump
7 If the water level is rapidh lowered, caution must be observed as the pump is lowered m the
\ icmiry of the bottom of the well In this region, be sure to observe the clarity of the water
and ihe amps being registered on the amp meter If the water becomes extremely rurbid and
ihe amps increase beyond the acceptable range, these are indications that the pump has been
lowered into silt at the bottom of the well If this occurs, the pump should be momentarily
reversed to dislodge the silt from the screen and rotors If more volume is required to fully
evacuate the well under these conditions, a bailer may be a more appropriate choice for the
remainder of the purge
8 After completing the required purge, remove the pump from the well and reverse the motor
10 empty the pump and hose of all contained water The pump should be switched off as soon
as the last water is discharged, since running the pump dry may damage the rotors This
water should be collected with the other purge water and handled appropriately The pump
and wetted portion of the hose may now be decontaminated prior to use at the next sampling
location
EIBSOPQAM E - 5 May 1996
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E 2 3 Tips and Precautions
The following tips and precautions should be observed for best performance and operating
conditions
1 Watch the hose for kinks as the pump is lowered into the well, particularly checking what
remains on the hose frame Kinks will decrease pump performance and will generally
manifest themselves as decreased output with higher amp meter readings Persistent kinked
areas can be repaired by several wraps of duct tape to "round" the hose and provide
reinforcement Badly kinked hose should be "red-tagged" for replacement
2 Before going to the field, the pump's performance should be checked At zero head, a
properly operating Fultz* pump should pump 1.1 to 1.2 gallons per minute If much less
than 1 1 gallons per minute is pumped, the rotors should be replaced and the pump re-
checked Worn rotors do not merely decrease (he pump rate, they also reduce the operating
head of the pump
3 Make sure spare fuses are available The 1.75-inch diameter pump heads require 2 5 amp
fuses The 2.5-inch diameter pump heads require 5 amp fuses
E 2 4 Rotor Replacement
Remove the five screws that hold the pump head on Carefully rotate the pump cover at the wire.
exposing the rotors With needle-nose pliers, grip each rotor by a tooth and pull it out Replace with new
rotors b> pushing them into place with your thumb Be careful not to shave off the sides of the teeth on
the pump body Replace the pump cover and five screws Gently snug the screws into place and back
them off one mm Place the pump in a bucket of water and. while running, gradually tighten the screws
This will wear off any burrs on the rotors and give the best performance
EIBSOPQAM £-6 May 1996
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E 2 5 Trouble Shooting
No Power to Pump
Pump Output Reduced
High Amp Meter Reading
1 Loose connection to
power supply.
2 Water leakage into
motor
1 Hose kinked
2 Rotors worn
3 Intake clogged
4 Power supply low
5 Silt or sediment in
water
1 Pump out of water
2 Silt or sediment in
water
1. Make sure clips on
battery are snug
2 Return to factory
1 Straighten hose
2 Replace rotors
3 Reverse pump
direction to clear
4 Replace batteries
5 If too bad. discontinue
pump use
1 Lower pump into
water column
2 Watch amp reading
If it exceeds the
recommended
operating range,
reverse direction of
pump to clear intake
If this does not work,
discontinue pumping
and use bailer
E.3 Large Diameter Electric Submersible Pumps
E 3 1 Introduction
Pumps included within trm catepon. are an\ of the typical, large diameter (3-inch to 4-mch)
electric submersibles. such as Goulds*. Grunfo<*. or Jacuzzi* These pumps are necessary when large
amount of water must be removed from wells such as deep. 4-mch monitoring wells and drilled or bored
poiable wells
These pumps are generally powered b> 120-vok generators and require a minimum of two persons
lor operation As such, utmost care should be observed to ensure the safe operation of this equipment.
particularly from an electrical hazard standpoint The following sections detail the safety and operation
of these pumps
EIBSOPQAM
E-7
May 1996
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E 3 2 Safety
1 Place the generator on dry ground or plastic sheeting as far as practical from the well, in ihc
down-wind direction, and ground it Several grounding kits consisting of a roll of copper
wire and a grounding rod are available. Wet the ground thoroughly with up water at the
grounding location, if dr>. and drive the grounding rod several feet into the ground
2 Inspect the electrical cord for frays, breaks, exposed wiring, etc.
3 Check the head space of the well for the presence of an explosive atmosphere with a
combustible gas meter
4 With the current tnpod and spool set-up, a minimum of two people are required to place.
retrieve, and operate these pumps safely. If they are used without the aid of the tripod, i.e .
all electrical and suspension lines are spooled separately, at least three people are needed to
successfully lower and raise the pumps.
