Environmental Investigations

Standard Operating Procedures

and

Quality Assurance Manual

NOVEMBER 2001

U.S. Environmental Protection Agency

Region 4

980 College Station Road

Athens, Georgia 30605-2720

www.epa.gov/region4/sesd/eisopqam/eisopqam.html

**(706) 355-8603**
EISOPQAM

TABLE of CONTENTS

EISOPQAM ToC - i November 2001

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 - 1

2.3 Civil Enforcement Investigations and Studies . . . . . . . . . . . . . . . . . . . . . . . . . . 2 - 2

2.3.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 - 2

2.3.2 Facility Entry . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 - 3

2.3.3 Unreasonable Search and Seizure . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 - 4

2.3.4 Requesting Information . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 - 5

2.3.5 Photographs . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 - 5

2.3.6 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

2.5.2 CWA Inspection Types . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 - 7

2.5.3 Study Plans . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 -09

2.5.4 NPDES Compliance Inspection Reports . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 -10

2.6 Superfund Investigations, Technical Assistance, and Overview Activities . . 2 -11

2.6.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 -11

2.6.2 Superfund Investigation Types . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 -11

2.6.3 Planning for Field Investigative Support . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 -11

2.6.4 Requests for Superfund Studies . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 -12

2.6.5 Investigation Study Plans . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 -12

2.6.6 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

2.7.4 Requests for RCRA Studies . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 -15

2.7.5 Investigation Study Plans . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 -15

2.7.6 Investigation Reports . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 -15

2.8 Underground Storage Tank (UST) Investigations . . . . . . . . . . . . . . . . . . . . . . 2 -16

2.8.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 -16

2.8.2 Investigation Study Plans . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 -17

2.8.3 Investigation Reports . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 -17

2.9 Underground Injection Control (UIC) Investigations . . . . . . . . . . . . . . . . . . . 2 -18

2.9.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 -18

2.9.2 Investigation Study Plans . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 -18

2.9.3 Investigation Reports . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2 -19

2.10 Ambient Air Monitoring Evaluations and Audits . . . . . . . . . . . . . . . . . . . . . . 2 -19
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EISOPQAM ToC - ii November 2001

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 -21

Table 2.10.2 - Population Levels for which NAMS Monitoring of 

Pollutants other than PM10 and SO2 is Required .......................... 2 -22

Table 2.10.3 - Summary of Spatial Scales Usually Needed for SLAMS & NAMS 2 -22

Table 2.10.4 - Summary of Probe Siting Criteria ......................... 2 -24

Table 2.10.5 - Minimum Distance between Sampling Probe and Roadways .... 2 -25

2.10.3 State and Local QA Plan Reviews ................................... 2 -26

2.10.4 Performance Audits .............................................. 2 -26

2.10.5 Air Monitoring Technical System Audit ............................. 2 -28

2.10.6 National Performance Audit Program ............................... 2 -29

2.10.7 PM2.5Federal Reference Method (FRM) Performance Audit Program (PEP).. 2 -30

2.11 References ....................................................... 2 -32

Exhibit 2.1 - Hazardous Waste Field Overview Checklist .................. 2 -33

Exhibit 2.2 - State Contractor Overview Checklist ........................ 2 -48

Exhibit 2.3 - State Program Evaluation - Hazardous Waste Field Activities .... 2 -51

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, Digital, Image, and Video 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

3.3.2 Sample Custody ................................................... 3 - 4

3.3.3 Documentation of Chain-of-Custody ................................... 3 - 5

3.3.4 Transfer of Custody with Shipment .................................... 3 - 6

3.4 Receipt for Samples Form (CERCLA/RCRA/TSCA) .................... 3 - 7

3.4.1 Introduction ....................................................... 3 - 7

3.4.2 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 - Chain-of Custody Form ................................... 3 -11

Figure 3-2 - Media Codes ........................................... 3 -12

Figure 3-3 - Sample Tag ............................................ 3 -13

Figure 3-4 - Receipt for Samples Form ................................. 3 -14

Figure 3-5- EPA Custody Seal ....................................... 3 -15

SECTION 4 - Branch Safety Protocols ........................................ 4 - 1
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EISOPQAM ToC - iii November 2001

4.1 Introduction ...................................................... 4 - 1

4.2 Hazard Communication Procedure ................................... 4 - 2

4.2.1 Introduction ....................................................... 4 - 2

4.2.2 Scope ............................................................ 4 - 2

4.2.3 Labels and Other Forms of Warnings ................................... 4 - 2

4.2.4 Material Safety Data Sheets (MSDSs) .................................. 4 - 3

4.2.5 The Hazard Chemical Inventory ....................................... 4 - 4

4.3 Safety Protocols ................................................... 4 - 5

4.3.1 Site Safety Officer Duties ............................................ 4 - 5

4.3.2 Safety Equipment .................................................. 4 - 6

4.3.3 OSHA Confined Space Entry ......................................... 4 - 6

4.3.4 Entry into Enclosed Areas ............................................ 4 - 6

4.3.5 Training Status Tracking System ...................................... 4 - 7

4.3.6 Site 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

4.3.7 Boating Operations ................................................ 4 -27

Exhibit 4.2 - Float Plan ............................................ 4 -29

4.3.8 Field Procedures for Handling Pathogenic Samples ....................... 4 -30

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

5.3.2 Representative Sampling . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 - 5

5.3.3 Stratification and Heterogeneous Wastes . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 - 5

5.3.4 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 - 7

5.3.9 Stratified Random Sampling . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 - 7

5.3.10 Systematic Grid Sampling . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 - 7

5.3.11 Adaptive Cluster 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, Site Survey, and Site History . . . . . . . . . . . . . . . . . . . . 5 - 9

5.5.2 Data Quality Objectives (DQOs) . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 - 9

5.5.3 Authoritative Designs for Soil Investigations . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 - 9

5.5.4 Systematic Grid Sampling Designs for Soil Investigations . . . . . . . . . . . . . . . . . 5 -10

5.6 Ground Water Sampling Designs . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -14

5.6.1 Single Source Iterative Programs . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -14
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EISOPQAM ToC - iv November 2001

5.6.2 Multiple-Source Area Grided Programs . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -15

5.6.3 Typical Ground Water Screening Devices . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -15

5.7 Surface Water and Sediment Sampling Designs . . . . . . . . . . . . . . . . . . . . . . . 5 -16

5.7.1 Sampling Site Selection . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -16

5.7.2 Rivers, Streams, and Creeks . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -17

5.7.3 Lakes, Ponds, and Impoundments . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -19

5.7.4 Estuarine Waters . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -20

5.7.5 Control Stations . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -21

5.8 Waste Sampling Designs . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -21

5.8.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -21

5.8.2 Waste Investigation Objectives . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -22

5.8.3 Considerations for Waste Sampling Designs . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -22

5.8.4 Waste Sampling Equipment . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -23

5.8.5 Field Screening . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -23

Figure 5-1 - RCRA Waste Characterization Flow Chart . . . . . . . . . . . . . . . . . . . 5 -25

5.9 Wastewater Sampling Designs . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -26

5.10 UST and UIC Sampling Designs . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -27

5.11 Air Toxics Monitoring Designs . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -27

5.12 Data Quality Objectives . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -28

5.13 Specific Sample Collection Quality Control Procedures . . . . . . . . . . . . . . . . . 5 -31

5.13.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -31

5.13.2 Experience Requirements . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -31

5.13.3 Traceability Requirements . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -31

5.13.4 Chain-of-Custody . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -32

5.13.5 Sampling Equipment Construction Material . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -32

5.13.6 Sample Preservation . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -32

5.13.7 Special Precautions for Trace Contaminant Sampling . . . . . . . . . . . . . . . . . . . . . 5 -32

5.13.8 Sample Handling and Mixing . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -33

5.13.9 Special Handling of Samples for Volatile Organic Compounds (VOCs) Analysis 5 -34

5.13.10 Estimating Variability . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -34

5.13.11 Special Quality Control Procedures for Water Samples for Extractable

Organic Compounds, Pesticides, or Herbicides Analysis (Matrix Duplicate) . . . 5 -36

5.13.12 Special Quality Control Procedures for EPA Contract Laboratories . . . . . . . . . . 5 -36

5.13.13 Special Quality Control Procedures for Dioxins and Furans . . . . . . . . . . . . . . . . 5 -37

5.14 Internal Quality Control Procedures . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -37

5.14.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -37

5.14.2 Traceability Requirements . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -37

5.14.3 Specific Quality Control Checks . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -38

5.15 Investigation Derived Waste (IDW) . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -38

5.15.1 Types of IDW . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -38

5.15.2 Management of Non-Hazardous IDW . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -39

5.15.3 Management of Hazardous IDW . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -39

Table 5.15.1 - Disposal of IDW . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -41

5.16 References . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 5 -42
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EISOPQAM ToC - v November 2001

SECTION 6 - Design and Installation of Monitoring Wells ....................... 6 - 1

6.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 - 1

6.2 Permanent Monitoring Wells - Design Considerations . . . . . . . . . . . . . . . . . . . 6 - 1

6.3 Drilling Methods . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 - 2

6.3.1 Hollow-Stem Auger . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 - 2

6.3.2 Solid-Stem Auger . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 - 2

6.3.3 Sonic Methods . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 - 3

6.3.4 Rotary Methods . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 - 3

6.3.5 Other Methods . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 - 4

6.4 Borehole Construction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 - 5

6.4.1 Annular Space . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 - 5

6.4.2 Overdrilling the Borehole . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 - 5

6.4.3 Filter Pack Placement . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 - 5

6.4.4 Filter Pack Seal-Bentonite Pellet Seal (Plug) . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 - 5

6.4.5 Grouting the Annular Space . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 - 6

6.4.6 Above Ground Riser Pipe and Outer Protective Casing . . . . . . . . . . . . . . . . . . . . . 6 - 6

6.4.7 Concrete Surface Pad . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 - 7

6.4.8 Surface Protection-Bumper Guards . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 - 7

6.5 Construction Techniques . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 - 7

6.5.1 Well Installation . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 - 7

6.5.2 Double Cased Wells . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 - 9

6.6 Well Construction Materials . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 -10

6.6.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 -10

6.6.2 Well Screen and Casing Materials . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 -10

6.6.3 Filter Pack Materials . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 -11

6.6.4 Filter Pack and Well Screen Design . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 -11

6.7 Safety Procedures for Drilling Activities . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 -12

6.8 Well Development . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 -14

6.9 Well Abandonment . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 -15

6.9.1 Abandonment Procedures . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 -15

6.10 Temporary Monitoring Well Installation . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 -16

6.10.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 -16

6.10.2 Data Limitation . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 -17

6.10.3 Temporary Well Materials . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 -17

6.10.4 Temporary Monitoring Well Borehole Construction . . . . . . . . . . . . . . . . . . . . . . 6 -17

6.10.5 Temporary Monitoring Well Types . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 -17

6.10.6 Backfilling . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 -18

6.11 Temporary Monitoring Well Installation Using Geoprobe® Screen Point 15

Groundwater Sampler . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 -19

6.11.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 -19

6.11.2 Assembly of Screen Point 15 Groundwater Sampler . . . . . . . . . . . . . . . . . . . . . . 6 -19

6.11.3 Installation of Screen Point 15 Groundwater Sampler . . . . . . . . . . . . . . . . . . . . . 6 -19

6.11.4 Special Considerations for Screen Point 15 Installations . . . . . . . . . . . . . . . . . . . 6 -20

6.12 References . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6 -21
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SECTION 7 - Ground Water Sampling ........................................ 7 - 1

7.1 Introduction ...................................................... 7 - 1

7.2 Purging .......................................................... 7 - 1

7.2.1 Purging and Purge Adequacy ......................................... 7 - 1

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

7.2.3 Purging Techniques - Wells with In-Place Plumbing ....................... 7 - 5

7.2.4 Purging Techniques - Temporary Monitoring Wells ....................... 7 - 6

7.2.5 Investigation Derived Waste .......................................... 7 - 7

7.3 Sampling ........................................................ 7 - 7

7.3.1 Equipment Available ................................................ 7 - 7

7.3.2 Sampling Techniques - Wells with In-Place Plumbing ..................... 7 - 7

7.3.3 Sampling Techniques - Wells without Plumbing .......................... 7 - 8

7.3.4 Sample Preservation ................................................ 7 - 9

7.3.5 Special Sample Collection Procedures .................................. 7 - 9

7.3.6 Specific Sampling Equipment Quality Assurance Techniques ............... 7 -11

7.3.7 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 ........................................................ 8 - 3

SECTION 9 - Wastewater Sampling .......................................... 9 - 1

9.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9 - 1

9.2 Site Selection . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9 - 1

9.2.1 Influent . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9 - 2

9.2.2 Effluent . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9 - 2

9.2.3 Pond and Lagoon Sampling . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9 - 2

9.3 Sample Types . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9 - 2

9.3.1 Grab Samples . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9 - 2

9.3.2 Composite Samples . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9 - 2

9.4 Use of Automatic Samplers . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9 - 3

9.4.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9 - 3

9.4.2 Conventional Sampling (Inorganic Parameters) . . . . . . . . . . . . . . . . . . . . . . . . . . . 9 - 4

9.4.3 Metals . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9 - 4

9.4.4 Extractable Organic Compounds, Pesticides, and PCBs . . . . . . . . . . . . . . . . . . . . 9 - 5

9.4.5 Automatic Sampler Security . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9 - 5

9.4.6 Automatic Sampler Maintenance, Calibration, and Quality Control . . . . . . . . . . . 9 - 5

9.5 Manual Sampling . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9 - 5

9.6 Special Sample Collection Procedures . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9 - 6

9.6.1 Organic Compounds and Metals . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9 - 6
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9.6.2 Bacteriological .................................................... 9 - 6

9.6.3 Immiscible Liquids/Oil and Grease ..................................... 9 - 6

9.6.4 Volatile Organic Compounds ......................................... 9 - 7

9.7 Special Process Control Samples and Tests ............................ 9 - 7

9.8 Supplementary Data Collection ...................................... 9 - 8

9.9 Sample Preservation .............................................. 9 - 8

9.10 References ....................................................... 9 - 9

SECTION 10 - Surface Water Sampling ...................................... 10- 1

10.1 Introduction ..................................................... 10- 1

10.2 Surface Water Sampling Equipment ................................ 10- 1

10.2.1 Dipping Using Sample Container ..................................... 10- 1

10.2.2 Scoops .......................................................... 10- 1

10.2.3 Peristaltic Pumps .................................................. 10- 1

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- 1

11.1 Introduction ..................................................... 11- 1

11.2 Sediment Sampling Equipment ..................................... 11- 1

11.2.1 Scoops and Spoons ................................................ 11- 1

11.2.2 Dredges ......................................................... 11- 2

11.2.3 Coring .......................................................... 11- 2

11.3 Special Consideration for Collection of Samples for Volatile Organic

Compounds ...................................................... 11.4

SECTION 12 - Soil Sampling ............................................... 12- 1

12.1 Introduction ..................................................... 12- 1

12.2 Equipment ...................................................... 12- 1

12.2.1 Precautions for trace Contaminant Soil Sampling ........................ 12- 1

12.3 Sampling Methodology ............................................ 12- 2

12.3.1 Manual Collection Techniques and Equipment .......................... 12- 2

12.3.2 Powered Equipment ............................................... 12- 3

12.4 Soil/Sediment Sampling (Method 5035) .............................. 12- 6

12.4.1 Equipment ....................................................... 12- 6

12.4.2 Sampling Methodology - Low Concentrations ........................... 12- 6

12.4.3 Sampling Methodology - High Concentrations ........................... 12- 7

12.4.4 Waste Samples ................................................... 12- 7

12.4.5 Special Techniques and Considerations 12- 7

12.4.6 Summary ....................................................... 12- 9

SECTION 13 - Waste Sampling ............................................. 13- 1
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EISOPQAM ToC - viii November 2001

13.1 Introduction ..................................................... 13- 1

13.1.1 Safety........................................................... 13- 1

13.1.2 Quality Control Procedures .......................................... 13- 1

13.1.3 Collection of Auxiliary Information and Data ........................... 13- 1

13.2 Waste Unit Types ................................................ 13- 2

13.2.1 Open Units ...................................................... 13- 2

13.2.2 Closed Units ..................................................... 13- 2

13.3 Equipment ...................................................... 13- 3

13.3.1 Waste Sampling Equipment ......................................... 13- 4

13.3.2 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

13.4.2 Surface Impoundments ............................................. 13- 6

13.4.3 Drums .......................................................... 13- 6

Figure 13-1 - Drum Data Form ....................................... 13- 8

13.4.4 Tanks ........................................................... 13- 9

13.5 Miscellaneous Contaminated Materials .............................. 13-10

13.6 Waste Sample Handling Procedures ................................. 13-11

13.7 Particle Size Reduction ............................................ 13-11

13.8 References ...................................................... 13-13

SECTION 14 - Ambient Air Monitoring ...................................... 14- 1

14.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 14- 1

14.2 Criteria Pollutant Monitoring (Reference/Equivalent Monitors)/for Air Pollutants

which National Ambient Air quality Standards have been established . . . . . 14-1

14.2.1 Monitoring Ozone in Ambient Air . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 14-1

14.2.2 Monitoring Carbon Monoxide in Ambient Air . . . . . . . . . . . . . . . . . . . . . . . . . . . 14-2

14.2.3 Monitoring Nitrogen Dioxide in Ambient Air . . . . . . . . . . . . . . . . . . . . . . . . . . . . 14-3

14.2.4 Monitoring Sulfur Dioxide in Ambient Air . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 14-4

14.2.5 Sampling of Particulate Matter in Ambient Air as PM2.5 . . . . . . . . . . . . . . . . . . . . 14-5

14.2.6 Sampling of Particulate Matter in Ambient Air as PM10 . . . . . . . . . . . . . . . . . . . . 14-6

14.3 Non-Criteria Pollutant Monitoring for Air Pollutants for which National 

Ambient Air Quality Standards have not been established . . . . . . . . . . . . . . . 14-7

14.3.1 Formaldehyde Sampling with Dinitrophenylhydrazine Cartridges using

Method TO-11A . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 14-7

14.3.2 Volatile Organic Compounds (VOC) Sampling with SUMMA® Electro-polished

Stainless Steel or Silcosteel Canisters Using Method TO-15A . . . . . . . . . . . . . . . 14-9

14.3.3 Sampling for Semi-Volatile Organic Compounds (SVOC) Analysis with 

High Volume PUF Samplers Using Methods TO-4A & TO-13A . . . . . . . . . . . . 14-10

14.3.4 Collecting Samples for Metals Analysis Using the High Volume Sampler . . . . . 14-12

14.3.5 Standard Operating Procedure for Mercury Analysis of Air Using the Tekran 

Mercury Vapour Analyzer model 2537A . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 14-13

14.3.6 Sampling for Dioxin and Dibenzofuran Analyses with High Volume

PUF Samplers Using Method TO-9A . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 14-16