5 Wear rubber safety boots to insulate against shock hazards.
6 If purge water is not collected, direct the discharge away from the well and generator,
preferably downgradieni of area
7 Make sure that the generator is set to proper voltage.
8 Do not add gasoline or oil to the generator while it is running
9 Carry the generator, gasoline, and oil in a trailer dedicated to this type of equipment Do not
haul this equipment in ihe back of any passenger vehicle or with any sampling equipment or
containers
E 3 3 Pre-loadout Checkout Procedure
I Check the oil and gasoline in generator, filling up as needed Take generator outside and
start it Place a load on the generator, if possible
2 Inspect the pump, and all hose, rope and electrical cord and connections
E 3 J Operation
I Erect tripod over well head and load hose spool Connect pump to steel winch cable. Using
winch crank, lower pump, hose and electrical cord into the well. If no tripod is available.
lower the pump into the well b> hand This will require at least three people, one to lower
pump with the rope, one to feed the hose and cord into the well, maintaining proper tension.
and one to feed rope, hose and electrical cord from can.
NOTE Keep all hose, electrical cord and cable off of the ground at all times Do not allow the
rope, cord, or the hose to scrape or rub on the well casing
2 Place pump five feet belou the top of the water column
E1BSOPQAM E-8 May 1996
-------
Stan generator, then connect power cord from pump.
E1BSOPQAM E - 9 May 1996
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4 After starting pump, closely observe operation to determine if drawdown is occurring in well
If the water level is noi pulled down significantly, keep pump at initial level and continue10
purge If the water level drops, lower the pump to keep up with the drawdown Do not
allow, the pump to run dr>. as this will damage it
E 3 5 Maintenance and Precautions
1 Do not put up wet
2 Empty hose of contaminated water before leaving sampling location Do not bring back hose
with water in it
3 Do not pump dry
4 Do not run generator without checking oil
5 Do not put pump m trailer with generator.
E 3 6 Trouble Shooting
No Power to Pump
Generator Running.
No Pump Output
Sluggish Discharge
1 Loose connections at
pump
2 Cord unplugged at
cenerator
1 Pump out of water
2 Hose collapsed or
kinked
3 Generator output
failing
1 Sediment or other
maienal clogging
screen
2 Kinked hose
1 Check wiring at pump
Repair as needed
(Generator Off)
2 Plug pump back m
1 Lower pump into
water
2 Unkmk hose
3 Put load on generator
and check output or
check voltage output
meter
1 Remove material from
screen.
2 Unkmk hose
EIBSOPQAM
E- 10
May 1996
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E.4 QED* Bladder and Purge Pumps
E 4 1 Introduction
Several QED' bladder pumps and purge pumps (no bladder) which can be used for purging
monitoring wells are available Bladder pumps have a very low efficiency when used near the top of the
water column and will generally not purge more than 0.5 gallon per minute The purge pump, however
can achieve pump rates of several gallons per minute in these situations The efficiency of the bladder
pumps is restricted by the rigid Teflon* bladder, which requires significant hydrostatic head for rapid and
complete filling The purge pump, having no bladder, fills much faster under the same conditions
Both pumps operate by cycling a pressurized gas on and off in a discharge and refill cycle The
gas. usualK atmospheric air, is pressurized and regulated by a compressor/regulator combination
(controller), which can consist of either a small, battery powered unit, capable of providing pressure to
operate the bladder pump at a depth of approximately 75 feet, or a larger, gasoline powered unit that will
allow operation at depths of over 150 feet
£42 Operation - Bladder Pump
1 Connect air suppl\ hose to "pump supply" connection on controller and to brass air
connection on hose reel can
2 Lower pump into well and place top of pump several feet below the top of the water column
3 Turn on the compressor If the gasoline powered compressor is used, place as far from the
uell as possible, in the down wind direction
4 Adjust the timing of the discharge and refill cycles until maximum flow is achieved
5 Lower pump, as necessarj . if water level is reduced in well
E 4 3 Operation - Purge Pump
1 Connect air suppl> hose to 'pump supply" connection on controller and connection on top
of pump Observe flow direction arrow on purge pump exhaust adapter The arrow must
point in the direction of air flow from the controller to the pump
2 Attach adequate length of standard garden hose to hose fitting at lop of pump
3 Lower pump, air hose and garden hose into water column until top of pump is several feel
below iop of water column
4 Follow Steps 3 through 5 above
ElBSOPQAM E-M May 1996
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E 4 -4 Trouble Shooting
Compressor running.
no pressure on discharge cvcle
Compressor running .
pressure low.
no water discharged
1 Air supply fitungs
loose
2 Bladder is perforated
3 Exhaust adapter
installed in wrong
direction.
1 Obstruction in ball
check assembly
allowing water to be
pushed out of pump at
check
2 Air supply fittings
loose
1 Check all fittings and
tighten
2. Replace bladder
3 Remove adapter and
replace in correct
orientation
4 Remove obstruction
5. Check all fitungs
E.5 Small Diameter Electric Submersible Pumps
E 5 1 Introduction
Included within this category is the Grundfos Redi-Flo2 small diameter electric submersible pump
With a diameter of approximate!) 1 75 inches, it is designed to be used in 2-inch diameter and larger wells
(Note If used in am well larger than 4-mch diameter, this pump must be equipped with a coolmc shroud
io prevent the pump from overheating If this condition occurs, internal sensors will send a shut-off signal
to the controller and the pump will not be operable until it cools to a temperature within the operatmc
range» The Redi-Flo2 is a variable speed pump capable of providing pump rates from less than 100
ml/minute 10 in excess of 8 gallons per minute
The pump, depending on the controller being used, operates with either 115v or 220v power The
pump rate is controlled b\ adjusting the frequenc> of the current going to the pump motor li is a light-
weight pump and can be easily handled b> one person when lowering, bui two people are generally needed
xvhen remn\ ing the pump, one to pull and another 10 reel in the hose and power lead
E 5 2 Safet\
Place the generaior on dn ground or plastic sheeting as far as practical from the well, in the
down-wind direction, and ground it Several grounding kits consisting of a roll of copper
wire and a grounding rod are available Wet the ground thoroughly with tap water at the
grounding location, if dry. and drive the grounding rod several feet into the ground
Inspect the electrical extension cord, as well as the lead to the pump, for frays, breaks.
exposed wiring, etc
Check the head space of the well for the presence of an explosive atmosphere with a
combustible gas meter
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May 1996
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4 Wear rubber boots 10 msulaie against shock hazards
5 If purge water is not collected, direct the discharge away from the well and generator
preferably downgradiem of the area
6 Make sure that the generator is set to the proper voltage
7 Do not add gasoline or oil 10 the generator while it is running
8 Carry the generator, gasoline, and oil in a trailer dedicated to this type of equipment Do not
haul this equipment in the back of any passenger vehicle or with any sampling equipmem or
containers.
E 5 3 Pre-loadoul Checkout Procedures
1 Check the oil and gasoline in the generator, making sure that there is enough gasoline m test
the generator prior 10 loading onto the trailer Take the generator outside and start Place
a load on the generator, if possible
2 Inspect the pump and all hoses, rope, and electrical cord and connections In particular, open
the water reservoir on the bottom of the pump and check to make sure that it is full of water
If not. using the syringe in the controller case, top the reservoir off with orgamc/analyte-free
water Return the pump to its operating vertical position and shake Re-open the reservoir
and add additional water, if needed, to top it off a second time
E 5 4 Operation
1 Place the pump, the controller, and enough hose for the measured well depth on plastic
sheeting next to the well Set the generator in a dry. safe location downwind of the well, but
do not plug the cord from the controller into the generator
2 After checking the head space of the well for safety, lower the pump, power lead, and hose
into the well, placing the pump approximately five feet into the water column
3 Start the generator, jjieji connect the power cord from the pump Make sure the proper
voltage has been selected
4 After suning the pump. closeU observe operation to determine if drawdown is occurring in
the well If the water le*el is not pulled down, raise the pump in the water column one to
two feet from the top of the waier column and continue to purge If the water level drops,
however, lower the pump to keep up with the drawdown Do not allow the pump to run dry.
This condition will create a thermal overload and shut the pump down. While this may not
necessarily damage the pump, n will create delays in sampling.