14.3.7 Mercury Sampling Using Gold-Coated Glass Bead Tubes . . . . . . . . . . . . . . . . . . 14-17

14.3.8 Standard Operating Procedure for Chlorofluorocarbon (CFC) . . . . . . . . . . . . . . 14-19
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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

15.2.3 Specific Equipment Quality Control Procedures . . . . . . . . . . . . . . . . . . . . . . . . . 15- 3

15.2.4 Procedures for Traversing . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15- 5

Figure 15.2.1 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15- 5

Figure 15.2.2 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15- 6

Figure 15.2.3 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15- 7

Figure 15.2.4 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15- 8

Figure 15.2.5 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15- 9

Figure 15.2.6 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15- 9

15.2.5 Procedures for Differential GPS . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-10

15.3 Vertical Location (Elevation) Surveys . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-16

15.3.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-16

15.3.2 Equipment Available . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-17

15.3.3 Specific Equipment Quality Control Procedures . . . . . . . . . . . . . . . . . . . . . . . . . 15-18

15.3.4 Procedures for Differential Leveling . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-18

Figure 15.3.1 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-19

15.3.5 Procedures for Trigonometric Leveling . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-19

Figure 15.3.2 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-20

Figure 15.3.3 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-21

Figure 15.3.4 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-21

15.4 Hydrological Studies . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-22

15.4.1 Scope and Applicability . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-22

15.4.2 Methods . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-22

15.4.2.1 Surface Water Stage/Tape Downs . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-22

15.4.2.2 Time of Travel . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-23

15.4.2.3. Dilution . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-25

15.4.3 Current Measurement . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-27

15.4.4 Equipment . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-27

15.4.5 General Quality Assurance Procedures . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-28

15.4.6 Data/Records Management . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-28

15.5 Ground Water Level Measurements . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-28

15.5.1 General . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-28

15.5.2 Specific Ground Water Level Measuring Techniques . . . . . . . . . . . . . . . . . . . . . 15-29

15.5.3 Total Well Depth Measurement Techniques . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-29

15.5.4 Equipment Available . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-29

15.5.5 Specific Quality Control Procedures . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-30

15.6 Surface Geophysical Studies . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-31

15.6.1 General (17)(18) . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-30

15.6.2 Specific Surface Geophysical Methods . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-31

15.6.3 Instrument Operations . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15-33
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15.6.4 Specific Instrument Quality Control Procedures .......................... 15-34

15.7 References ..................................................... 15-35

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- 8

16.7 Dissolved Oxygen (DO) ............................................ 16- 8

16.8 Total Residual Chlorine ........................................... 16-10

16.9 Flash Point ...................................................... 16-13

16.10 Halogen Test .................................................... 16-14

16.11 References ...................................................... 16-16

SECTION 17 - Air Monitoring Safety Equipment Calibration Procedures ................ 17- 1

17.1 Introduction ........................................................... 17- 1

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 1000B) ....................................... 17- 7

17.5 Toxic Vapor Analyzer (TVA 1000A) ..................................... . 17-13

17.6 Century Model OVA-128 Organic Vapor Analyzer ......................... . 17-17

17.7 Ludlum Model 3 Radiation Survey Meter ................................. . 17-18

17.8 MiniRAE ............................................................. . 17-19

Sampling and Analysis of Mercury in Ambient Air Using Arizona Instrument

®

Mercury Dosimeter Tubes and the Model 511 Gold Film Mercury Vapor Analyzer

SECTION 18 - Flow Measurement ................................................. 18- 1

18.1 Introduction ........................................................... 18- 1

18.2 Wastewater Flow Measurement ........................................... 18- 1

18.2.1 Introduction ............................................................ 18- 1

18.2.2 Site Selection ........................................................... 18- 1

18.2.3 Flow Measurement Systems ............................................... 18- 2

18.2.4 Use of Existing Flow Measurement Systems .................................. 18- 2

18.2.5 Specific Techniques ...................................................... 18- 3

18.2.6 Open Channel Flow Measurements .......................................... 18- 4

18.2.7 Closed Conduit Flow Measurements ......................................... 18- 5

18.3 Surface Water Flow Measurements ....................................... 18- 6

18.3.1 Introduction ............................................................ 18- 6

18.4 Quality Assurance Procedures ............................................ 18- 7

18.5 Equipment ............................................................ 18- 7

18.6 References ............................................................. . 18-8

SECTION 19 - SOIL GAS SAMPLING ...................................... 19-1

19.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 19-1
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19.1.1 GORE-SORBER ® Implants ........................................ 19-1

19.1.2 Geoprobe® Grab Sampling using the PRT System ........................ 19-3

19.1.3 Geoprobe® Permanent Soil Gas Implants ............................... 19-4

19.2 References ....................................................... 19.6

APPENDIX A - Recommended Containers, Holding Times, & Preservation ......... A- 1

Soil and Sediment ................................................. A -1

Water and Waste Water ........................................... A -3

Waste .......................................................... A -6

Footnotes . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . A -7

APPENDIX B - Standard Field Cleaning Procedures ........................... . B - 1

B.1 Introduction ..................................................... . B - 1

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

B.2.3 Sampling Equipment used for the Collection of Trace

Organic/Inorganic Compounds . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . B - 4

B.2.4 Well Sounders or Tapes . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . B - 4

B.2.5 Goulds® Pump Cleaning Procedure . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . B - 5

B.2.6 Redi-Flo2® Pump . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . B - 5

B.2.7 Automatic Sampler Tubing . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . B - 5

B.3 Downhole Drilling Equipment . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . B - 6

B.3.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . B - 6

B.3.2 Preliminary Cleaning and Inspection . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . B - 6

B.3.3 Drill Rig Field Cleaning Procedure . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . B - 6

B.3.4 Field Cleaning Procedure for Drilling Equipment . . . . . . . . . . . . . . . . . . . . . . . . . B - 7

B.4 Emergency Disposal Sample Container Cleaning . . . . . . . . . . . . . . . . . . . . . . . B - 7

APPENDIX C - Field Equipment Center Standard Cleaning Procedures ................. C - 1

C.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 1

C.1.1 Specifications for Cleaning Materials . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 1

C.1.2 Handling and Containers for Cleaning Solutions . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 2

C.1.3 Disposal of Spent Cleaning Solutions . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 2

C.1.4 Safety Procedures for Cleaning Operations . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 3

C.1.5 Handling and Labeling of Cleaned Equipment . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 3

C.1.6 Initial Processing of Returned Equipment . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 4

C.2 Trace Organic and Inorganic Constituent Sampling Equipment . . . . . . . . . . . . . . . . C - 4
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EISOPQAM ToC - xii November 2001

C.2.1 Teflon® and Glass . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 4

C.2.2 Stainless Steel or Steel . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 5

C.2.3 Reusable Composite Sample and Organic/Analyte Free Water Containers . . . . . . . . . . . C - 5

C.3 Automatic Wastewater Sampling Equipment . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 5

C.3.1 ISCO® and other Automatic Samplers . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 5

C.3.2 ISCO® 1680, 2700, and 3700 Rotary Funnel, Distributor, and Metal Tube . . . . . . . . . . . C - 5

C.3.3 All Sampler Headers . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 6

C.3.4 Reusable Glass Composite Sample Containers . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 6

C.3.5 Plastic Reusable Composite Sample Containers (2700 - 5 gal., 3700 - 4 gal.) . . . . . . . . . C - 6

C.3.6 ISCO® 1680, 2700, and 3700 Glass Sequential Bottles for GC/MS Analyses . . . . . . . . . C - 7

C.3.7 Bottle Siphons for Composite Containers . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 7

C.3.8 Reusable Teflon® Composite Mixer Rods . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 7

C.4 Cleaning Procedures for Tubing . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 7

C.4.1 Silastic® Pump Tubing . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 7

C.4.2 Teflon® Sample Tubing . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 8

C.4.3 Stainless Steel Tubing . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 8

C.4.4 Glass Tubing . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 8

C.5 Cleaning Procedures for Miscellaneous Equipment . . . . . . . . . . . . . . . . . . . . . . . . . . C - 9

C.5.1 Well Sounders and Tapes . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 9

C.5.2 Goulds® Pump . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 9

C.5.3 Redi-Flo2® . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C - 9

C.5.4 Little Beaver® . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C -10

C.5.5 Drill Rig, Grout Mixer, and Associated Equipment . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C -10

C.5.6 Miscellaneous Sampling and Flow Measuring Equipment . . . . . . . . . . . . . . . . . . . . . . . . C -11

C.5.7 Field Analytical Equipment . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C -11

C.5.8 Ice Chests and Shipping Containers . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C -11

C.5.9 Pressure Field Filtration Apparatus . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C -11

C.5.10 Organic/Analyte Free Water Storage Containers . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C -12

C.5.11 Portable Solvent Rinse System . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C -13

C.5.12 Splash Suits . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C -13

C.5.13 SCBA Facemasks . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C -13

C.5.14 Garden Hose . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C -13

C.5.15 Portable Tanks for Tap Water . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C -14

C.5.16 Vehicles . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C -14

C.6 Preparation of Disposable Sample Containers . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C -14

C.6.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C -14

C.6.2 Plastic Containers used for "Classical" Parameters . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C -14

C.6.3 Glass Bottles for Semi-Volatile GC/MS Analytes . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C -15

C.6.4 Glass Bottles for Volatile GC/MS and TOX Analyses . . . . . . . . . . . . . . . . . . . . . . . . . . . C -15

C.6.5 Plastic Bottles for ICP Analytes . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . C -16

APPENDIX D - Sample Shipping Procedures

D.1 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
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APPENDIX E - Pump Operating Procedures ......................................... E - 1

E.1 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 Large Diameter Electric Submersible Pumps . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . E - 3

E.2.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . E - 3

E.2.2 Safety . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . E - 3

E.2.3 Pre-loadout Checkout Procedure . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . E - 3

E.2.4 Operation . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . E - 4

E.2.5 Maintenance and Precautions . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . E - 4

E.2.6 Trouble Shooting . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . E - 5

E.3 QED® Bladder and Purge Pumps . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . E - 5

E.3.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . E - 5

E.3.2 Operation - Bladder Pump . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . E - 5

E.3.3 Operation - Purge Pump . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . E - 6

E.3.4 Trouble Shooting . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . E - 6

E.4 Small Diameter Electric Submersible Pumps . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . E - 6

E.4.1 Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . E - 6

E.4.2 Safety . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . E - 7

E.4.3 Pre-loadout Checkout Procedures . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . E - 7

E.4.4 Operation . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . E - 7

E.4.6 Maintenance and Precautions . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . E - 8

E.4.7 Trouble Shooting . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . E - 8

APPENDIX F - Regional Technical Support for Criminal Investigations ........... . F - 1

F.1 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 - 1

G.1 Receiving Batteries from the Field . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . G - 1

G.2 Charging Batteries . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . G - 2

G.3 Post-Charging . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . G - 3

G.4 Maintenance . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . G - 4

Figure G.1 - Battery Log . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . G - 5

Figure G.2 - Battery Building Maintenance Report . . . . . . . . . . . . . . . . . . . . . . . G - 6

APPENDIX H - TECHNICAL SYSTEMS AUDIT FORM QUESTIONNAIRE ............ H - 1

A. NETWORK MANAGEMENT . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . H - 2
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B. FIELD OPERATIONS . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . H - 6

C. LABORATORY OPERATIONS (WHERE APPLICABLE) . . . . . . . . . . . . . . . . . . . H -10

D. DATA and DATA MANAGEMENT . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . H-16

E. QUALITY ASSURANCE/QUALITY CONTROL . . . . . . . . . . . . . . . . . . . . . . . . . . . H-20
EISOPQAM 1 - 1 November 2001

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 , was revised in 1986 with the same title. It was revised

again in 1991 with the title, Environmental Compliance Branch Standard Operating Procedures and Quality

Assurance Manual. In 1996, it was revised with the present title. The specific procedures outlined in the

manual are based on the experiences of Region 4 field investigators or documents 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 intent 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 in 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 2 - 1 November 2001

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.

Enforcement related activities include criminal investigations, 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

Superfund 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, 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.
EISOPQAM 2 - 2 November 2001

2.2 Potable Water Supply Investigations

Potable water supply investigations are usually conducted as part of a larger investigation such as

a spill, leaking tanks, nearby superfund site, etc. However, an investigation may be conducted independently

of a potential contamination source. 

Potable water supply investigations may include collecting samples from wells, surface waters,

distribution systems, private residential wells, etc. 

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 event

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 of analytical data, the project leader should carefully examine the data.

Web sites listed at the bottom of this section may be useful in an evaluation. If any of the primary or

secondary drinking water standards are exceeded, or any priority pollutants, RCRA 40 CFR 261 Appendix

VIII compounds, or the CERCLA 40 CFR 302 list of hazardous substances are detected, the project leader

will immediately provide the information listed below to the appropriate individuals in the Water

Management Division or Waste Management Division. The Water Management Division primary contact

is Lee Thomas in the Water Programs Enforcement Branch; the secondary contact is Carol Tarras. The

Waste Management Division primary contact is Glenn Adams in the Office of Technical Services; the

secondary contact is Kevin Koporec. 

 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 it to the Water

Management Division.

Web sites that may be useful: 

For the current MCLs and SMCLS with potential health effects and sources:

 http://www.epa.gov/OGWDW/wot/appa.html

 For a summary of drinking water health advisories:

 http://www.epa.gov/ost/drinking/standards/

 Region 4 Office of Technical Services http://www.epa.gov/region4/wastepgs/oftecser/oftecser.htm

 Region 3 Risk Assessment tables http://www.epa.gov/reg3hwmd/risk/riskmenu.htm

 Region 9 Risk Assessment tables http://www.epa.gov/region09/waste/sfund/prg/index.html

 NCEA (ORD-Cinn.) web page http://www.epa.gov/ncea/biblio.htm

 Oak Ridge National Laboratory risk http://risk.lsd.ornl.gov/homepage/rap_tool.htm

 assessment page

 EPA's Intergrated Risk Information http://www.epa.gov/ngispgm3/iris/

 System (ref. doses and slope factors):
EISOPQAM 2 - 3 November 2001

2.3 Civil Enforcement Investigations and Studies

2.3.1 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, conducting, 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 Re-authorization 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)

2.3.2 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 (i) shall have a right of entry to, upon, or through any premises in which an

effluent source is located or in which any records required to be maintained. . .are located,

and

 (ii) may at reasonable times have access to and copy any records, inspect any monitoring

equipment or method 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 - 4 November 2001

2.3.3 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, they should request the guard 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.

 Cite 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 - 5 November 2001

2.3.4 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). 

2.3.5 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 by 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 - 6 November 2001

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-in-Charge of the investigation in accordance with Appendix F of this SOP.
EISOPQAM 2 - 7 November 2001

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 main 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). Compliance monitoring inspections are usually requested

by the Clean Water Act Enforcement Section, Water Programs Enforcement Branch, Water Management

Division. 

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 a 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.

2.5.2 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 - 8 November 2001

Compliance Sampling Inspections (CSI)

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 action against

the permittee. Guidance for conducting CSI's is given in the NPDES Compliance Sampling Inspection

Manual (3).

Toxic Sampling Inspections (XSI)

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 Biomonitoring Inspection (CBI)

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 to ensure the

biological integrity of the receiving waters;

 Identify those permittees which may have potential toxic substances 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 biomonitoring 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 (PAI)

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 self-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 - 9 November 2001

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 (PCI)

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.

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 scale technical

evaluations 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 provided to Clean Water Act Section staff.
EISOPQAM 2 - 10 November 2001

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 appropriate parties 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 permission

from legal counsel.

Completion of NPDES Compliance Inspection Report Form (EPA Form 3560-3)

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 - 11 November 2001

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.

2.6.2 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 variety of training and technical assistance activities for Regional, State, and other Federal agency

personnel in methods of conducting field operations at hazardous waste sites. 

2.6.3 Planning for Field Investigative Support

Periodic meetings are typically held between a representative(s) of the Superfund Staff 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.

Based on the priorities agreed upon by the Superfund Staff, and the Waste Management Division,

field investigation schedules are prepared by the Superfund Staff and updated as needed. 
EISOPQAM 2 - 12 November 2001

2.6.4 Requests for Superfund Studies

Superfund investigations are prioritized by the 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 Staff leader. Requests are then

brought to the Superfund Staff 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.
EISOPQAM 2 - 13 November 2001

2.6.6 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 - 14 November 2001

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 the RCRA programs and

field investigations for 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 requirements.

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 Guidance Document (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 (confirmatory sampling)

to determine whether or not releases of hazardous wastes or constituents have occurred. Guidance for

conducting the RFA is in the RCRA Facility Assessment 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, delisting

investigations, 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 - 15 November 2001

2.7.3 Planning for Field Investigative Support

Periodic meetings are typically held between representative(s) of SESD 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,

a tentative field investigation schedule is prepared and updated as needed. 

2.7.4 Requests for RCRA Studies

RCRA investigations are prioritized by the Region 4, RCRA programs based on their need for field

investigative support. Requests for field investigative support are coordinated with the RCRA team

Supervisor or their designee(s). A memorandum with a request form is recommended 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 the 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, study dates and personnel.

 Methodology -- Analyses to be conducted and who will conduct analyses, field and laboratory

SOP references, and when samples will be received by the laboratory.

2.7.6 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. 

 Summary -- A brief summary of the key results and conclusions of the study.

 Discussion -- All aspects pertinent to the investigation e.g., sampling, figures, photographs,

analytical results, RCRA deficiencies, etc.
EISOPQAM 2 - 16 November 2001

 Methodology -- What information was obtained and from whom, what sampling procedures

were used, what analytical methods were used, 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 plans and reports will be reviewed internally. Final copies of the plan/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.

2.8 Underground Storage Tank (UST) Investigations

2.8.1 Introduction

USTs were traditionally investigated because of potential, or actual, contamination of the

environment from petroleum products. More recently, UST investigations have been conducted because

tanks contain hazardous substances. UST field investigations are requested by the Water Management

Division, Ground Water/Drinking Water Branch, UST Section and usually involve ground water and/or soil

sampling for UST constituents or related products. 

UST investigation objectives may include:

• Determining if there has been a release to the environment from the UST.

 Determining if potable wells are contaminated with UST constituents. 

• Determining if ground water is contaminated with UST constituents.

• Determining if vicinity soils have been contaminated with UST constituents.

 Determining the direction of the contamination plume and the source of the contamination. 
EISOPQAM 2 - 17 November 2001

2.8.2 Investigation Study Plans

Study plans are prepared for all UST investigations and 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 ensure that the plan will

meet their objectives. As a general rule, the Data Quality Objectives (DQO) process will 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 UST Section, 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.

2.8.3 Investigation Reports

An investigation report containing the following information will be completed:

 Introduction -- When , where and why the investigation was conducted and requesting office.

Staff who conducted the investigation.

 Background -- Site history, description, and results of previous studies.

 Summary -- Summary of the field investigation and resulting analyses, which constituents are

present, direction of plume movement if determined, possible sources of contamination, and

potable well owners’ names, phone numbers, addresses, if appropriate.

 Sketches/maps -- Showing sampling locations, UST locations, direction of plume, etc.

• Methodology – Reference to field and laboratory SOPs

Internal Peer Review and Report Recipients

UST reports will be reviewed internally. Final copies of the report will be sent to the requestor in

the UST Section. If private or public potable water supplies are sampled, refer to Section 2.2 for reporting

requirements.
EISOPQAM 2 - 18 November 2001

2.9 Underground Injection Control (UIC) Investigations

2.9.1 Introduction

Laws protecting ground water from contamination by injection of wastes allow for the sampling of

injection wells as well as nearby wells. UIC field investigations are requested primarily by the Region 4,

Water Management Division, Ground Water/Drinking Water Branch, GW & UIC Section and usually

involves ground water sampling for constituents related to the wastes being injected. 

UIC investigation objectives may include:

 Determining if vicinity potable water wells are contaminated with waste products from the

injection wells.

 Determining if vicinity ground water monitoring wells are contaminated with waste products

from the injection wells.

 Determining the direction of the contamination plume and the source of the contamination.

2.9.2 Investigation Study Plans

Study plans are prepared for all UIC investigations and 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 ensure that the plan will

meet their objectives. As a general rule, the Data Quality Objectives (DQO) process will 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 GW & UIC Section, 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.

2.9.3 Investigation Reports 

An investigation report containing the following information will be completed:

 Introduction -- When , where and why the investigation was conducted and requesting office.

Staff who conducted the investigation.

 Background -- Site history, description, and results of previous studies.
EISOPQAM 2 - 19 November 2001

 Summary -- Summary of the field investigation and resulting analyses, which constituents are

present, direction of plume movement if determined, possible sources of contamination, and

potable well owners’ names, phone numbers, addresses, if appropriate.

 Sketches/maps -- Showing sampling locations, location of injection well(s), other pertinent

information

• Methodology – Reference to field and laboratory SOPs

Internal Peer Review and Report Recipients

UIC reports will be reviewed internally. Final copies of the report will be sent to the requestor in

the GW & UIC Section. If private or public potable water supplies are sampled, refer to Section 2.2 for

reporting requirements.

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.
EISOPQAM 2 - 20 November 2001

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 PM10 or SO2, in which case it must be a Category (a) station.
EISOPQAM 2 - 21 November 2001

Network Design

Network design for State and Local Air Monitoring Stations (SLAMS), National Air Monitoring

Stations (NAMS), and Photochemical Assessment Monitoring Stations (PAMS) is detailed in Appendix D

of 40 CFR 58. Tables 2.10.1 and 2.10.2 show the population levels for which NAMS monitoring is required.

The required spatial 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 SO2 NAMS NETWORK SIZE

(APPROXIMATE NUMBER of STATIONS PER AREA)

 Population Concentration

Population Area Higha Mediumb Lowc

>1,000,000 6-10 4-8 2-4

500,000-1,000,000 4-8 2-4 1-2

250,000-500,000 3-4 1-2 0-1

100,000-250,000 1-2 0-1 0

 (a) PM10: High concentration areas are those for which ambient PM10 data show ambient

concentrations exceeding PM10 National Ambient Air Quality Standards (NAAQS) by

20% or more.

SO2: Defined as high when the ambient concentration exceeds the level of the 

primary NAAQS.

(b) PM10: Ambient concentrations exceed 80% of the NAAQS.

SO2: Ambient concentrations exceed 60% of the primary or 100% of the secondary

NAAQS.

(c) PM10: Ambient concentrations are less than 80% of the NAAQS.

SO2: Ambient concentrations are less than 60% of the primary or 100% of the secondary

NAAQS.
EISOPQAM 2 - 22 November 2001

TABLE 2.10.2

POPULATION LEVELS FOR WHICH NAMS MONITORING OF POLLUTANTS OTHER THAN

PM10 AND SO2 IS REQUIRED

POLLUTANT POPULATION

Lead

CO

Ozone

NO2

PM2.5

 500,000a

 500,000

 200,000

1,000,000

N/A 35-50 sites total

(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

Scale Appropriate for SLAMS

SO2 CO O3 NO2 Pb PM10 PM2.

5

Micro X X X X

Middle X X X X X X

Neighborhood X X X X X X X

Urban X X X X X X

Regional X X X X X

Spatial Scale

Scale Appropriate for NAMS

SO2 CO O3 NO2 Pb PM10 PM2.

5

Micro X X X X1

Middle X X X1

Neighborhood X X X X X X X

Urban X X X2

Regional X2

1 Only permitted if representative of many such micro-scale environments in a residential district (for middle

scale, at least two).

2 Either urban or regional scale for regional transport sites.
EISOPQAM 2 - 23 November 2001

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 these 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 United States Environmental

Protection Agency, National Exposure Research Laboratory (NERL), Human Exposure and Atmospheric

Sciences Division (MD-46), Research Triangle Park, North Carolina 27711.

Probe Siting

Probe siting criteria for State and Local Air Monitoring Stations (SLAMS), National Air Monitoring

Stations (NAMS), and Photochemical Assessment Monitoring Stations (PAMS) is detailed in Appendix E

of 40 CFR 58. Tables 2.10.4 and 2.10.5 display the requirements for probe siting. For further details,

clarification, or justification, refer to Appendix E of 40 CFR 58.

Borosilicate glass and FEP Teflon®, or their equivalent, are acceptable materials for SLAMS/NAMS

intake sampling lines. FEP Teflon® is not acceptable for VOC and carbonyl sampling at PAMS sites.

Borosilicate glass, stainless steel, or its equivalent, are the acceptable probe materials for VOC and carbonyl

sampling. The residence time in sampling probes for reactive gases must be less than 20 seconds. 
EISOPQAM 2 - 24 November 2001

TABLE 2.10.4

SUMMARY of PROBE SITING CRITERIA

Pollutant Scale

Height Above

Ground(m)

Horizontal and

Vertical

Distance From

Supporting

Structure 1

Distance From

Trees to Probe

Distance From

Roadways to

Probe

SO2

2,3,4,5 All 3 - 15 >1 >10 N/A

CO 3,4,6 Micro

All Others

3 ± 1⁄2

3 - 15

>1

>1

>10

>10

2-10

See Table

2.10.5

O3

2,3,4 All 3 - 15 >1 >10 See Table

2.10.5

NO2

2,3,4 All 3 - 15 >1 >10 See Table

2.10.5

Pb 2,3,4,5,7,8 Micro

All Others

2-7

3 - 15

>2

 (All Scales, 

Horizontal

Distance)

>10

(All Scales)

See Table

2.10.5

PM10

2,3,4,5,7,8 Micro

All Others

2-7

3 - 15

>2

 (All Scales, 

Horizontal

Distance)

>10

(All Scales)

5-15

See 58CFR,

App. E

PM2.5

2,3,4,5,7,8 >2

 (All Scales, 

Horizontal

Distance)

>10

(All Scales)

2-10

 See 58CFR,

App. E

 1. When probe is located on a rooftop, this separation distance is in reference to walls, parapets, or penthouses.

 2. Should be greater than 20 meters from tree driplines and must be 10 meters from the dripline when trees act as an

obstruction.

 3. 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.

 4. Must have unrestricted airflow 270 degrees around the inlet probe, or 180 degrees if the probe is on the side of a building.

 5. 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.

 6. 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).

 7. Must be greater than 10 meters from a street intersection and should be located mid-block.

 8. For collocated Pb and PM10 samplers, a 2-4 meter separation distance must be met.

 9. Must have unrestricted airflow 270 degrees around the sampler, except for street canyon sites.
EISOPQAM 2 - 25 November 2001

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 10

 15,000 25

 20,000 45

 30,000 80

 40,000 115

 50,000 135

>60,000 >150

Neighborhood and Urban Scale Ozone and NO2 Stations

<10,000 10

 15,000 20

 20,000 30

 40,000 50

 70,000 100

>110,000 >250

Lead Stations

Micro Scale

Middle

Neighborhood,

Urban Scale

Regional

Scale

 10,000 5 - 15 >15 - 50 >50

 20,000 5 - 15 >15 - 75 >75

 40,000 5 - 15 >15 - 100 >100

* Distances should be interpolated based on traffic flow.

2.10.3 State and Local QA Plan Reviews

Introduction

40 CFR, Part 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 SESD Air Monitoring Staff (AMS)

has been assigned the responsibility of reviewing QA Plans for SLAMS in Region 4.
EISOPQAM 2 - 26 November 2001

Review/Approval Process

The Air Monitoring Staff reviews state and local QA Plans submitted to the Regional Administrator

for approval. At a minimum, each QA Plan must include operational procedures for the elements listed in

Section 2.0 of 40 CFR Part 58, Appendix A. Based on the review results and comments received from the

reviewers, the AMS recommends approval/disapproval action to the Region 4 QA Officer. If the AMS

reviewer 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.

2.10.4 Performance Audits

Introduction

Performance audits are conducted by the appropriate AMS 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. 

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.

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 Concentration (ppm CO)

1 3 - 8

2 15 - 20

3 35 - 45

4 80 - 90

Note: Audit point #4 will be run only on monitors operated in the 0 to 100 ppm range.
EISOPQAM 2 - 27 November 2001

Ozone

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 Concentration (ppm O3)

1 0.03 - 0.08

2 0.15 - 0.20

3 0.35 - 0.45

4 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 particulate filter.

The audit concentration should be introduced through the probe, if possible. Audit concentration points will

be in the following ranges:

Audit Point Concentration (ppm SO2)

1 0.03 - 0.08

2 0.15 - 0.20

3 0.35 - 0.45

4 0.80 - 0.90

Note: Audit point #4 will only be run on monitors operating in the 0 to 1.0 ppm range.

Nitrogen Dioxide

Nitrogen dioxide audit concentrations shall be introduced into the monitor through the particulate

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 NO2)

1 0.03 - 0.08

2 0.15 - 0.20

3 0.35 - 0.45

4 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 by gas phase titration (gpt), it will be necessary to run a zero and span point on the monitor's NOx

and NO channels. If NO and/or NOx data collected by a state/local agency are submitted to the AIRS system,

the NO and/or NOx channel must be audited using either cylinder dilution or gpt.
EISOPQAM 2 - 28 November 2001

2.10.5 Air Monitoring Technical System Audit

Introduction

A technical system audit (TSA) 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 a modified version of the questionnaire (see Appendix H) in "The QA Handbook for Air Pollution

Measurement System," Volume II: Part 1, Ambient Air Quality Monitoring Program, Quality System

Development, US EPA, Office of Air Quality Planning and Standards, Research Triangle Park, NC.

(commonly referred to as the "Red Book."). The scope of the systems audit includes an appraisal of network

management, field operations, laboratory operations, data management, quality assurance, and reporting.

The TSA 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 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 sites be inspected during a systems

audit. For smaller agencies, at least two sites should be inspected. One half of the sites 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 Appendix 2,Section 2 (5.0 Data and Information

Management Audits) of the Red Book.

Guidelines for Conducting Systems Audits of State and Local Agencies

A systems audit should consist of three separate phases:

  pre-audit activities;

  on-site activities; and

  post-audit activities.

Each of these activities is discussed in detail in Sections 15.3.1, 15.3.2, 15.3.3, and Appendix 15,

Section 2 of the Red Book. Because of the length of these Red Books sections, they are incorporated by

reference.
EISOPQAM 2 - 29 November 2001

Audit Reporting

The systems audit report shall include:

 Introduction

 Observations and Recommendations

 Field

 Laboratory

 Data Review

 Conclusion

 Appendix of Supporting Documentation

The report's Appendix of Supporting Documentation contains copies of the completed 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 Staff

The Air Monitoring Staff’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-annually

on continuous sampler (SO2, O3, NO2, and CO) and lead (Pb).
EISOPQAM 2 - 30 November 2001

2.10.7 PM2.5 Federal Reference Method (FRM) Performance Audit Program (PEP)

Introduction

Appendix L, of 40 CFR Part 50 provides the Reference Method for the Determination of Fine

Particulate Matter as PM2.5 in the Atmosphere. This method provides for the measurement of the mass

concentration of fine particulate matter having and aerodynamic diameter less than or equal to a nominal 2.5

micrometers (PM2.5) in ambient air over a 24-hour period for purposes of determining whether the primary

and secondary national standards for fine particulate matter specified in § 50.6 of this part are met. 

Quality assessment procedures are provided in Part 58, Appendix A, and quality assurance guidance

are provided in the 1) Quality Assurance handbook for Air Pollution Measurement Systems, Volume I,

Principles. EPA/600/R-94/038a, April 1994; 2) Section 2.12 of the Quality Assurance handbook for Air

Pollution Measurement Systems, Volume II, Ambient Air Specific Methods, EPA/600/R-94/038b,

November, 1998; 3) Quality Assurance Handbook for Air Pollution Measurement Systems, Volume IV:

Meteorological Measurements, (revised edition) EPA/600/R-94/038d, March, 1995.

To achieve the designated Data Quality Objectives (DQO’s), Measurement Quality Objectives

(MQO’s) were designed to evaluate and control measurement uncertainty to tolerable levels. Hence, the

Federal Reference Method Performance Evaluation Program (FRM PEP) was implemented to provide a

mechanism to understand total measurement bias and compare all environmental data operations against one

data operation. 

Air Monitoring Staff

The Air Monitoring Staff’s role is to:

1. Manage the national work assignment for two ESAT field scientists and one laboratory scientist.

2. Plan and cluster sites on the annual FRM PEP schedules. 

3. Provide oversight and communication with the Region 4 State and Local ambient air monitoring

agencies.

4. Conduct Technical Systems Audits (TSA) of each reporting organization once every 3 years.

5. Assure that every federal reference method designation within a reporting organization have 25

percent of sites audited (including collocated sites).

6. Assure that at least one monitor in each reporting organization is audited annually.

7. Audit each scheduled SLAM PM2.5 monitoring sites at a frequency of 4 times per year. 

8. Assure that all FRM and Federal Equivalent Methods (FEM) sampling sites are audited once every

four years.

9. Ensure that each site platform can accommodate the portable sampler within 1 to 4 meters of the

routine sampler.

10. Review and recommend approval/disapproval of all Quality Assurance Project Plans (QAPP) and

Standard Operating Procedures (SOP) for Region 4 State and Local ambient air monitoring agencies.
EISOPQAM 2 - 31 November 2001

11. Design, install and manage the operation of the East Coast PM2.5 Filter Weighing Laboratory for the

client Regions 1, 2, 3, 4, 6, and FRM PEP filters for the State of Washington, Region 10.

12. Act as liaison between and provide technical assistance to the twenty four Region 4 State and Local

agencies, OAQPS, and the EPA client Regions.

Audits

In accordance with 40 CFR Part 58, Appendix A, and EPA Quality Assurance Guidance Document

2.12, Section 10.3, the Air Team will conduct TSA on each Region 4 reporting organization, once every 3

years. These audits are designed to assess the entire measurement system and data management activities

with regards to the PM2.5 monitoring networks. These activities will include the following:

Initial equilibration, weighing, and transportation of the filters to the sampler

Site selection criteria assessment

Equipment installation

Site security

Equipment maintenance

Calibration procedures

Handling and placement of filters

Operation of the sampler and sample collection

Removal, handling, and transportation of the filters from the sampler to the laboratory

Post-sampling equilibration, weighing, storage, and archival of the sampled filters

Data analysis and reporting

An example checklist for the PM2.5 TSA is shown in the EPA Quality Assurance Guidance Document

2.12, Section 10.3, pages 10 - 14.

The FRM PEP audits are conducted on 25 percent of the SLAMS monitoring network per reporting

organization, and 25 percent of the designated methods used per reporting organization four times per year.

Each primary and collocated sampler should receive at least one FRM PEP audit every four years.
EISOPQAM 2 - 32 November 2001

2.11 References

1. US-EPA, NPDES Compliance Inspection Manual, United States Environmental Protection Agency,

September 1994.

2. US-EPA, NPDES Compliance Evaluation Inspection Manual, MCD-75, United States

Environmental Protection Agency, Washington, D.C. 1981.

3. US-EPA, NPDES Compliance Sampling Inspection Manual, MCD-51, United States Environmental

Protection Agency, Washington, D.C., 1979.

4. Compliance Biomonitoring 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 Guidance Document ,United States Environmental

Protection Agency, Office of Solid Waste, Washington, D.C., (EPA/530/R-001) November 1992.

7. RCRA Facility Assessment Guidance, United States Environmental Protection Agency Office of 

Solid Waste, Washington, D.C., (PB87-107769) October, 1986.
EISOPQAM 2 - 33 November 2001

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 study?

Study plan issued? Date issued?

Study plan reviewed by the Division? Acceptable?

Comments:

Was study plan followed?

Comments: 

Was a safety plan prepared for the study?

Comments:

Was the safety plan adequate?

Comments:

Was the safety plan followed?

Comments:

Additional comments or information:

Checklist sections completed

for this overview: 1. 2. 3. 4. 5. 6.

Key: 1. General Procedures 4. Surface Water Sampling

2. Ground Water Sampling 5. Waste Sampling

3. Soil, Sediment, Sludge Sampling 6. Monitoring Well Installation
EISOPQAM 2 - 34 November 2001

SECTION 1 - GENERAL PROCEDURES - SAFETY, RECORDS, QA/QC, CUSTODY, ETC.

 1. Type samples collected?

Comments:

 2. Were sampling locations properly selected?

Comments:

 3. Were sampling locations adequately documented in a bound field log book using indelible

ink? 

Comments:

 4. Were photos taken and a photolog maintained? 

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

book?

Comments: 

 7. Was sampling equipment properly wrapped and protected from possible contamination

prior to sample collection?

Comments:

 8. Was sampling equipment constructed of Teflon®, glass, or stainless steel?

Comments:

 9. Were samples collected in proper order? (least suspected contamination to most

contaminated?)

Comments:

10. Were clean disposable latex or vinyl gloves worn during sampling?

Comments:

11. Were gloves changed for each sample station?

Comments:

12. Was any equipment field cleaned?

Comments:

13. Type of equipment cleaned:

Comments:

14. Were proper field cleaning procedures used?

Comments:

15. Were equipment rinse blanks collected after field cleaning?

Comments:

16. Were proper sample containers used for samples?

Comments:
EISOPQAM 2 - 35 November 2001

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 collected?

Comments:

20. Were samples properly field preserved?

Comments:

21. Were preservative blanks utilized?

Comments:

22. Were field and/or trip blanks utilized?

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 collection?

Comments:

26. Were chain-of-custody and receipt for samples forms properly completed?

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

sampling?

Comments:

31. Was safety monitoring equipment properly calibrated and calibrations recorded in a bound

field log book?

Comments:
EISOPQAM 2 - 36 November 2001

SECTION 2 - SAMPLING - GROUND WATER

 1. Type of wells sampled? (monitoring, potable, industrial,etc.)

Comments:

 2. Were wells locked and protected?

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 infiltration?