E1BSOPQAM E - 13 May 1996
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E 5 6 Maintenance and Precautions
1 Empty the hose of contaminated water before leaving the sampling location Do not brim:
the hose back to the FEC if n contains purge water from a site
2 Field clean the pump before leaving the sampling location (see Appendix B)
3 Do not run the generator without first checking the oil
4. Do not put the pump in the trailer with the generator.
5 If the pump is equipped with a check valve or back flow preventer, periodically check this
device to make sure that n is operating This is a common place for debris or other material
to accumulate and interfere with the proper operation of the device.
E 5 7 Trouble Shooting
Generator Running.
No Pump Output
1 Loose connection at
pump.
2 Cord unplugged at
cenerator
3 Over voltage on
controller display
4 Pump out of water
5 Hose collapsed or
kinked
6 Pump will not run or
shuts down with
thermal overload
signal
1 . Check wiring at pump
Repair as needed
(Generator off ' )
2. Plug pump back in
3 Adjust generator
output/ idle speed.
allow generator more
warm-up time
4 Lower pump into
water
5. link ink hose
6 Open cooling water
reservoir and check
cooling water Add
additional
orgamc/analyie-free
water to cooling water
reservoir
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May 1996
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APPENDIX F
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APPENDIX F
REGIONAL TECHNICAL SUPPORT FOR CRIMINAL INVESTIGATIONSEPA REGION 4
The Division provides technical support to the Region 4, Office of Criminal Enforcemeni. Criminal
Investigations Division (CID), for those investigations requiring the collection of samples laburau>r\
analyses, or technical information These procedures address how technical support is requested b\ CID
and provided by the Division Detailed technical procedures will be referenced to the various Standard
Operating Procedures and Quality Assurance Manuals utilized by the Division
The primary objectives of support for criminal investigations are to provide accurate, complete
admissible, and defensible reports and data for case development and subsequent legal proceedings
F.I Technical Assistance Required bj CID
The CID under the direction of a Special Ageni-m-Charge (SAIC) conducts criminal investigations
in Region 4 pursuant to Federal environmental laws and regulations The technical assistance requirements
for criminal cases vary from investigation to investigation To assist the SAIC in identifying the type and
scope of technical assistance required, a Technical Coordinator position has been established m the
Regional Office The Technical Coordinator's primary function is to provide technical advice to ihe SAIC
and Case Agents It is the responsibilit> of the Technical Coordinator to assure that requests for technical
support are directed to the appropriate Regional Program and Divisional offices After a decision has been
made by the SAIC to inmate a criminal imesncanon. the Technical Coordinator will discuss the case with
the Division Director or his designated represenianve The Division Director in consultation and with the
concurrence of the Deputy Regional Administrator (DRA) will decide whether technical support will be
pro\ ided b> the Division
Following a decision that technical suppon will be provided by the Division, the SAIC wilt prepare
a written request addressed through the DRA 10 the Division Director Copies of the request will be routed
id the appropriate Regional program offices
Prior 10 conducting the investigation, the Technical Coordinator will discuss the case with Division
personnel, and will inform the Case Agent of am technical requirements that may influence project
planning Also, it is the responsibility of the Technical Coordinator to inform Division personnel of the
presence of am known situations that uould pose health risks or otherwise interfere with their operations
The Technical Coordinator in consultation with the Case Agent will discuss with Division personnel the
progress or scheduled analyses and the potential need for additional analyses. Information regarding the
need to alter work schedules so as to meet changing Grand Jury or Federal Court dates will be transmitted
immediatelv from the Technical Coordinator to the Division When work schedules must be delayed, the
technical reasons for the dela\ will be communicated from the Technical Coordinator to the Case Agent
Ijpon completion of analyses and report preparation and. prior to presentation of the results to a
Grand Jur\ or Federal Court, the Technical Coordinator will arrange for an audit and inventory of
evidence and files in the Division s possession A copy of the inventory will be provided 10 the Case
Agent, to be used in selecting and preparing trial exhibits
EIBSOPQAM F - I May 1996
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F.2 Project Requests