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 depths?

Comments:

10. Were measurements made to the nearest 0.01 ft?

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 determined?

Comments:

14. Was a sufficient volume purged prior to sampling?

Comments:

15. How many volumes?

Comments:

16. How was the purged volume measured?

Comments:

17. What was the method of purging?

Comments:
EISOPQAM 2 - 37 November 2001

18. Were pH, conductivity, temperature, and turbidity measurements taken and recorded at least

once during each well volume purged?

Comments:

19. Were pH, conductivity, temperature, and turbidity readings stable prior to sampling?

Comments:

20. How many wells were sampled? Upgradient? Downgradient?

Comments:

21. How were the samples collected? Bailer Pump Other

Comments:

22. If a pump was used, what type?

Comments:

23. If a pump was used, was it properly cleaned before and/or between wells?

Comments:

24. What were the cleaning procedures?

Comments:

25. Did bailers have Teflon® coated wire leaders to prevent rope from coming into contact with

water?

Comments:

26. Were bailers open or closed top?

Comments:

27. Was a clean bailer and new rope used at each well?

Comments:

28. Were samples properly transferred from the sampling device to the sample containers? (i.e.,

volatile sample first - not aerated, etc.)

Comments:

29. Was pH of preserved samples checked to insure proper preservation?

Comments:

30. Were samples iced immediately after collection?

Comments:

31. For what analyses were the samples collected?

Comments:

32. If samples were split, what were the sample/station numbers for these?

Comments:

33. Are the ground water samples being filtered?

Comments:

34. If the ground water are being filtered, what procedure is being used?

Comments:
EISOPQAM 2 - 38 November 2001

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.
EISOPQAM 2 - 39 November 2001

SECTION 3 - SAMPLING - SOIL, SEDIMENT, SLUDGE, ETC. (Non-containerized)

 1. Type of samples collected?

Comments:

 2. General description of samples?

Comments:

 3. How many samples were collected?

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?

Comments:

11. Were samples properly placed into sample containers?

Comments:

12. Were samples iced immediately after collection?

Comments:

13. For what analyses were the samples collected?

Comments:

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 site?

Comments:

17. What was the condition of the drilling and sampling equipment when it arrived on site?

Comments:
EISOPQAM 2 - 40 November 2001

18. Was a decontamination area located where the cleaning activities would not crosscontaminate 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 SOP?

Comments:

22. Other comments or observations:
EISOPQAM 2 - 41 November 2001

SECTION 4 - SAMPLING - SURFACE WATER (Pond, Stream, River, Leachate, Etc.)

 1. Type of samples collected?

Comments:

 2. General description of samples?

Comments:

 3. How many samples were collected?

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 containers?

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 collected? 

Comments:

13. Was the pH of preserved samples checked to insure proper preservation?

Comments:

14. Were samples iced immediately after collection?

Comments:

15. For what analyses were the samples collected?

Comments:

16. If samples were split, what were the sample/station numbers for these?

Comments:

17. Other comments or observations:
EISOPQAM 2 - 42 November 2001

SECTION 5 - WASTE SAMPLING - DRUMS, TANKS, BARRELS, ETC. (Containerized) 

1. What was the objective of the sampling investigation?

Comments:

2. Description of units or sources sampled (closed/open, etc.)?

Comments:

3. General description of samples (Oil, sludge, waste)

Comments:

4. How many samples were collected?

Comments:

5. Were grab or composite samples collected?

Comments:

6. How many aliquots were taken for the composite sample?

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

containers?

Comments:

10. Were samples properly placed into sample containers?

Comments:

11. For what analyses were the samples collected?

Comments:

12. Was equipment field cleaned?

Comments:

13. Was clean equipment properly wrapped and stored in a clean area?

Comments:

14. Were the cleaning and decontamination procedures conducted in accordance with the

Appendix B of the EISOPQAM?

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 - 43 November 2001

18. What level of safety protection was required for collection of the samples?

Comments:

19. Other comments or observations:
EISOPQAM 2 - 44 November 2001

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)?

Comments: 

 2. Were the wells installed starting in the least contaminated area and proceeding to the most

contaminated area?

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 rig(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 site?

Comments:

 7. Was a decontamination area located where the cleaning activities would not

cross-contaminate clean and/or drying equipment?

Comments:

 8. Was clean equipment properly wrapped and stored in a clean area?

Comments:

 9. Was the drilling rig(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 wells?

Comments:

12. Was this drilling method(s) the same as proposed in the study plan and/or POP?

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:

15. If air rotary was used, was an in-line organic air filter employed? Was a cyclone velocity

dissipator used?

Comments:
EISOPQAM 2 - 45 November 2001

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 depth?

Comments:

19. Were the wells double cased?

Comments:

20. If yes to 19, explain procedure.

Comments:

PERMANENT WELL INSTALLATION

21. What type of well casing(s) and screen(s) were used?

Comments:

22. What diameter were the well casing(s) Screen(s)?

Comments:

23. Was there a minimum two inch annulus around the casing between casing and borehole was

or inside augers)?

Comments:

24. What was the length of the well screen(s)?

Comments:

25. What was the slot size of the well screen(s)?

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 installed?

Comments:

29. Specify type of materials in 28 [(play sand, Ottawa sand, etc.) and grain 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 size?

Comments:

31. Were the wells installed to the proper depths?

Comments: 

32. Were well screens placed at the proper intervals?

Comments:

33. Were the filter packs placed a minimum of two feet above the well screens?

Comments:
EISOPQAM 2 - 46 November 2001

34. Was the tremie tube method used to place the filter packs?

Comments:

35. Were seals placed above the filter packs?

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 bentonite 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

time?

Comments:

40. Was the tremie tube method used to place the bentonite pellets?

Comments:

41. Was the annulus grouted from the seal to within two feet of the ground surface, or below the

frost line?

Comments:

42. Was the tremie tube method used to place the grout in the annulus?

Comments:

43. If no to 42, what method was used?

Comments:

44. What type of grout was used to seal the annulus (neat cement, cement/bentonite, cement/sand,

etc.)?

Comments:

45. What grout mix ratio was used? (should be stated in the POP)

Comments:

46. What was the density of the grout? (lb/gal, etc.)

Comments:

47. If bentonite grout was used, was the density at least 9.4 lb/gal?

Comments:

48. Was the density determined using a mud balance?

Comments:

49. Was the grout allowed to set a minimum of 24 hours before the surface pad was installed?

Comments:

50. Was a concrete surface pad installed with an outer protective casing and locking cap?

Comments:

51. How far below the ground surface did the concrete pad extend?

Comments:
EISOPQAM 2 - 47 November 2001

52. What were the dimensions of the concrete pads?

Comments:

53. Did the well casings extend to a minimum of 2.5 feet above the ground surface?

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 developed?

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 - 48 November 2001

EXHIBIT 2.2

REGION 4

STATE/CONTRACTOR OVERVIEW CHECKLIST

*** NOTE *** This checklist is for overviewing State personnel overviewing a facility or contractor or for

overviewing a contractor overviewing contractors.

PART 1

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 study?

Study/Work plan issued? Date issued?

Study/Work plan reviewed by the Division? Acceptable?

Was the Study/Work plan reviewed by the State/Contractor?

Comments:

Was the study plan followed? 

Comments:

Was a safety plan prepared for the study?

Did the State/Contractor review the safety plan?

Was the safety plan adequate?

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 - 49 November 2001

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 investigation?

Comments:

 8. Were there improper procedures or practices used which the State/Contractor failed to

recognize?

Comments:

 9. Was sampling conducted in accordance with the SOP or other EPA standard operating

procedures?

Comments:

10. Was equipment decontamination conducted in accordance with standard operating procedures

specified by EPA?

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 name?

Comments:

13. Had those personnel received training in sampling techniques and equipment handling?

Comments: 

14. When was the latest training received and by whom was it provided?

Comments:

15. What equipment was available and/or used during the investigation?

Comments:
EISOPQAM 2 - 50 November 2001

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 EPA?

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 collected?

Comments:

26. Had investigative/sampling personnel received appropriate safety training?

Comments:

27. Do investigative/sampling personnel undergo periodic refresher safety training?

Comments:

28. Did investigative/sampling personnel have appropriate safety equipment for the investigation?

Comments: 

29. Are investigative/sampling personnel classified as to the type of investigations they can

conduct?

Comments:

30. Have investigative/sampling personnel had comprehensive physicals?

Comments:

31. Do investigative/sampling personnel participate in a medical monitoring program?

Comments:

32. Give a general evaluation of the activities observed during the overview and note any other

comments or observations.

Comments:
EISOPQAM 2 - 51 November 2001

EXHIBIT 2.3

STATE PROGRAM EVALUATION

HAZARDOUS WASTE FIELD ACTIVITIES

State 

Agency 

Specific Activity RCRA or CERCLA

Location 

Telephone 

Activity Managers 

Evaluator

Date

PART 1 -- FIELD ACTIVITY STAFFING

Description of Field Activity:

Field Activity Personnel Staffing

NAME(s) TITLE TRAINING EXPERIENCE

Field Safety Program

and Training:

Personnel categorized as to activity?

Does a formal safety training program exist?

Does a formal safety training tracking system exist?

Does a formal medical monitoring program exist?

Safety Training

Received?

In-House Outside EPA

Safety Program Needs:

Field Activity Adequately Staffed to meet Existing RCRA or CERCLA Inspection and Investigation

Needs: Adequate Inadequate

Projected Staffing Needs:
EISOPQAM 2 - 52 November 2001

PART 2 -- FIELD OPERATING PROCEDURES

 1. Does a standard operating procedures manual exist or is one being prepared?

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 prepared?

Comments:

 6. Are the field activities adequately addressed in the SOP Manual?

Comments:

 7. Does the SOP address: (Sample Collection) YES NO

- Ground Water

- Surface Water

- Surface Soil

- Subsurface Soil

- Waste - Pits, Ponds, Lagoons

- Waste - Closed Container

- Tissue (Fish, etc.)

- Air

- QC

Comments:

 8. Does the SOP address: (Sample Handling Techniques) YES NO

 - Standard Sampling Containers

- Field Equipment & Sample Container Cleaning Procedures

- Sample Identification

- Sample Preservation & Holding Times

- Sample Chain-of-Custody

- Sample Packaging Techniques

- Identification of Hazardous Samples to Lab

- QC

Comments:
EISOPQAM 2 - 53 November 2001

 9. Does the SOP address: (Field Documentation and Records) YES NO

Field Documentation or Bound Record Books

Comments:

Photographs

Comments:

Site Mapping (Sketching of sites)

Comments:

PART 3 -- FIELD CONTRACTORS 

 1. Are field contract personnel used to conduct field investigations?

Comments:

 2. What activities do field contractors perform?

Comments:

 3. If yes, does a quality control program exist to monitor contractor activities?

Comments:

PART 4 - FACILITIES

 1. Is adequate space provided for the storage of field equipment?

Comments:

 2. Are facilities and/or space provided for the cleaning, repair, and preparation of field

equipment?

Comments:

 3. Specific Facility Needs:

 
EISOPQAM 2 - 54 November 2001

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:

 3. Safety Equipment Available

 - Monitoring Equipment

 - Protective Clothing

 - Respiratory Protection

 4. Are Safety Procedures available in written form or in a manual?

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 3 - 1 November 2001 

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

Sample identification, chain-of-custody records, receipt for sample forms, and field records (with

the exception of surveying notes) 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 stickon 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 and Chain-of-Custody Record

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 responsible for accepting custody of samples from the field

sample custodian or a transferee.

One individual may fulfill more than one of the roles described above.
EISOPQAM 3 - 2 November 2001 

3.2 Sample and Evidence Identification

PERFORMANCE OBJECTIVE:

 To accurately identify samples and evidence collected.

3.2.1 Sample Identification

The method of sample identification used depends on the type of sample collected. In-situ field

samples are those collected for specific field analysis or measurement where the data are recorded directly

in bound field logbooks or on the Chain-of-Custody Record, with identifying information, while in the

custody of the sampling team. Examples of such in-situ field measurements and analyses include pH,

temperature, dissolved oxygen and conductivity. Samples other than those collected for in-situ analysis are

identified by using a standard sample tag (Figure 3-3) which are attached to the sample container. In some

cases, particularly with biological samples, the sample tag may have to be included with or wrapped around

the sample. 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;

 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

 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 3-3, 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 not available, the white sample tag may be used and should be marked "Criminal" in bold letters on

the tag.

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). 
EISOPQAM 3 - 3 November 2001 

3.2.2 Photograph, Digital Still Image and Video Identification

Photographs and Digital Still Images

When photographs or digital images are taken, a record of each exposure or image shall be kept in

a bound field logbook. The following information shall be recorded in the logbook:

 an accurate description of what the photograph or image shows, including the name of the

facility or site and the specific project name and project number;

 the date and time that the photograph or image was taken;

 the name of the individual who took the photograph or digital image.

When photographs are used in technical reports or placed in the official files, the film shall be

developed with the negatives supplied uncut. The identifying information that was recorded in the field

logbook shall be entered on the back of the prints. For criminal investigations, the negatives must be

maintained with the bound field logbook in the project file and stored in a secured file cabinet.

When digital images are used in technical reports or placed in the official files, the disk with the

original, unaltered file of the images or a printed copy of the unaltered images shall be placed in the official

files as well. If printed copies of the images are used, each image shall be identified using the information

that was recorded in the field logbook. For enforcement cases, it is imperative that the individual who took

the image be identified in the field logbook in the event their testimony is required.

Video

When a video tape is made for use as evidence in an enforcement case, the following information

should be recorded in a bound field logbook:

 the date and time that the video was recorded;.

 a brief description of the subject of the video tape;

 the person recording the video.

Video records shall include a visual notation (placard) at the beginning of the of the video with the

appropriate information (i.e., location, date, time). An audio record may also be included in the video tape

with the above logistical information as well as a narrated description of the video record.

A label shall be placed on the video tape with the appropriate identifying information (i.e., project

name, project number, date, location etc.). In the event testimony regarding a video tape recording is

required for an enforcement case, one individual should be responsible for recording the video for each case.

The original, unaltered tape shall be placed in the official files.

 
EISOPQAM 3 - 4 November 2001 

3.2.3 Identification of Physical Evidence

Physical evidence, other than samples, shall be identified by using 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), the vessel or container should be marked 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 logbooks. 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.

 An instantaneous measurement of the media being measured by the recorder shall be taken and

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 other information required to interpret the

data such as type of flow device, chart units, factors, etc.

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

site 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

Chain-of-custody procedures are comprised of the following elements: 1) maintaining custody of

samples or other evidence, and 2) documentation of the chain-of-custody for evidence. To document chainof-custody, an accurate record must be maintained to trace the possession of each sample, or other evidence,

from the moment of collection to its introduction into evidence.
EISOPQAM 3 - 5 November 2001 

3.3.2 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.

3.3.3 Documentation of Chain-of-Custody

Sample Tag

A sample tag (Figure 3-3) should be completed for each sample using waterproof, non-erasable ink

as specified in Section 3.2.

Sample Seals

Samples should be sealed as soon as possible following collection using the EPA custody seal shown

in Figure 3-5. The sample custodian should write the date and their initials on the seal. Except for criminal

investigations, 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. Custody seals will always be used for criminal investigations. 

Chain-of-Custody Record

The field Chain-Of-Custody Record (Figure 3-1) 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 Chain-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 separate Chain-of-Custody Record should be used for each final

destination or laboratory used during the investigation.

All information must be supplied in the indicated spaces (Figure 3-1) to complete the field ChainOf-Custody Record. The reverse side of the Chain-of-Custody Record (Figure 3-2) describes the

requirements for station ID, sample ID and media codes

 All samplers and sampling team leaders (if applicable) must sign in the designated signature

block.

 One sample should be entered on each line and 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 Number" column (or adjacent to this column) for the appropriate

sample(s).
EISOPQAM 3 - 6 November 2001 

 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/Air bill" block at the

top of the Chain-of-Custody Record. The “Remarks/Air bill” block may also be used to record

Air bill numbers or registered or certified mail serial numbers.

 The total number of sample containers for each sample must be listed in the "Total Containers"

column. The number of individual containers for each analysis must also be listed in the

respective column. Required analyses should be circled or entered in the appropriate location

as indicated on the Chain-of-Custody Record.

 The tag numbers for each sample and any needed remarks should be in the "Tag Numbers"

column.

 The sample custodian and subsequent transferee(s) should document the transfer of the samples

listed on the Chain-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 occurs should be documented in the proper

space on the Chain-of-Custody Record.

 Usually, the last person receiving the samples or evidence should be the laboratory sample

custodian or their designee(s).

The Chain-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

chain-of-custody should be evaluated based upon its inclusion of all of the above information in a legible

format.

If chain-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 Chain-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 initials and 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 Chain-of-Custody Record and a new seal affixed. The information on the seal

should include the sample field custodian's initials and 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 Chain-Of-Custody

Record shall be completed for each set of samples.

3.3.4 Transfer of Custody with Shipment
EISOPQAM 3 - 7 November 2001 

 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 Chain-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, an Air Bill should be used. Receipts from post offices and Air Bills shall be retained as

part of the documentation of the chain-of-custody. The Air Bill number or registered mail serial

number shall be recorded in the remarks section of the Chain-Of-Custody Record. 

3.4 Receipt for Samples Form (CERCLA/RCRA/TSCA)

PERFORMANCE OBJECTIVE:

 To assure that staff comply with environmental laws which require providing a Receipt

for Samples Form.

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. The laws do not require that homeowners or

other off-site property owners be given this form.

3.4.2 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. All information

must be supplied in the indicated spaces to complete the Receipt for Samples form.

 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./Remarks" column.

 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.
EISOPQAM 3 - 8 November 2001 

 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 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;

 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;
EISOPQAM 3 - 9 November 2001 

 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.)
EISOPQAM 3 - 10 November 2001 

3.6 Document Control

 PERFORMANCE OBJECTIVE:

 To assure that project files are maintained in accordance with Divisional guidelines.

Document control refers to the maintenance of inspection and investigation project files. All

information 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 transmittal memorandum(s); and

 relevant documents related to the original investigation/inspection or follow-up activities related

to the investigation/inspection.

Inappropriate personal observations and irrelevant information should not be placed in the official

project files. At the conclusion of the project, the project leader shall review the file to ensure that it is

complete. 
EISOPQAM 3 - 11 November 2001 

3.7 Disposal of Samples or Other Physical Evidence

 PERFORMANCE OBJECTIVE:

 To ensure that proper disposal procedures are used for samples or other evidence. 

Disposal of samples or other physical evidence obtained during investigations is conducted on a caseby-case basis. Before samples which have been analyzed are disposed of, the ASB sample custodian shall

contact the project leader via E:mail, indicating that the samples will be disposed of by a certain date unless

the project leader dictates otherwise. If the sample custodian does not receive a message from the project

leader within the time specified in the E:mail, the samples will be disposed of. 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 investigation

shall be disposed of without written permission from EPA's Criminal Investigations Division.