All requests for support for criminal investigations shall originate with the CID in the Regional
Office Am information obtained by Division staff regarding potential criminal activity shall be
immediately referred to the Region 4 SAIC Direct requests from any other Federal agency. Slate agenc\
or local agency shall be referred to the Region 4 SAIC for appropriate action
Prior to an official request from CID, an informal contact shall be made with the Division Director
or the appropriate Division Branch or Section Chief concerning the availability of resources and expertise
necessary for providing (he requested technical support, If support can be provided, the SAIC shall
prepare an official request to the Division Director, through the DRA (with copies to the appropriate
Branch) or Section Chief In routine criminal investigations when priorities prohibit an immediate
response, the RA/DRA will determine an appropriate course of action. If the RA/DRA determines thai
providing the requested technical support will be in the best interest of the Region, the support will be
provided and adjustments will be made 10 other commitments. Technical support may begin immediate!;,
after receiving concurrence from the RA/DRA The SAIC is responsibile for notifying appropriate
regional organizational units, e g . Office Directors, Division Directors, etc., of potential or on-going
investigations receiving technical assistance from the Division or the technical divisions at NEIC
All emergency requests shall be handled expeditiously In such instances, the requested assistance
may be provided immediately upon being notified by the SAIC that verbal approval has been obtained from
the DRA However, all such requests shall be followed by a written request from the SAIC, through the
DRA to the Division Director
F.3 Project Coordination
Once the decision has been made to provide technical support, the Division Director or the Depim
Director shall assign the project to the appropriate Branch/Section for assignment of a project leader The
proieu leader will be responsible for coordinating with the Case Agent to obtain necessary background
information to determine logistical requirements, skill needs, laboratory' support, etc . The project leader
will coordinate all necessary activities with ORC. DOJ. FBI. trial attorney, etc. at the direction of the Case
Aceni
The protect leader shall discuss the technical and workload requirements with their immediate
supervisor A core team shall then be selected which will conduct the study and/or coordinate analytical
support When required, additional staff will be assigned from other Sections or Branches with the
approval of the appropriate Branch Chief or Division Director Once a core team has been selected, initial
planning for the investigation shall begin under the direction of the Project Leader and in concert with the
Case Acent and with the prosecutors if the> are already involved in the matter.
F.4 Project Planning
After the appropriate or available background material has been obtained, specific assignments will
be given to each member of the core team for development of a study plan. Concurrently, the Project
Leader shall discuss analytical requirements and time-frames with local laboratory personnel The study
plan and sue-safer, plan shall be assembled under the direction of the Project Leader and submitted to the
core team, appropriate management, and Case Agent for review and concurrence. The time-frame for
receiving comments will depend upon the urgency of the investigation, but in no cases should exceed 10
EIBSOPQAM F • 2 May 1996
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working days Dunne emergencies an investigation may be conducted without the preparation of d deunoJ
stud> plan However, during these situations, a memorandum shall be prepared by the Project Leaner
briefly describing the technical work to be accomplished and stating that the investigation will stricth
conform 10 appropriate Standard Operating Procedures and Quality Assurance Manuals
A final study plan will be prepared once all appropriate comments are received by the Projeci
Leader In general, these study plans should contain the following elements However, upon advice of
the Case Agem. the comem and format of any study plan may be substantially changed to meet the need?.
of the particular investigation
• Introduction -- a brief history, a statement of the problem to be investigated and what
specific laws may have been violated.
• Objectives -- a statement as to what the investigation is to accomplish and how the
information is to be used
• Scope -- a definition of the limits of the study
• Stud\ Procedures -- the specific plan to collect the required information (not field
methodology)
• Analytical Requirements -- an estimate of the number of samples to be collected, required
analyses and which laboratory(s) will analyze the samples.