 Samples associated with routine inspections may be disposed of following approval from the

project leader. Sample tags will be discarded along with the samples.

3.8 Field Operations Records Management System (FORMS)

 PERFORMANCE OBJECTIVE:

 To introduce the procedure for streamlining sample documentation

FORMS is a computer program designed to streamline the documentation required by SESD and/or

the Contract Laboratory Program (CLP) for sample identification and chain-of-custody. Once the appropriate

information is entered into the computer, FORMS will generate stick-on labels for the sample tags and sample

containers (CLP), and will generate sample receipt forms and chain-of-custody records 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 for the tags,

bottle labels, sample receipt forms and chain-of-custody records. Operating instructions are available for use

with the FORMS program.
EISOPQAM 3 - 12 November 2001 

FIGURE 3-1

CHAIN-OF-CUSTODY FORM
EISOPQAM 3 - 13 November 2001 

FIGURE 3-2

MEDIA CODES

 Station ID - Station ID is required if positional data is recorded for the sample.

Any combination of letters, numbers, or other characters. Maximum of 20 characters. Use this

column to identify a sampling station where one or more samples or field measurements are

taken. A few examples are well numbers, NPDES permit numbers, Air permit numbers, AOC

numbers, Grid numbers, Site designations, etc., or combinations of these as appropriate.

Sample ID - Required. Any combination of letters or numbers. Maximum of 8

characters. NOTE: For QA/QC samples, the Sample ID must begin with the

letters “QA for the sample to be properly identified.

 Media Code - Required. Choose the code that most closely describes the sample:

Environmental Samples

SF -Surface Soil (0"-12")

SB -Subsurface Soil (>12")

PW -Potable Water

MS -Municipal Water Supply

IW -Industrial Well

WA -Waste

SW -Surface Water

SD -Sediment

GW -Groundwater

PC -Precipitation

OT -Other (Unknown)

OB -Other Biota

MP -Municipal Proc. Wastewater

IP -Industrial Proc. Wastewater

WP -Wipe Sample

FI -Fish Sample

VG -Vegetation

MI -Macroinvertebrates

WW -Wastewater

SL -Sludge (non-RCRA)

UI -UIC Injection Wells

US -Underground Storage Tanks

PT -Petroleum Tanks

AA -Ambient Air

IA -Indoor Air

ME -Municipal Eff. Wastewater

IE -Industrial Eff. Wastewater

PE -Periphyton

TI -Tissue

Field QA/QC Samples

TS -Trip Blank-Soil

TW -Trip Blank-Water

TP -Trip Blank-Wipe

EB -Equipment Rinse Blank

GR -Grout Blank

MB -Drilling Mud Blank

DB -Potable Decon Blank

BB -Bentonite Blank

FA -Field Blank Air

 

FB -Filter Sand Blank

OW -Organic Free Water Blank

PB -Preservative Blank

GB -Glove Blank

BO -Bottle Blank

FL -Field Blank

IB -Dry Ice Blank

BK -Other Blank
EISOPQAM 3 - 14 November 2001 

BL -Blender Blank

FIGURE 3-3

SAMPLE TAG
EISOPQAM 3 - 15 November 2001 
EISOPQAM 3 - 16 November 2001 

FIGURE 3-5

EPA CUSTODY SEAL
EISOPQAM 4 - 1 November 2001 

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 site operations is ultimately the responsibility of each individual worker. 

Field investigators will not be required to participate 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.

29 CFR Part 1910.134, Respiratory Protection: These OSHA regulations govern the use and

maintenance of respiratory protection equipment used by personnel handling hazardous wastes.

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 (f) to study the problem of protecting the

safety and health of workers at hazardous waste sites. 
EISOPQAM 4 - 2 November 2001 

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.

Safety, Health and Environmental Management Program Procedures and Policy Manual: This

manual covers safety practices and rules governing activities at SESD facilities and field sites. 

The remaining parts of this section cover hazard communication, safety protocols, training, and equipment

that 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.

4.2.3 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

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.
EISOPQAM 4 - 3 November 2001 

4.2.4 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 current MSDSs are available on the Lan

and the following locations:

 The Field Equipment Center;

 Battery Charging Shed; and

 All field vehicles used to transport hazardous chemicals or used as mobile laboratories where

such hazardous chemicals are utilized.

Access to MSDSs on the Lan is accomplished by the following procedure:

MSDS Access

The following instructions cover basic use of the MSDS system. If you encounter problems or if you

have any questions, please call Jim Gray at X8613.

1. In LAN Windows, double click on the SESD Applications Icon, then double click on the OHS

Database Icon. 

2. Once the program is loaded, use any key to go through the Title, Warning and Disclaimer

screens. At the Main Screen, press F2 to activate the Pull Down Menu. The Select Data Base

function will be highlighted. Scroll right to the SEARCH Pull Down Menu. The Enter Query

function will be highlighted. Press ENTER to activate the Query screen.

3. The first line of the Query screen asks for the Chemical Name. For example, type in Nitric Acid.

DO NOT PRESS THE ENTER KEY AFTER TYPING IN THE CHEMICAL NAME. Press F3

for the search. The search screen will eventually show 1 document found. After 10 or so

seconds, the MSDS will appear. 

4. You can navigate through the MSDS by using Page Up/Down or by scrolling with the arrow

keys, but it is slow. The recommended method is to press F7 which activates the Jump To pull

down menu. In this menu, highlight the information you want and press ENTER. For example,

you want to make up a HazComm label for a container of Nitric Acid. In the Jump To menu,

scroll down to HAZARDS IDENTIFICATION and press enter. After a few seconds, that

portion of the MSDS will be displayed showing the NFPA numbers to enter on the label. Now

suppose you want to know how to store your newly labeled container of nitric acid. Press F7

again to activate the pull down Jump To menu. Scroll to HANDLING AND STORAGE and

press enter. The screen will display the portion of the MSDS dealing with handling and storage.

If you would like to know what the incompatibles are that the MSDS keeps referring to, Press

F7, and on the Jump To menu scroll to STABILITY AND REACTIVITY then press ENTER.

The screen will display the types of things and a list of specific things that nitric acid should be

kept separate from (and why).
EISOPQAM 4 - 4 November 2001 

5. If you would like to print the MSDS, press F2 for the Menu. Scroll down to PRINT DATA and

press the ENTER key. The MSDS will print out on the network printer you have selected for

your PC.

6. To exit the program, press F2 for the Menu. Scroll down to EXIT and press the ENTER key.

Finally, here are a few suggestions to help you when doing a search. Take the example of methylene

chloride. If you try this one by following the instructions given above, you will find that the search

will find 0 documents. This does not mean there is no MSDS for methylene chloride, it means that

the program calls it something else. When you encounter a situation like this, delete the name you

have typed into the CHEMICAL NAME space. Scroll down to TRADE NAME/SYNONYM and

retype the name, in this case methylene chloride. You will find the search gives you 12 documents

found. Upon review of the documents, you can see that the program calls methylene chloride,

dichloromethane. By selecting that name from the 12 given, you will get the correct MSDS.

When using TRADE NAME/SYNONYM for a search, you can get over a hundred documents to

search. By far the easiest and most direct way to search is by CAS Number. If you need a CAS

number, call an ASB chemist or call the SHEM. 

4.2.5 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.

The Hazardous Chemical Inventory will be updated quarterly and reported to the Chemical Hygiene

Officer (CHO).

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

Chemical Inventory List on the LAN, and the locations of MSDSs as stated in Section 4.2.4.
EISOPQAM 4 - 5 November 2001 

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 hazards, and specific

procedures to be implemented to protect them from exposure to hazardous chemicals; 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 (SHEM).

Safety protocols are to be followed by the SSO as well as each individual that is a part of the investigation.

Safety during hazardous waste site investigations begins with the individual. However, it is the responsibility

of the SSO to plan and coordinate the following during an investigation: 

1. Ensure that each member of the investigative team is up to date on their site safety training (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 gain knowledge of site operations and sampling strategies.

3. Prepare and enforce the site safety plan.

4. Make sure that necessary project specific safety equipment is available and operational. This

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

medical monitoring for heat stress throughout the operation.
EISOPQAM 4 - 6 November 2001 

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)

 hearing protection

 hard hat

 steel toe/shank safety boots (leather and rubber)

 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:

 Enclosed area entry;

 Level A, B, or C operations;

 Drilling or power augering;

 Drum openings;

 Brush cutting with power equipment;

 Boat operations;

 Generator operations; and

 Steam cleaning.

4.3.3 OSHA Confined Space Entry 

According to 29 CFR Part 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 that 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.

4.3.4 Entry into Enclosed Areas 

When conducting hazardous waste site investigations in areas that do not meet the definition in

OSHA 29 CFR Part 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 Part 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
EISOPQAM 4 - 7 November 2001 

enter after conducting appropriate air monitoring include, building interiors (if possible the field

investigator(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 (tri-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 no more than 90 days after

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.

4.3.6 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.

 
EISOPQAM 4 - 8 November 2001 

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 ionization 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

limited 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. 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.

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.

Level A Level B LEVEL C LEVEL D

Respiratory Maximum Maximum Moderate Minimum

Skin Maximum High Moderate Minimum

Eye Maximum High Moderate Minimum
EISOPQAM 4 - 9 November 2001 

The relationship between air monitoring results and levels of protection (LOP) is shown in the following

table. 

Instrument Response LOP

PID/FID Background D

PID/FID Less than 5 PPM above background C

PID/FID 5 PPM to 200 PPM B

PID/FID Greater than 200 PPM A

Oxygen Less than 19.5% B

CN Greater than 0 PPM and less than 10 PPM B

CN 10 PPM or greater 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.

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

Shirt, long pants or coveralls

Boots with steel toes and shank

OPTIONAL

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, rain gear, cool vests,

and heat stress monitors)

LEVEL D

is used when:

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 - 10 November 2001 

LEVEL C

REQUIRED

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 enclosed area initial entry)

OPTIONAL

Boot covers (disposable)

Hard hat

Face shield

ELSA (for other than initial operations)

Thermal/weather protection (coat, overalls, sweater, hat, rain gear, cool vests

and heat stress monitors)

LEVEL C

is used when:

The atmospheric contaminants, liquid splashes, or other direct contact will

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 the contaminants.

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 - 11 November 2001 

MODIFIED LEVEL C

REQUIRED

LEVEL C (modified to include chemically resistant splash suit and triple

glove system)

Cool vests and heat stress monitors (if ambient temperature exceeds 80F) -

see below

Splash shield

ELSA (for enclosed area initial entry)

OPTIONAL

Boot covers (disposable)

Hard hat

ELSA (for other than initial operations)

Cool vests and heat stress monitors are optional if ambient temperature is

80F or less)

Modified 

Level C

is used when:

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 a chemically resistant suit for more than 30 minutes

and the temperature is 80F to 90F.

 Cool vests are required when wearing an chemically resistant suit for more than 15 minutes

and the temperature is above 90F.

 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 the SSO.
EISOPQAM 4 - 12 November 2001 

LEVEL B

REQUIRED

MODIFIED LEVEL C (without the requirement for splash shield, ELSA, and

APR)

Positive pressure, full-face piece self-contained breathing apparatus

(SCBA)/airline system

OPTIONAL

Boot covers (disposable)

Hard hat

ELSA

Cool vests and heat stress monitors (if ambient temperature is

80F or less)

Splash shield

Level B

is used when:

The type and concentration of atmospheric contaminants have been identified

and require the maximum level of respiratory protection, but 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 risk of fire/explosion cannot

be mitigated.

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 80F to 90F.

 Cool vests are required when wearing an chemically resistant suit for more than 15 minutes

and the temperature is above 90F.

 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 the SSO.
EISOPQAM 4 - 13 November 2001 

LEVEL A

REQUIRED

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)/airline system

OPTIONAL

Boot covers (disposable)

Hard hat

Cool vests and heat stress monitors (if ambient temperature is 80F or less)

LEVEL A

is used when:

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 mitigate the risk of fire/explosion.

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 80F to 90F.

 Cool vests are required when wearing a totally-encapsulated, chemical-protective suit for

more than 15 minutes and the temperature is above 90F.

 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 the SSO.
EISOPQAM 4 - 14 November 2001 

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 80F 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 80F. 

 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 - 15 November 2001 

Site Control

 Site control serves to minimize exposure to contaminants and is accomplished by: 1) providing site

security to 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 - 16 November 2001 

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. Site

workers will then proceed to the first decontamination wash tub where their suit, 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.
EISOPQAM 4 - 17 November 2001 

Level B Decontamination Procedures

Level B operations pose a limited risk of exposure to decontamination personnel. Level B site

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 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.

4. Once in the support 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 suit 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.

5. 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
EISOPQAM 4 - 18 November 2001 

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 - 19 November 2001 
EISOPQAM 4 - 20 November 2001 
EISOPQAM 4 - 21 November 2001 

Site 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 site. 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 - 22 November 2001 

**EXHIBIT 4.1

SITE SAFETY PLAN

SAFETY PLAN

Site Name: Contact:

Address:

Phone Number:

Purpose of Visit:

Proposed Date of Work:

Directions to Site:

SITE INVESTIGATION TEAM:

PERSONNEL * SAFETY CATEGORY RESPONSIBILITIES

* All employees have been trained/medically monitored in accordance with OSHA 29

CFR 1910.120 requirements and US-EPA Region IV Field Health and Safety Manual,

1990 edition. 

PLAN PREPARATION:

Prepared by: Date

Reviewed/Approved by: Date

Section Chief: Date

SITE STATUS:

Active Inactive Unknown
EISOPQAM 4 - 23 November 2001 

EMERGENCY INFORMATION:

Local Resources:

Ambulance (Name): Phone:

Hospital (Name): Phone:

Police (Local or State): Phone:

Fire Department: Phone:

Office Resources:

OFFICE/POINT of CONTACT WORK PHONE HOME PHONE

SESD Office - Haz. Waste Section (706) 355-8603

EPA - Emergency Response - Atlanta (404) 562-8700

SHEM - Betty Kinney (706) 355-8511 (770) 725-2023

Branch Safety Officer - Jim Gray (706) 355-8613 (706) 742-8467

EMERGENCY CONTACTS:

Poison Control Center Phone: (800) 282-5846

National Response Ctr (ENVIRONMENTAL EMERGENCY ONLY) Phone: (800) 424-8802

 

Directions to Hospital (Attach Map if Available):

SAFETY AND HEALTH RISK ANALYSIS

Waste Types/Chemicals (Attach MSDS for each):
EISOPQAM 4 - 24 November 2001 

HAZARD EVALUATION:

Known or Suspected Hazardous/Toxic Materials (If applicable include: PEL/IDLH and/or

TLV-TWA/TLV-STEL, LEL, flammability, odor, reactivity, stability, corrosivity) 

OVERALL HAZARD:

SERIOUS MODERATE LOW UNKNOWN

SITE PERIMETER ESTABLISHMENT:

Map/Sketch attached?

Perimeter identified?

Zone(s) of contamination identified?

RECOMMENDED LEVEL(S) OF PROTECTION:

Level of Protection:

(check those that apply)

LEVEL A LEVEL B LEVEL C LEVEL D

Modifications:

Respiratory:

Field Dress:

Monitoring Procedures/Equipment*:

TVA® 1000 PID/FID OVA® FID

Rae® PID MicroTip® PID

CN Monitor Halogen

Radiation Survey Meter LEL/Oxygen

Other, Specify:

*All instruments are calibrated in accordance with the U.S. Environmental Protection Agency,

Region 4, Environmental Investigations Standard Operating Procedures and Quality Assurance

Manual, May 1996, or according to the manufacturer's specifications.
EISOPQAM 4 - 25 November 2001 

Method of Air Surveillance:

Additional Site Specific Information/Stipulations:

Site Decontamination Procedures:

Confined Space Entry (check one) YES NO

If yes, define procedures to be used:
EISOPQAM 4 - 26 November 2001 

AUGERING and DRILLING OPERATIONS:

Underground Utilities:

All underground utilities must be located prior to commencement of drilling operations involving the

drill rig and power augers. Complete the underground utilities checklist below and prepare a site map

showing the locations of all underground utilities identified.

UTILITY LOCATOR/CONTACT PERSON PHONE # DATE of 

LOCATION

Power:

Telephone: *

Gas:

Water:

Sewer:

Other:

* Include non-AT&T lines such as Sprint, MCI, etc.

Above Ground Utilities:

All above ground utilities must be located prior to commencing drilling/augering activities. A

map will be prepared showing the locations of all power lines, telephone lines, video cables, guy

wires, and other objects which could pose a hazard to personnel operating the drill rig, power

auger, or hand auger with multiple extensions. The SSO will insure that all operations are kept

well clear of such hazards.

DAILY CHECKS: 

Check all proposed drilling locations with a pipe-seeker. As a minimum, the first three feet of a

power bored hole will be dug using a post hole digger/hand auger. Personnel involved in the

drilling will wear eye and head protection in addition to normal safety gear appropriate for the

required level of protection. The SSO will insure that all personnel remove watches, rings, and

other jewelry, as well as securing loose fitting or dangling articles of clothing while in the

vicinity of the drilling operations. Additionally, the SSO will insure that a 90-degree clear zone is

maintained for a radius of at least 6 feet behind the drill rig. The following items will be visually

checked daily by the designated driller.

1. All control mechanisms for adjustment, wear and lubrication.

2. Guy wire tension

3. Air and hydraulic systems for deterioration or leakage.

4. Rope reeving.

5. Hoist brakes, clutches and operating levers.

6. Kill switches.
EISOPQAM 4 - 27 November 2001 

4.3.7 Boating Operations

The skipper must be familiar with the capabilities of their vessel (care and maintenance of

engines, batteries, emergency procedures, and rules of navigation as prepared by the United States Coast

Guard). The skipper is responsible for everything that happens on the vessel.

When participating in field work, make sure that your field party knows where you will be

working (a “float plan”) and the expected hour of your return.

When deploying equipment on station make sure that it is secured and not a danger to fellow

workers. When the vessel is underway all equipment should be placed in the boat and secured. 

Boats need to be checked out through the Boat Log in F107.

Upon return to the SESD facility, all temporary/portable gas cans must be removed from the

boats and placed in the Boat Hotel Hazardous Materials Building.

Consumption of alcohol will not be permitted on any boat at any time.

Smoking will not be permitted on any boat at any time.

The law prohibits the throwing, discharging, or depositing of any refuse matter of any kind

(including trash, garbage, oil or hazardous substances into the waters of the United States to a

distance of three miles from the coastline.

Required Equipment:

Outboard motorboats less than 26 feet in length which are so constructed that entrapment of

flammable vapors cannot occur are not required to carry fire extinguishers but they are recommended and

should be capable of extinguishing fires involving flammable liquids and grease (class “B” fires).

1) all recreational boats less than sixteen (16) feet in length, including sailboats and rowboats,

and all kayaks and canoes, carry at least one Coast Guard Approved Type I, II, III or IV

Personal Flotation Device (PFD) for each person on board, and 

2) all recreational boats sixteen (16) feet or over in length, including sailboats and rowboats,

carry at least one Type I, II, or III (wearable) PFD for each person on board and one Type IV

(throwable) PFD in each boat. Weather or working conditions may dictate the wearing of

PFD’s. 

All recreational boats 16 feet or more are required to be equipped with visual distress signaling

devices (VDS) at all times when operating on coastal waters. Also, boats less than 16 feet long are

required to carry visual distress signals when operating on coastal waters at night. Coastal waters are

defined as (1) The ocean (territorial sea) (2) The Great Lakes (3) Bays or sounds that empty into those

waters, and (4) Rivers over two miles across at the mouth, upstream to a point where they narrow to two

miles. The simplest VDS is a bright orange flag bearing a black square and a black circle (other forms

can be found in the U.S. Coast Guard Auxiliary Boating Skills and Seamanship).
EISOPQAM 4 - 28 November 2001 

Trailering:

Trailering of boats 

1. Make sure to use the proper class of hitch for the weight of the trailer being towed;

2. Check to have the proper size coupler for the ball being used; 

3. Trailer must have safety chains; 

4. A tire-pressure gauge should be used to check tire pressure frequently; 

5. Running lights, brake lights and turn signals should be functioning; 

6. Every unattached piece of gear in the trailered boat should be firmly secured, and the boat

itself should be firmly lashed in place; 

A more detailed description of boating regulations and safety can be found in the United States

Coast Guard Auxiliary Manual Boating Skills and Seamanship. ISBN #0-930028-03-1
EISOPQAM 4 - 29 November 2001 

**EXHIBIT 4.2

FLOAT PLAN

Complete this plan, before going boating and leave it with a reliable person who can be

depended upon to notify the Coast Guard, or other rescue organization, should you not return as

scheduled. Do not file this plan with the Coast Guard.

PROJECT DATES_____________________________________(if overnight, date returning)

1. NAME OF PERSON REPORTING_____________________________________________________________

 TELEPHONE NUMBER_____________________________________________________________________

BOAT MAKE COLOR LENGTH ENGINES OCCUPANTS

Wahoo White 26 IB

Privateer White 24 2 OB

Parker White 23 2 OB

Parker White 21 OB

Mako White 20 OB

Privateer White 18 OB

Shocker Tan 18 OB

Shocker Gray 16 OB

Jon Gray 14 OB

Jon Gray 12 OB

4. TRIP EXPECTATIONS: LEAVE AT_____________________________________________________(TIME)

 FROM____________________________________________________________________________________

 GOING TO________________________________________________________________________________

 EXPECTED TO RETURN BY________________________________________________________(TIME)

 AND IN NO EVENT LATER THAN__________________________________________________(TIME)

5. IF NOT RETURNED BY__________________________________(TIME), CALL THE COAST GUARD, OR

 LOCAL AUTHORITY) ____________________________________________ TELEPHONE NUMBERS

_____________________________________________________________________

6. SURVIVAL EQUIPMENT: (CHECK AS APPROPRIATE)

_____PFDs _____FLARES _____MIRROR _____SMOKE SIGNALS _____EPIRB

_____CLOTHING _____FLASHLIGHT _____FOOD _____ PADDLES

_____WATER _____OTHERS _____ANCHOR _____ RAFT OR DINGHY

7. RADIO:_____YES _____NO

 TYPE_________________________________________ FREQS._____________________________________

8. ANY OTHER PERTINENT INFO:_____________________________________________________________

 ________________________________________________________________________________________

9. FOR SINGLE BOAT OPERATION: AUTOMOBILE LICENSE____________________TYPE_____________

 TRAILER LICENSE____________________________COLOR/MAKE OF

AUTO_______________________

 WHERE PARKED__________________________________________________________________________

10. OTHER:__________________________________________________________________________________
EISOPQAM 4 - 30 November 2001 

4.3.8 FIELD PROCEDURES FOR HANDLING PATHOGENIC SAMPLES:

Whenever there is a possibility that water, soil or sediment may contain pathogenic materials all

precautions should be taken to prevent exposure to those collecting and handling the samples.

1. Latex/neoprene gloves shall be worn, as well as boots, waders, and respirators when

necessary, for the collection of possible pathogenic samples.

2. After sample collection, gloves will be contained and boots, waders, equipment, etc. used in

the sample collection will be decontaminated with soap and water. Hands will be

thoroughly washed before proceeding to other tasks.

3. Sample containers shall be cleaned on the outside to help eliminate contamination of

handlers in the laboratory and placed in containment if necessary.
EISOPQAM 5 - 1 November 2001 

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 - 2 November 2001 

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 uncontaminated 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 a sample.

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/varying

volume (TCVV) method. The TVCV method is typically used with automatic samplers that are

paced by a flow 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 estuaries.
EISOPQAM 5 - 3 November 2001 

Quality Control Samples

Quality control samples are collected during field studies for various purposes which include the

isolation of site effects (control samples), define background conditions (background sample), evaluate

field/laboratory variability (spikes and blanks, trip 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

of concern.

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. A split sample will also measure inter-or intra-laboratory precision.

Duplicate Sample -- two or more samples collected and representative of a given population. The

purpose of a duplicate sample is to estimate the variability of a given characteristic or contaminant

associated with a population. 

Trip 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 they reach the laboratory. Trip 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,(also known as proficiency test (pt) samples)-- 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 with each shipment to contract laboratories only.

Spiked samples are used to measure bias due to sample handling or analytical procedures. 

Equipment Field Blanks -- a sample collected using organic-free water which has been run

over/through sample collection equipment. 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 rinse blanks of equipment that has been field cleaned.

Temperature Blanks -- a container of water shipped with each cooler of samples requiring

preservation by cooling to 4C (ice). The temperature of the blanks are measured at the time of

sample receipt by the laboratory. No temperature blank is necessary for samples designated as

“waste”.
EISOPQAM 5 - 4 November 2001 

Preservative Blanks -- a sample that is prepared in the field and used to determine if the preservative

used during field operations was contaminated, thereby causing a positive bias in the contaminant

concentration. On studies of short duration, usually only a post-preservative blank is prepared at the

end of all sampling activities. On studies extending beyond one week, a pre-preservative 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 organic/analyte-free water in the container and then preserving

the sample with the appropriate chemical.

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-borne 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 dusty

environments and/or from areas where volatile organic contamination is present 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., organic/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

is handled, packaged, and transported in the same manner as all other wipe 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. 

Filter Pack Blanks -- a sample of the material used to create an interface around the screened

interval of a monitoring well.

Construction Water Blanks -- a sample of the water used to mix or hydrate construction

materials such as monitoring well grout.

Organic/Analyte Free Water Blanks -- a sample collected from a field organic/analyte free water

generating system. The sample is normally collected at the end of sampling activities since the

organic/analyte free water system is recharged prior to use on a study. On large studies, samples

can be collected at intervals at the discretion of the project leader. The purpose of the

organic/analyte free water blank is to measure positive bias from sample handling variability due

to possible localized contamination of the organic/analyte free water generating system or

contamination introduced to the sample containers during storage at the site. Organic/analyte

free water blanks differ from field blanks in that the sample should be collected in as clean an

area as possible (a usual location for the organic/analyte free water system) so that only the

water generating system/containers are measured.
EISOPQAM 5 - 5 November 2001 

5.3 Sampling Design

5.3.1 Introduction

Development of a sampling design may follow the seven steps outlined in the EPA publications,

"Guidance for the Data Quality Objectives Process" (1) and "Data Quality Objectives Process for Hazardous

Waste Sites" (2). The Data Quality Objectives (DQOs) process is a logical step-by-step method of

identifying the study objective, defining the appropriate type of data to collect, clarifying the decisions that

will be based on the data collected, and considering 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 (authoritative 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" (3), and "Standard Guide for the

Generation of Environmental Data Related to Waste Management Activities: Quality Assurance and Quality

Control Planning and Implementation" (4).

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.

5.3.3 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

uncontaminated fire brick. 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. 
EISOPQAM 5 - 6 November 2001 

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 (5).

5.3.4 Specific Sampling Designs

Sampling strategies used by the Branch typically fall into two general groups: authoritative or

probabilistic. Authoritative (also known as directed, subjective, and/or biased) 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. Professional judgement should always be used to develop both authoritative and probabilistic

sampling designs. 

5.3.5 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

(6), the US-EPA document Characterization of Hazardous Waste Sites - A Methods Manual, Volume 1 - Site

Investigations (7), the US-EPA document Guidance of Choosing a Sampling Design for Environmental Data

Collection (8) and Statistical Methods for Environmental Pollution Monitoring by Richard O. Gilbert (5).

5.3.6 Authoritative Sampling

 Authoritative sampling is based on the judgement of the investigator, and does not necessarily result

in a sample that reflects the average characteristics of the entire matrix. There are two types of authoritative

designs: judgmental sampling and biased sampling. Judgmental sampling uses the knowledge and experience

of the investigator to attempt to derive “average” conditions at a site. In contrast, biased sampling attempts

to determine the maximum or minimum value for contaminant of concern. Biased sampling often focuses

on "worst case" conditions in a matrix, for example, the most visually contaminated area or the most recently

generated waste. 

The primary advantages of authoritative sampling are the designs tend to be quick and simple to

implement, and the designs have relatively low costs. Authoritative sampling is ideally suited for sites where

contaminants of concern greatly exceed, or are significantly below, predetermined action levels. Because

the experience of the investigator is often the basis for sample collection, personal bias (depending on the

study objectives) may be introduced and should be recognized as a potential problem. However, preliminary

or screening investigations, and certain regulatory investigations, will correctly employ authoritative

sampling. 

5.3.7 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. 
EISOPQAM 5 - 7 November 2001 

5.3.8 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 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 grid 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 grid. Also, the grid size would typically

be adjusted according to the number of samples that are required.

5.3.11 Adaptive Cluster Sampling

Adaptive sampling designs are ones in which additional decisions units or sample locations are

selected depending on the interpretation of measurements or observations made during an initial survey (8).

Additional sample locations are selected when a contaminant of concern in one or more units exceeds some

predetermined action level in the initial survey. Adaptive cluster sampling is a beneficial design for sites

where a contaminant of concern is sparsely distributed but highly concentrated. Simple random or systematic

grid sampling can be used in conjunction with adaptive cluster sampling designs. 
EISOPQAM 5 - 8 November 2001 

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;

 UST/UIC 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 process may not be strictly followed, but the elements of the process are always considered

during study planning. These elements include:

 State the environmental problem;

 Collection of information concerning historical data, site survey, and site history;

 Identification of the decision to be made with the data collected;

• Identification of data gaps;

• Identification of objectives, and investigation boundaries;

 Sampling design selection and design optimization;

 Sample types and number;

 Analytical requirements and limitations; and 

 Data interpretation and assessment.
EISOPQAM 5 - 9 November 2001 

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 site survey includes:

 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.

5.5.2 Data Quality Objectives (DQOs)

Consideration of the purpose which the data generated from the soil sampling effort is to serve drives

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.

5.5.3 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.
EISOPQAM 5 - 10 November 2001 

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.

5.5.4 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

variability, with confirmation of the estimate being made during the more extensive systematic study. If a

variability study is to be conducted, it will be limited in scope and will use certain default values or

assumptions 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 - 11 November 2001 

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 (t) 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 = t

2

(CV)2

 p2

Where:

n = number of samples to collect

t = 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 = (1.96)2(0.65)2 

 (0.20)2

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

COCs within the limits of confidence and error stated. If the second value for "n" is significantly greater, 
EISOPQAM 5 - 12 November 2001 

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): 

Coefficient of Variation (CV)

0.1 0.5 0.65 1.0 2.0

Margin of Error (p)

0.1 4 96 162 384 1537

0.2 1 24 40 96 384

0.3 - 10 18 42 170

0.5 - 4 6 15 61

1.0 - 1 2 4 15

2.0 - - - 1 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 site 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 in 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 - 13 November 2001 

Establishment of the Grid

Having determined the number of samples to collect, the project leader should then determine how

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 grid design. Grids may also be used to determine sampling

locations when using a random design; however, with this type of design every grid 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 grid. By taking the square root of the grid area, the length

of a grid side is determined. 

 

G = (a/n)1/2

Where:

G = length per side of each individual grid

a = area

n = number of samples required

The length of a grid size should be "rounded" down to some number convenient for the method used

in laying out the grid (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 appropriate.

Grab vs Composite Samples

When designing a systematic grid 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 grid cells, and therefore, limit the representativeness of the data set. If the study involves a small

area with grid cells of 25 feet or less in length, then grab samples could be collected in each grid cell without

significantly affecting the representativeness of the data. However, most studies have much larger grids (100

to 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 grid. Composite samples are most appropriate where a

reasonable degree of variability 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

types of distribution into account is required. Situations where the distribution of contaminants is strongly

non-random (heterogeneous distributions) are the most difficult to plan for and characterize.

Composite samples should consist of five to nine aliquots per sample located on compass points

within the grid 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 grid cell. A certain number of

samples are collected (10 percent of the grid cells is often selected) during the investigation for variability

determinations based on rotating the aliquot distribution pattern on the points of the compass within the grid

cell. 
EISOPQAM 5 - 14 November 2001 

Surface vs Sub-Surface Samples

The two main 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.

5.6 Ground Water Sampling Designs

Sampling design, as it pertains to ground water, often involves the use of some form of temporary

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 waterbearing 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 downgradient 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.
EISOPQAM 5 - 15 November 2001 

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 activities, 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 serious vertical profiling problems,

however, the sampling device should be capable of identifying the presence of and determining the

thicknesses of the floating LNAPL layers. 

A more complex situation would be a single source area in which there is a dense non-aqueous phase

liquid (DNAPL) product layer with associated aqueous phase contamination. The initial part of the

investigation would be conducted in a manner similar to the simplest case. After delineation of the aqueous

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, samples should be collected from the boundary

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 flow 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.

5.6.2 Multiple-Source Area Grided Programs

Some ground water screening investigations 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-determine and establish a grid 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 locations and concentrate on other areas within the grid pattern. It may

even be appropriate to expand the area of investigation by establishing additional sampling locations. These

locations may be determined by using a grid or 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 constituents may be present, sampling should be conducted at the

surface of the confining unit to determine if product layers are present.

5.6.3 Typical Ground Water Screening Devices

Listed below are numerous tools, devices, 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 installed temporarily, either inside hollow-stem augers

or in an open hole after removal of hollow- or solid-stem augers. Because of the potential for

cross-communication between vertical intervals, this technique is appropriate only for screening

the upper portion of the saturated zone. Samples are pumped or bailed directly from the well

casing. Because turbidity is likely to be a problem using this technique, care should be taken

when using the samples for metals screening. Depth of the investigation is limited only by the

capability of the drill rig and cross-contamination considerations. See section 6.10 for

temporary well installation procedures.
EISOPQAM 5 - 16 November 2001 

 Geoprobe® -- Slotted steel pipe is hydraulically pushed or hammer driven to the desired

sampling depth. Samples are usually acquired with a peristaltic pump. The device is subject

to cross-communication at threaded rod joints. It requires some knowledge of the saturated

interval. The Geoprobe® is most useful at depths less than 30 to 40 feet below ground surface.

 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 rig 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.

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 sediment sampling

locations:

 Study objectives;

 Water use;

 Point source discharges;

 Nonpoint 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 (estuarine).

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 reference guide to conducting surface water stream studies is

F. W. Kittrells, "A Practical Guide to Water Quality Studies" (9).
EISOPQAM 5 - 17 November 2001 

Before any sampling is conducted, an initial reconnaissance should be made to locate suitable

sampling locations. Bridges and piers are normally good choices as sampling 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 not 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 estuarine 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. Estuarine environments are a special case and are discussed separately.

5.7.2 Rivers, Streams, and Creeks 

In the selection of a surface water sampling site in rivers, streams, or creeks, areas that exhibit the

greatest degree of cross-sectional homogeneity should be located. When available, previously collected data

may indicate if potential sampling locations are well mixed or vertically or horizontally stratified. Since

mixing is principally governed by turbulence and water velocity, the selection of a site immediately

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 located:

 Inside of river bends;

 Downstream from islands;

 Downstream from obstructions; and

 Areas of flow reversals, such as back-shoots.

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 time-of-water-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.
EISOPQAM 5 - 18 November 2001 

 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.

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 river. 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.
EISOPQAM 5 - 19 November 2001 

For slightly larger streams, at 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. 

For large rivers, 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 depths

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 crosscontamination.

In most circumstances, a number of sediment samples should be collected along a cross-section of

a river 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 laboratory.

Often, sediment must be collected in back-shoots or areas on the inside of bends in the stream due to scouring

in the main channel. To insure representative samples, the preferred method is diver deployed coring tubes.

5.7.3 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 river 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 river 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 grid. 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

hypolimnetic zones (above and below the thermocline or depth of greatest temperature change).
EISOPQAM 5 - 20 November 2001 

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, tributaries, land use characteristics, etc., are

suspected of influencing water quality.

When collecting sediment samples in lakes, ponds, and reservoirs, the sampling site 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

fine-grained materials. The shape, inflow pattern, bathymetry, and circulation must be considered when

selecting sediment sampling sites in lakes or reservoirs.

5.7.4 Estuarine Waters 

Estuarine 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 halocline (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 tapering

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 estuarine study unless prior knowledge

of the estuarine 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;

 Salinometer;

 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 non-point source problem, provide the focus for selecting sampling locations. More often than not,

preplanned sampling locations in estuarine areas are changed during the actual study period. Because of the

dynamics of estuaries, the initial sampling results often reveal that the study objective could be better served

by relocating, adding, or deleting sampling locations.
EISOPQAM 5 - 21 November 2001 

Water sampling in estuarine areas is normally based upon the tidal phases, with samples collected

on successive slack tides. All estuarine 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 Dorn (or similar type) horizontal sampler or peristaltic

pump are suitable.

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 halocline (salinity stratification). In that case, samples are

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, estuarine investigations are two phased, with study investigations conducted during wet

and dry periods. Depending upon the freshwater inflow sources, estuarine water quality dynamics cannot

normally be determined by a single season study.

5.7.5 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 timeof-water-travel between the stations should be sufficient to permit accurate measurement of the change in

the constituent under consideration.

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 hazardous constituents, closed

units are regarded as high hazards due to their potential to accumulate gases and vapors.

5.8.2 Waste Investigation Objectives

Systematic planning is critical for identifying a study’s objectives and conducting a successful

investigation. Thorough understanding of the waste generation/management practices is required for the

samples and associated data to reflect the waste population characteristic(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.
EISOPQAM 5 - 22 November 2001 

Common objectives in waste sampling investigations include:

 to determine if a constituent is present in a waste,

 to determine if a waste exhibits a property or characteristic,

 to determine if a material is a hazardous waste,

 to characterize a wastestream, and 

 to determine if a waste material has been released into the environment.