• Lopistics -- an estimate of manpower requirements and a general description of specific
functions of project personnel, special equipment, use of mobile laboratories, etc
• Time Schedule -- a statement outlining when the study will be conducted, analytical results
will be available, the drah report will be written, and the final report will be completed
• Methodology -• specific field techniques to be employed A statement that the techniques
in the Division s Standard Operating Procedures and Quality Assurance Manuals will be
employed shall be included The use of any techniques not included in the Standard
Operating Procedures and Qualu\ Assurance Manuals shall be thoroughly justified and
must produce e\ idence which can withstand objections by the defense
• Safet\ Plan -- a safen connnpenc) plan will be included
F.5 Field Investigation
The field investigation will be conducted under the direct supervision of the project leader and the
central supervision of the Case Agent responsible for the criminal investigation All of the objectives set
forth in the stud} plan should be mei as well as any on-scene changes or additional activities requested by
the Case Agem The project leader and the Sue Safer)1 Officer (SSO) shall have responsibility for
enforcing the provisions of the safety plan The study will be conducted conforming to the requirements
and objectives of the study plan and appropriate Standard Operating Procedures and Quality Assurance
Manuals Am deviations from the study plan or the appropriate Standard Operating Procedures and
Quality Assurance Manuals must be approved and documented by the project leader The deviations must
produce evidence which can withstand objections b'y the defense
ElBSOPQAM F • 3 May 1996
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EIBSOPQAM F • 4 May 1996
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Dunne the field stud}, the proieci leader or designee is responsible for seeing thai all chdin-o;
custod} and quality control procedures for sampling, flow monitoring, field analyses, record-keepmi: ttt
are followed However, the field personnel must understand and follow the chain-of-custoch and qujht\
control procedures relative to their assignments Following completion of the field activities the Pruieit
Leader or designee shall accouni for all field documentation, such as field logbooks, sample tags and
cham-of-custody records, and verify thai they are complete Sample tags will remain on the sample
containers in the custody of the local laboratory until relinquished to the court or final disposition of the
case
F.6 Laboratory Support
Upon delivery of samples to the local laboratory, the samples shall be immediately transferred VM
cham-of-custody procedures, from the Project Leader or designee to the laboratory sample custodian or
designee After receipt of samples, the laboratory sample custodian shall immediately transport the samples
to the sample cusuxh room The laboratory sample custodian shall document the condition of the samples
and verif) the uniformity of information on the sample tags and cham-of-custody records prior to placmc
the sample tags in the sample custod> room All sample handling, sample preparation, and analyses shall
be m sinci conformance with the appropriate Standard Operating Procedures and Qualn\ Assurance
Manual
The laboratory coordmaior shall notify the Project Leader as results become available Final
analytical data shall be reported directlv to the Project Leader after all QA/QC procedures have been
completed Any analytical problems or de\ lanons concerning holding times, analytical procedures, etc
shall be reported to the Project Leader When requested by the Case Agent, this information will be
documented in a memorandum stamped "CONFIDENTIAL", and transmitted to the Project Leader.
Technical Coordinator, and Case Agent
F.7 Final Report
The proiect leader is responsible for preparing a final investigative report A draft report shall be
prepared for internal review b> the core team members and the Case Agent The draft report may also
be reviewed b\ other appropriate staff, i e . supervisors and technical experts All draft reports shall be
destroyed upon completion of a final report
A final investigative report will be prepared by the projeci leader This report shall contain factual
information and observations but shall not contain conclusions, recommendations, or personal opinions
At the request of the Case Agent a memorandum will be prepared containing conclusions.
recommendations, or personal opinions Uhen this is done, the memorandum will be stamped
CONFIDENTIAL' on each pace and delivered to the Case Agent The final reports) shall be delivered
to the Case Agent who shall be responsible for us ultimate distribution
F.S Document Control
The core team members are responsible for the initial collection and maintenance of all documents,
records, and evidence obtained during the field investigation As required by the project leader, all
documents, records and evidence obtained during the field investigation shall be delivered to the project
leader who shall immediately consiruct an inventor) of them If requested, the projeci leader will deliver
EIBSOPQAM F . 5
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all such records to the Case Agent
EIBSOPQAM F - 6 May 1996
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All original analytical data and supporting documentation, e.g.. chromatograms. mass spears
QA/QC records, calculations, etc . shall be maintained by the local laboratory according to their Standard
Operating Procedures and Quality Assurance Manual If requested, copies of all records shall be prm ided
10 the Case Agent Dissemination of such records shall only occur under Federal court order, as direcied
b\ DOJ. or as directed by the prosecuting attorney Laboratory personnel shall construct a project file of
all laboratory data and supporting documentation immediately after completing analyses and reporting of
data to the project leader An inventory of that file will be prepared and furnished to the Project Leader
and the Case Agent
All documents, records, evidence, etc retained will be maintained in a locked filing cabinet or a
secure area
F.9 Sample Disposal
All excess samples and/or sample containers shall be maintained in the sample custody room until
written authorization for sample disposal is received from the Case Agent. Because of lack of space in the
sample custody room, the Case Ageni shall expeditiously inform the laboratory when samples can be
disposed Sample disposal procedures shall be as described in the appropriate Standard Operating
Procedures and Qualit\ Assurance Manual
OBSOPQAM F - 7 May 1996
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APPENDIX G
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