The most frequently used objective during RCRA Case Development/Investigation Evaluations and

Criminal Field 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 (particle 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 a liquid phase

on top of solids, a glass thief or a COmposite LIquid WAste SAmpler (COLIWASA) could be used to sample

only the liquid to determine if the phase of interest exhibits the characteristic of ignitability as described in

40 CFR, Part 261.21. 

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 in the population, and the ability to

access all portions of the population for purposes of sampling. Elements of the sampling design should

include the determination of the sample 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 sample locations are usually restricted to accessible portions of a waste unit’s population, the number

of samples to be collected is usually determined by the objective of the study. Factors to consider when

determining the appropriate number of samples are; preliminary information on the waste, the size of the

sample population, field screening results, the variability of the waste, and the budget for the investigation.

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, or to determine compliance with Land

Disposal Restrictions (LDR) treatment standards.

A small wastestream that has a hazardous constituent or characteristic randomly distributed in a

relatively homogeneous matrix requires fewer samples than a large wastestream that has a constituent or

characteristic of concern which is non-randomly distributed in a heterogeneous matrix. For a waste with

constituent of concern that is randomly distributed, an authoritative or systematic grid sampling design would

be appropriate depending on the objectives. On the other-hand, a stratified sampling or very specialized

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.
EISOPQAM 5 - 23 November 2001 

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

contaminant 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 collected 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. For a heterogeneous

waste population, it may be necessary to segregate and sample components suspected of containing

constituents of concern.

Background samples are not required when collecting highly concentrated waste samples.

5.8.4 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 while planning a sampling investigation. 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 stratify due to different densities of phases, settling

of solids, or varying waste constituents generated at different times, it also may be important to obtain a

vertical cross section of the entire unit.

Other desired features of sampling equipment that should be considered; 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 particle 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 investigations’s planning phase 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.

5.8.5 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, container labels/markings, physical characteristics, 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 when attempting to make RCRA Characteristic Waste

determinations. 
EISOPQAM 5 - 24 November 2001 

FIGURE 5-1

RCRA WASTE CHARACTERIZATION FLOW CHART
EISOPQAM 5 - 25 November 2001 

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. Sampling activities are usually conducted for National

Pollutant Discharge Elimination System (NPDES) compliance, compliance assistance, civil and criminal

investigations, and water quality studies. Collection of wastewater samples is necessary in order to aobtain

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 main considerations in developing a wastewater sampling strategy are:

 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:

 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 time for sampling activities will dictate logistical considerations (e.g., shipment

of samples, additional supplies, etc.).
EISOPQAM 5 - 26 November 2001 

5.10 UST and UIC Sampling Designs

UST Designs

The UST investigation focuses on determining whether a release from a tank(s) to the environment

has occurred and usually includes both shallow ground water and subsurface soil sampling. Usually, the

area of concern is not large, and if it is determined a release has occurred, delineation of a contaminant plume

will probably be conducted during a subsequent investigation. 

General sampling designs for soil sampling and ground water sampling are included in Section 5.5

and 5.6 of this SOP. However, specific considerations in developing a UST sampling strategy are:

 Identification of constituents in the tank.

 Identification of pollutants in ground water.

 Identification of pollutants in subsurface soil.

Complexity of the sampling program will vary based on a number of factors. Some primary factors

are as follows:

 Size of the target area (One small tank or several large tanks).

 Hydro-geological conditions of the target area.

 Accessibility to potable and ground water monitoring wells.

UIC Designs

The UIC investigation focuses on determining the quality of the ground water in a target area and

usually involves sampling ground water from deep wells. The UIC source is permitted and should have a

monitoring well network. 

General sampling designs for ground water sampling is included in 5.6 of this SOP. However,

specific considerations in developing a UIC sampling strategy are:

 Identification of constituents being injected

 Identification of pollutants in ground water.

 Delineation of 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.

 Hydro-geological conditions of the target area.

 Accessibility to potable and ground water monitoring wells.

 
EISOPQAM 5 - 27 November 2001 

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 fencelines, 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.
EISOPQAM 5 - 28 November 2001 

5.12 Data Quality Objectives

 PERFORMANCE OBJECTIVE:

 To provide guidance on systematic planning and the use of DQO Process.

 To describe the steps, the purpose and activities of DQO Process 

The US-EPA’s Quality Assurance Division has developed guidance as part of its Quality System.

One component of this Quality System is the requirement that field investigators use a systematic planning

process as mandated in EPA Order 5360.1: Policy and Program Requirements for Mandatory Agency-wide

Quality System (10), The US-EPA has developed a nonmandatory systematic planning process, the Data

Quality Objectives (DQO) Process. The DQO process is an important tool for project managers, planners,

and field investigators to define the type, quality, and quantity of data needed to make defensible decisions.

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 documents: Guidance for the Data Quality Objectives Process (1), Data

Quality Objectives Process for Hazardous Waste Sites (2), and Standard Practice for Generation of

Environmental Data Related to Waste Management Activities: Development of Data Quality Objectives (3).

The DQO process contains seven steps that will assist in preparing plans for environmental data

collection activities (Figure 5-2). The steps are iterative and should be revisited as new information about

a problem is learned. It provides a systematic approach for defining the requirements that a field

investigation will attempt to fulfill. Such requirements may include when, where and how to collect samples,

the number of samples, and the limits on tolerable error rates.

Figure 5-2. Steps of the DQO Process

1. State the Problem

2. Identify the Decision

3. Identify Inputs to the Decision

4. Define the Study Boundaries

5. Develop a Decision Rule

6. Specify Limits on Decision

7. Optimize the Design
EISOPQAM 5 - 29 November 2001 

Below are the steps, the purpose and recommended activities of DQO Process from the the US-EPA

Data Quality Objectives Process for Hazardous Waste Sites (2). 

Step 1. State the Problem

Purpose: Summarize the contamination problem that will require new environmental data, and identify

resources available to resolve the problem.

Activities: 

 Identify members of the planning team.

 Develop or refine the conceptual site model.

 Define any exposure scenarios.

 Specify the available resources and constraints.

 Write a brief summary of the contamination problem.

Step 2. Identify the Decision

Purpose: To identify the decision that requires new environmental data to address the contamination

problem.

Activities:

 Identify the principal study question(s).

 Define alternative actions that could result from the resolution of the principal study question(s).

 Combine the principal study question and the alternative actions into a decision statement.

 Organize multiple decisions.

Step 3. Identify Inputs to the Decision

Purpose: To identify information that will be required to support the decision and specify which

inputs require new environmental measurements. 

Activities:

 Identify the information that will be required to resolve the decision statement. 

 Determine the sources for each item of information identified.

 Identify the information needed to establish the action level(s).

 Confirm the appropriate analytical methods exist to provide the necessary data.

Step 4. Define the Study Boundaries

Purpose: To define the spatial and temporal boundaries that data must represent to support the

decision.

Activities:

 Specify the characteristics that define the population of interest.

 Define the geographical area which the decision statement applies.

 When appropriate, divide the population into strata that have relatively homogenous

characteristics.

 Determine the time frame to which the decision applies.
EISOPQAM 5 - 30 November 2001 

 Determine when to collect the data.

 Define the scale of the decision making.

 Identify any practical constraints on data collection.

Step 5. Develop a Decision Rule

Purpose: Develop a logical “If ..., then ...” statement that defines the conditions that would cause

the decision maker to choose among alternate actions.

Activities:

 Specify the parameter(s) that characterizes the population of interest.

 Specify the action level for the decision.

 Confirm the measurement detection limits will allow reliable comparisons with action level.

 Combine the outputs from the previous DQO steps and develop a decision rule.

Step 6. Specify Limits of Decision Errors

Purpose: To specify the decision maker’s tolerable limits on decision errors, which are used to

establish performance goals for limiting uncertainty in the data. Note that a probabilistic sampling

design is necessary to develop limits on decision errors.

Activities:

 Determine the possible range of the parameter of interest.

 Define both types of decision errors and their potential consequences and select the baseline

condition. 

 Specify a range of possible parameter values where the consequences of a false negative decsion

error are relatively minor (the gray region).

 Assign probability values to points above and below the action level that reflect the tolerable

probability for the occurrence of decision errors.

Step 7. Optimize the Design for Obtaining Data

Purpose: To identify resource-effective sampling and analysis design for generating data that are

expected to satisfy the DQO’s.

Activities:

 Review the DQO outputs and existing environmental data.

 Develop general data collection design alternatives.

 Formulate the mathematical expression necessary for each design alternative.

 Select the sample size that satisfies the DQOs for each design alternative.

 Select the most resource-effective design that satisfies all DQOs.

 Document the operational details and theoretical assumptions of the selected design in the study

plan or quality assurance project plan (QAPP).

There are several benefits of using the DQO process including; providing a reliable methodology

for clarifying how decisions about the site will be supported by environmental data and for establishing sitespecific performance criteria for these decisions. Other benefits are: it helps conserve resources by

determining which data collection and analytical methods are most appropriate, and it provides investigators

with an end-point to make defensible decisions.
EISOPQAM 5 - 31 November 2001 

The DQO process has both qualitative and quantitative components. The qualitative steps encourage

logical and practical planning for environmental data collection activities while the quantitative steps use

statistical methods to design a data collection operation that will efficiently control the probability of making

an incorrect decision. Although the quantitative steps of the DQO process are important, investigators and

decision makers may choose not to apply statistics to every environmental field investigation. In some cases,

the planning team may only utilize the qualitative steps of the DQO process during the investigation planning

phases to generate authoritative data which may be used to confirm site characteristics. 

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.

5.13.2 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 of 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 Chain-of-Custody

Specific chain-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 chain-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 crosscontaminated. 
EISOPQAM 5 - 32 November 2001 

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.

5.13.7 Special Precautions for Trace Contaminant Sampling 

Some contaminants can be detected in the parts per billion and/or parts 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.

 Sample collection activities should proceed progressively from the least suspected contaminated

area to the most suspected contaminated area.
EISOPQAM 5 - 33 November 2001 

 Investigators should use equipment constructed of Teflon®, stainless steel, or glass that has been

properly pre-cleaned (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.

5.13.8 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 that 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 pre-cleaned 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, sulfides, and phenols

analyses may not be transferred using this procedure.

It is extremely important that waste (when appropriate), soil and sediment samples be mixed

thoroughly to 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. 

5.13.9 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.
EISOPQAM 5 - 34 November 2001 

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 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 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.

Soil samples for VOC analyses should be collected and handled as specified in section 12.4. Soil

and sediment samples collected for VOC analyses should not be mixed. 

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. When appropriate, spacial

duplicate grab and/or composite samples should be collected during 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 in 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.

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 collecting twice as much material as is 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.
EISOPQAM 5 - 35 November 2001 

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 on sample tags and Chain-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 required containers are specified in section

12.4. The preparation and pick up of this sample will be the same as for the water sample VOC

trip blank. Encore® containers (two for SESD laboratory or 3 for CLP) will be transported to

the field. These field blanks 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 identified on sample tags and Chain-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 field and preserved and submitted for the same

analyses as the other inorganic samples collected. These samples will be clearly identified as

preservatives blanks on sample tags and the 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 preservative blank should be prepared in the field at the

beginning and end of all major field investigations that last more than one week.

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 organic/analyte free water. The rinse water will be collected and submitted

for analyses of all constituents for which normal samples collected with that piece of equipment

are being analyzed.

3. Organic/Analyte Free Water System Blanks -- When using a portable organic-free water

generating system in the field, a sample of the raw source water and 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.).
EISOPQAM 5 - 36 November 2001 

 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 may be submitted in the event of a special investigation (ie, criminal or civil).

 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.

5.13.11 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.

5.13.12 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.

5.13.13 Special Quality Control Procedures for Dioxins and Furans

All samples collected for dioxins and furans analyses are analyzed by other EPA laboratories or

through contract laboratories. The Region 4 laboratory does not conduct in-house analyses for dioxins and

furans. The Region 4 laboratory should be consulted for the current quality control procedures for dioxin

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.
EISOPQAM 5 - 37 November 2001 

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:

 Organic/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.

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

rinsate 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.
EISOPQAM 5 - 38 November 2001 

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 rinsate 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.

4. 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.

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 washwater.

 Packing and shipping materials.

Table 5.15.1 lists the types 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.
EISOPQAM 5 - 39 November 2001 

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, decontamination

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. 

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 containerization, 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.
EISOPQAM 5 - 40 November 2001 

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 site operator, otherwise

return to FEC for proper disposal.

Place waste in trash bag. 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 site operator, otherwise return

to FEC for proper disposal.

N/A

Soil Cuttings Containerize in 55-gallon drum with tightfitting lid. Identify and leave on-site with

permission of site operator, otherwise

arrange with WMD site manager for testing

and disposal.

Containerize in 55-gallon drum with

tight-fitting lid. Identify and leave onsite with permission of site operator,

otherwise arrange with site manager

for testing and disposal.

Groundwater Containerize in 55-gallon drum with tightfitting lid. Identify and leave on-site with

permission of site operator, otherwise

arrange with WMD site manager for testing

and disposal.

Containerize in 55-gallon drum with

tight-fitting lid. Identify and leave onsite with permission of site operator,

otherwise arrange with site manager

for testing and disposal.

Decontamination

Water

Containerize in 55-gallon drum with tightfitting lid. Identify and leave on-site with

permission of site operator, otherwise

arrange with WMD site manager for testing

and disposal.

Containerize in 55-gallon drum with

tight-fitting lid. Identify and leave onsite with permission of site operator,

otherwise arrange with site 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 site

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-site with

permission of site operator, otherwise

arrange with site manager for testing

and disposal.

Trash N/A Place waste in trash bag. Place in

dumpster with permission of site

operator, otherwise return to FEC for

disposal in dumpster.
EISOPQAM 5 - 41 November 2001 

5.16 References

1. US-EPA, Guidance for the Data Quality Objectives Process (EPA QA/G-4, EPA/600/R-96/055,

August 2000)

2. US-EPA, Data Quality Objectives Process for Hazardous Waste Sites (EPA QA/G-4HW,

EPA/600/R-00/007, January 2000)

3. ASTM, Standard Practice for Generation of Environmental Data Related to Waste Management

Activities: Development of Data Quality Objectives (D5792-95).

4. ASTM, Standard Guide for the Generation of Environmental Data Related to Waste Management

Activities: Quality Assurance and Quality Control Planning and Implementation, (D5283-92 (1997).

5. Gilbert, Richard O., Statistical Methods for Environmental Pollution Monitoring, Van Nostrand

Reinhold Co., New York, NY, 1987.

6. ASTM, Standard Guide for General Planning of Waste Sampling. 

7. US-EPA, Characterization of Hazardous Waste Sites - A Methods Manual, Volume 1 - Site

Investigations (EPA 600/4-84/075).

8. US-EPA, Guidance of Choosing a Sampling Design for Environmental Data Collection, (EPA

QA/G5-5S, Peer Review Draft, August 2000)

9. Kittrell, F.W., A Practical Guide to Water Quality Studies.

10. US-EPA Order 5360.1, Policy and Program Requirements for the Mandatory Agency-wide Quality

System, May 5, 2000.
EISOPQAM 6 - 1 November 2001

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 to 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 procedures for installing permanent monitoring wells are those that temporarily case

the borehole during drilling and the construction of the well, e.g. hollow-stem augers and sonic methods.

However, site conditions may not always be amenable to using these methods 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. 
EISOPQAM 6 - 2 November 2001

6.3 Drilling Methods

The following drilling methods are listed in general order of preference; however, final selection

should be based on actual site conditions. In all cases, 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, filter sand,

bentonite pellets, grouts, and any potable water introduced during drilling. 

6.3.1 Hollow-Stem Auger

This type of auger consists of a hollow, steel stem or shaft with a continuous, spiraled steel flight,

welded onto the exterior stem. A hollow auger bit, generally with carbide teeth, disturbs soil material when

rotated, whereupon the spiral flights transport the 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 center plug. Augering 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 augering 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 spiraled 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 semiconsolidated (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.

6.3.3 Sonic Methods.

These methods alternately advance concentric hollow drill stems using rotation in conjunction with

axial vibration of the drill stem. After each stage of drill stem advancement, the inner string is removed with
EISOPQAM 6 - 3 November 2001

a core of drill cuttings while the outer string remains to hold the borehole open. The cuttings can be removed

nearly intact from the inner casing for examination of stratigraphy prior to disposal. Because there are no

auger flights to increase the drill stem diameter, the quantity of cuttings removed from the hole is minimized

as compared to hollow stem augering. Smearing of the formation materials on the borehole walls is reduced

as well. This drilling method is useful in a variety of materials, from flowing sands to heavily consolidated

or indurated formations. 

In flowing sands, the drill casings can be filled and/or pressurized with potable water to prevent

excess entry of formation materials into the drill string. The same QA/QC requirements for sampling of

material introduced to the borehole apply as in other drilling methods. Because the amount of water

introduced into the borehole can be significant, an approximation of the water used in the drilling process

should be logged for use in estimating appropriate well development withdrawal. 

Sonic drilling allows a larger diameter temporary casing to be set into a confining layer while drilling

proceeds into deeper aquifers. This temporary casing is then removed during the grouting operation. In

many cases this will be acceptable technique. However, the level of contamination in the upper aquifer, the

importance of the lower aquifers for drinking water uses, the permeability and continuity of the confining

layer, and state regulations should be taken into account when specifying this practice as opposed to

permanent outer casing placed into the confining unit. Note that when using the temporary casing practice,

it is critical that grout be mixed and placed properly as specified elsewhere in this section. 

Because the total borehole diameter in sonic drilling is only incrementally larger than the inner

casing diameter, particular care should be taken that the well casing is placed in the center of the drill stem

while placing the filter pack. Centralizers may be required to facilitate this in the case of deep wells with

PVC casing.

6.3.4 Rotary Methods

These methods 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, (or within a concentric drill stem in reverse

rotary). 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.

Due to the introduction of the various circulating fluids, the use of rotary methods requires

that the potential for contamination by these fluids be evaluated. Water and mud rotary methods

present the possibility of trace contamination of halogenated compounds when municipal water

supplies are used as a potable water source. Air rotary drilling can introduce contamination through

the use of lubricants or entrained material in the air stream. In any of the rotary (or sonic) methods,

care must be exercised in the selection and use of compounds to prevent galling of drill stem threads.

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
EISOPQAM 6 - 4 November 2001

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

Air rotary drilling uses air as a drilling fluid to entrain cuttings and carry them to the surface. High

air velocities, and consequently large air volumes and compressor horsepower are required. ‘Down-the-hole’

(DTH) percussion hammers driven by the air stream can be used with this method to rapidly penetrate

bedrock materials. Where a casing through unconsolidated material is required to prevent borehole collapse,

it can be driven in conjunction with advancement of the drill stem. 

When using air rotary drilling in any zone of potential contamination, dual-tube reverse circulation

with a cyclone velocity dissipater for cuttings containment and separation is the preferred method. Allowing

cuttings to blow uncontrolled from the borehole (as with the conventional air rotary method) is not

acceptable.

When using air rotary, the issue of contaminants being introduced into the borehole by the air stream

must be addressed. Screw compressor systems should have a coalescing filter system in good working order

to capture excess entrained compressor oils. The lubricant to be used with ‘down-the-hole’ hammers as well

as thread lubricants to be used on drill stem should be evaluated for their potential impact on analytical

samples.

 

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, cross contamination can occur along the borehole column,

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 uncontaminated

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. QA/QC samples of drilling muds and

potable water should be sampled at a point of discharge from the circulation system to assure that pumps and

piping systems are not contributing cross-contamination from previous use.

6.3.5 Other Methods

Other methods such as the cable-tool method, jetting method, and boring (bucket auger) method are

available. If these and/or other methods are selected for monitoring well installations, they should be

approved by a senior field geologist before field work is initiated.

6.4 Borehole Construction

6.4.1 Annular Space

The borehole or hollow stem auger should be of sufficient diameter so that well construction can

proceed without major difficulties. For open boreholes, the annular space should be approximately 2" to

allow the uniform deposition of well materials around the screen and riser, and to allow the passage of tremie

pipes and well materials without unduly disturbing the borehole wall. For example, a 2" nominal diameter

(nom.) casing would require a 6" inside diameter (ID) borehole. 
EISOPQAM 6 - 5 November 2001

In hollow stem augers and sonic method drill casing, the ID should be of sufficient size to allow the

passage of the tremie pipe to be used for well grout placement, as well as free passage of filter sands or

bentonite pellets dropped through the auger or casing. In general, 4-1/4" ID should be the minimum size used

for placement of 2"nom. casing and 8-1/4" ID for 4"nom. casing. Larger augers should be used where

installation difficulties due to geologic conditions or greater depths are anticipated, e.g. larger augers might

be required to place a bentonite pellet seal through a long water column.

6.4.2 Overdrilling 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 augering 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 overdrilling. 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 sediment 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,

chips, or the filter sand that is to be used for the filter pack. 

6.4.3 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

to allow for settling and to isolate the screened interval from the grouting material. In open boreholes, the

filter pack should be placed by the tremie or positive displacement method. Placing the filter pack by

pouring the sand into an open drill stem is acceptable with the use hollow stem augers, and other methods

where the borehole is temporarily cased down to the filter pack. 

6.4.4 Filter Pack Seal-Bentonite Pellet Seal (Plug)

Bentonite pellets consist of ground, dried bentonite compacted into pellets available in several sizes.

Bentonite pellets are compressed to a bulk density of 70-80 lbs/cu.ft. and hydrate to a 30% min. solids

material. 

Where neat cement grouts are to be used, the placement of a bentonite pellet seal above the filter

pack is mandatory to prevent the possibility of grout infiltration into the screened interval prior to setting.

Bentonite chips or other sealing products should not be substituted in this application. Where bentonite

grouts are to be used, the placement of a bentonite pellet seal is optional, but desirable.

 

Since the pellets begin hydrating rapidly, they are very difficult to place by the tremie method. They

may be placed by pouring slowly into either open boreholes or hollow stem augers. A tamper should be used

to ensure that the material is being placed properly and to rapidly break up any pellet bridging that occurs.

 

Pellet seals should be designed for a two foot thickness of dry pellets above the filter pack.

Hydration may extend the height of the seal. Where neat cement grouts are to be used the pellets should be

hydrated for eight hours, or the manufacturer’s recommended hydration time, whichever is greater. Where

the water table is temporarily below the pellet seal, potable (or higher quality) water should be added

repeatedly to hydrate the pellets prior to grouting.
EISOPQAM 6 - 6 November 2001

6.4.5 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 its intended use and integrity.

 

Bentonite grout shall be a 30% solids pure bentonite grout with a minimum density of 10 lb/gal.

Drilling muds are not acceptable for grouting. 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 frost line,

whichever is the greater depth. The bentonite pellet seal or filter pack should not be disturbed during grout

placement, either by the use of a side discharge port on the tremie tube, or by maintaining clearance between

the bottom of the tremie tube and the bentonite seal or filter pack. The grout should be allowed to cure for

a minimum of 24 hours before the concrete surface pad is installed. The preferred method of achieving

proper solids content is by measurement of ingredients per the manufacturer’s specifications during mixing.

Bentonite grouts should have a minimum density of 10 lbs/gal to ensure proper gelling and low permeability.

The density of the first batch of grout should be measured while mixing to verify proper measurement of

ingredients. In addition, the grouting operation should not cease until the bentonite grout flowing out of the

borehole has a minimum density of 10 lbs/gal. A mud balance should be used to measure the specified grout

density of the bentonite grout. Estimating the grout density is not acceptable. 

 

Neat cement grouts are generally dictated where a high level of dissolved solids or a particular

dissolved constituent would prevent proper gelling of a bentonite grout. Neat 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.

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. In areas where frost heave of the surface pad is possible,

the protective casing should first be pressed into the top surface of the grout seal and concrete poured around

the protective casing. A granular material such as sand or gravel can then be used to fill the space between

the riser and protective casing. The protective casing should extend approximately 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.

At each site, all locks on the outer protective casings should be keyed alike.
EISOPQAM 6 - 7 November 2001

6.4.7 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 pad forms and into the borehole (on top of the grout) in one operation making a contiguous

unit. 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 4 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 slightly sloped so that drainage will flow away from the protective casing and off of the pad. A

minimum of one inch of the finished pad should be below grade to prevent washing and undermining by soil

erosion. 

 

6.4.8 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. Substantial steel rails and/or other steel materials can be used in place

of steel pipe. Welding bars between the bumper posts can provide additional strength and protection in high

traffic areas, but the protective bumpers should not be connected to the protective casing. 

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. Deviation from plumb should be within 1° per 50ft of depth. 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, bentonite

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 bentonite

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, bentonite 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
EISOPQAM 6 - 8 November 2001

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 (by the tremie method in open boreholes) up to the

designated depth. After the filter pack has been installed, the bentonite pellet seal (if used) should be placed

directly on top of the filter pack to an unhydrated thickness of two feet. When installing the seal for use with

neat cement grouts, the bentonite 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 frostline, whichever is the greater depth. 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.

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. Expansive sealing plugs may be used in the well riser to prevent infiltration of any water

that might enter the flush 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
EISOPQAM 6 - 9 November 2001

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 bentonite grout

for a bottom plug or seal is not acceptable, because the bentonite 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. 

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

site 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. 
EISOPQAM 6 - 10 November 2001

 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, bentonite 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

bentonite seal and the screened interval. Rubber inflatable packers have been used to place the

bentonite seal when the filter pack is omitted, but the packers have to remain in the well permanently

and, over a period of time, will decompose and possibly contribute contaminants to the monitoring

zone. 

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.

6.6.2 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 are the

preferred choice. If the monitoring program calls for the analyses of only inorganic compounds or the

contaminants or formation are highly corrosive, then rigid PVC materials meeting National Sanitary

Foundation (NSF) Standard 14 type WC (Well Casing) are acceptable. PVC materials may be acceptable

for monitoring identified organic compounds in a soluble aqueous phase where incompatibilities are known

to not exist. EPA document EPA/540/S-95/503, Nonaqueous Phase Liquids Compatibility with Materials

Used in Well Construction, Sampling, and Remediation (http://www.epa.gov/ada/download/issue/napl.pdf)

should be used for guidance in this area and in the use of PVC with Nonaqueous Phase Liquids (NAPLs).

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 field 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 (type WC)

(3) Other (where applicable)
EISOPQAM 6 - 11 November 2001

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 cases where a driven casing is used, or a high strength outer

casing is needed, carbon steel may be acceptable in non-corrosive aquifers. This outer casing should have

threaded connections. Welding casing is not an acceptable practice unless all relevant safety issues have

been adequately addressed. 

The minimum nominal casing size for most permanent monitoring wells will be 2". Where a

complete program of installation, monitoring, and abandonment is being designed, smaller wells may be

installed if suitable purging and sampling equipment for the smaller diameter wells can be specified and

obtained. 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.

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 grain-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. 

6.6.4 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, modifications to the procedures used for the design of water

well filter packs may be required. In cases where insufficient experience exists with local or similar

materials, 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. 

In formations consisting primarily of fines (silts and clays), the procedures for water well screen

design may result in requirements for filter packs and screen slot sizes that are not available. In those cases

the selection of 0.010" screen slots with a 20-40 sand filter pack, or 0.005" screen slots with 100 sand filter

pack for very fine formations, will be acceptable practice. Table 6.6.1 provides size specifications for the

selection of sand packs for fine formation materials. ASTM standard D5092, Design and Installation of

Ground Water Monitoring Wells in Aquifers, may be consulted for further guidance on specifications for

sand appropriate for these applications. 
EISOPQAM 6 - 12 November 2001

Table 6.6.1

Sand Pack Specifications

Screen

Opening

(in)

Sand

Pack

Mesh

Name

1% Passing

Size (d-1)

(in)

10% Passing

Size (d-10)

(in)

30% Passing

Size (d-30)

(in)

Derived 

60% Passing

Size (d-60)

(in)

Range for

Uniformity

Coefficient

0.005"-0.006" 100 3.5 - 4.7 5.5 - 6.7 6.7 - 8.3 8.5 - 13.4 1.3 - 2.0

0.010" 20-40 9.8 - 13.8 15.7 - 19.7 19.7 -23.6 20 - 31.5 1.1 - 1.6

The following procedure should be used in coarser grained formations.

The data from the sieve analysis are plotted on a grain-size distribution graph, and a grain-size

distribution curve is generated. From this grain-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 unity

means that the individual grain 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 grain sizes is not acceptable because the smaller particles fill the

spaces between the larger particles thereby reducing the void spaces and increasing resistance to

flow. Therefore, filter material of the same grain size and well rounded is preferred. 

4. The filter pack design is based on the gradation of the finest aquifer materials being analyzed. 

Steps to design a filter pack in aquifers:

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 (PackAquifer 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. 
EISOPQAM 6 - 13 November 2001

3. Plot the point from step 2 on the d30 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 for 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 rig(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.

Rod wipers, rather than gloves or bare hands should be used to remove mud, or other material,

from drill stem as it is withdrawn from the borehole. 

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.
EISOPQAM 6 - 14 November 2001

10. Each drill rig will have a first-aid kit and a fire extinguisher located on the rig in a location

quickly accessible for emergencies. All drilling personnel will be familiarized with their

location.

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 main 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 reestablish 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.

The following development procedures, listed in increasing order of the energy applied to the

formation materials, are generally used to develop monitoring wells:

1. Bailing

2. Pumping/overpumping

3. Surging

4. Backwashing ("rawhiding")

5. Jetting

6. Compressed air (with appropriate filtering): airlift pumping and air surging

These developmental procedures can be used, individually or in combination, in order to achieve the

most effective well development. In most cases, overpumping and surging will adequately develop the well

without imparting undue forces on the formation or well materials. 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 stressful measures may require as long as a 7-day interval before sampling. In

particular, air surge developed wells require 48 hours or longer after development so that the formation can
EISOPQAM 6 - 15 November 2001

dispel the compressed air and restabilize to pre-well construction conditions. Because of the danger of

introducing contaminants with the airstream, the possibility of entraining air in the aquifer, and the violent

forces imparted to the formation, air surging is the least desired method of development. 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 bentonite

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).

6.9.1 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-inch) wells without too much difficulty. With wells having 6-inch 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 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. 
EISOPQAM 6 - 16 November 2001

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

site 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 normally

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.

6.10.2 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 delininate contaminant plumes.

6.10.3 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.
EISOPQAM 6 - 17 November 2001

6.10.5 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 water in the

borehole, which may increase the amount of time needed to purge the well to an acceptable level of turbidity.

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-in-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.

6.10.6 Backfilling
EISOPQAM 6 - 18 November 2001

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. Likewise, where the borehole is adjacent to or, downslope

of contaminated areas, the loose backfilled material could create a high permeability conduit for the

contaminant migration. 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. 

6.11 Temporary Monitoring Well Installation Using the Geoprobe® Screen Point 15 Groundwater

Sampler

6.11.1 Introduction

The Geoprobe® Screen Point 15 Groundwater Sampler is a discrete interval ground water sampling

device that can be pushed to pre-selected sampling depths in saturated, unconsolidated materials, opened and

sampled as a temporary monitoring well. It is a sealed sample device, opened at the desired depth, yielding

a representative, uncompromised sample from that depth. Using knock-out plugs, this method also allows

for grouting of the push hole during sample tool retrieval after sample collection.

The Screen Point 15 sampler consist of four parts (drive point, screen, sampler sheath and drive

head), with an assembled length of 52 inches (1321 mm) and a maximum OD of 1.5 inches (38 mm). When

opened, it has an exposed screen length of 41 inches (1041 mm). It is typically pushed using 1.25-inch

probe rod.

The following is a step-by-step description of the components and procedures used to install a Screen

Point 15 Groundwater Sampler.

6.11.2 Assembly of Screen Point 15 Groundwater Sampler

1. Install O-ring on expendable point and firmly seat in the necked end of the sampler sheath.

2. Place a grout plug in the lower end of the screen section.

3. When using a stainless steel screen, place another O-ring in the groove on the upper end of the

screen and slide it into the sampler sheath.

4. Place an O-ring on the bottom of the drive head and thread into the top of the sampler sheath.

5. The Screen Point 15 Groundwater Sampler is now assembled and ready to push for sample

collection.

6.11.3 Installation of Screen Point 15 Groundwater Sampler

1. Attach drive cap to top of sampler and slowly drive it into the ground. Raise the hammer

assembly, remove the drive cap and place an O-ring in the top groove of the drive head. Add a

probe rod and continue push.

2. Continue to add probe rods until the desired sampling depth is reached.

3. When the desired sampling depth is reached, re-position the probe derrick and position either the

casing puller assembly or the rod grip puller over the top of the top probe rod.
EISOPQAM 6 - 19 November 2001

4. Thread a screen push adapter on an extension rod and attach sufficient additional extension rods

to reach the top of the Screen Point 15 sampler. Add an extension handle to the top of the string of

extension rods and run this into the probe rod, resting the screen push adapter on top of the sampler.

5. To expose the screened portion of the sampler, exert downward pressure on the sampler, using

the extension rod and push adapter, while pulling the probe rod upward. To expose the entire open

portion of the screen, pull the probe rod upward approximately 41 inches.

6. At this point, the Screen Point 15 Groundwater Sampler has been installed as a temporary well

and may be sampled using appropriate ground water sampling methodology. EIB personnel typically

use a peristaltic pump, utilizing low-flow methods, to collect ground water samples from these

installations (see Section 7, Ground Water Sampling, for a detailed description of these techniques

and methods).

6.11.4 Special Considerations for Screen Point 15 Installations

Grouting

In many applications, it may be appropriate to grout the abandoned probe hole where a Screen Point

15 sampler was installed. This is accomplished via pressure grouting through the probe rod during sampler

retrieval. To accomplish this, the grout plug is knocked out of the bottom of the screen using a grout plug

push adapter and a grout nozzle is fed through the probe rod, extending just below the bottom of the screen.

As the probe rod and sampler are pulled, grout is injected in the open hole below the screen at a rate that just

fills the open hole created by the pull. Teflon® grout plugs are used for all EIB investigations using this

method of abandonment.

Screen Material Selection

Screen selection is also a consideration in sampling with the Screen Point 15 sampler. The screens

are available in two materials, stainless steel and PVC. Because of stainless steel’s durability, ability to be

cleaned and re-used and overall inertness and compatibility with most contaminants, it is the choice of

materials for all EIB investigations.
EISOPQAM 6 - 20 November 2001

6.12 References

1. National Ground Water Association, Manual of Water Well Construction Practices, NGWA,

Westerville, OH

2. US-EPA, Handbook of Suggested Practices for the Design and Installation of Ground-Water

Monitoring Wells (EPA/600/4-89, March 1991)

3. ASTM, Standard Practice for Design and Installation of Ground water Monitoring Wells in Aquifers

(D5092-90).

4. Driscoll, Fletcher, Ph.D., Groundwater and Wells, Johnson Division, St. Paul, MN, 1986

5. US-EPA,Nonaqueous Phase Liquids Compatibility with Materials Used in Well Construction,

Sampling, and Remediation , (EPA/540/S-95/503, July 1995),

(http://www.epa.gov/ada/download/issue/napl.pdf)
EISOPQAM 7 - 1 November 2001

SECTION 7

GROUND WATER SAMPLING

 PERFORMANCE OBJECTIVES:

 To collect a sample representative of ground water residing in 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 its

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. 

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.
EISOPQAM 7 - 2 November 2001

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 15.5 of this SOP. Once this information is obtained, the volume of water

to be purged can be determined using one of several methods. One is the equation:

V = 0.041 d2

h 

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 volume

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 Nephelometric Turbidity Units (NTUs) (twice the Primary Drinking Water Standard of 5 NTUs).

Although ten NTUs is normally considered the minimum goal for most ground water sampling objectives,

1 NTU has been shown to be easily achievable and reasonable attempts should be made to reach this level.

Stabilization occurs when pH measurements remain constant within 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 minutes 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 (up to five well volumes), should 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. If after five well volumes, pH and conductivity have been

stabilized and the turbidity is still decreasing and approaching an acceptable level, additional purging should

be considered to obtain the best sample possible. The conditions of sampling should be noted in the field

log. 
EISOPQAM 7 - 3 November 2001

 TABLE 7.2.1

WELL CASING DIAMETER vs. VOLUME 

WELL CASING DIAMETER 9 (INCHES) vs. VOLUME (GALS.)/FEET of WATER

CASING GALLONS/FT

1 0.041

2 0.163

3 0.367

4 0.653

5 1.02

6 1.469

7 1.999

8 2.611

9 3.305

10 4.08

11 4.934

12 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.

 It is particularly important that wells be sampled as soon as possible after purging. If adequate

volume is available, the well must be sampled immediately. If not, sampling should occur as soon as

adequate volume has recovered.

Equipment Available

Monitoring well purging is accomplished by using in-place plumbing and dedicated pumps or, by

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 the 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.
EISOPQAM 7 - 4 November 2001

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.

7.2.2 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 by rinses with tap water and analyte-free water. After cleaning, it 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.

When submersible pumps (bladder, turbine, displacement, etc.) are used, the pump itself is lowered

into 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. 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.

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.
EISOPQAM 7 - 5 November 2001

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

quality 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 RediFlo2® 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.

7.2.3 Purging Techniques - Wells with In-Place Plumbing

Wells with in-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, in-place pumps. The objective of purging wells with in-place pumps is the same

as with monitoring wells without in-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 in-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 in-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 in-place plumbing under the conditions described.
EISOPQAM 7 - 6 November 2001

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.

7.2.4 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 augering, power augering, or by drilling. They may 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 Wellpoint®, 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

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 routinely achieved

by the use of low-flow purging and sampling techniques.

The following low-flow purging technique using peristaltic pumps has been used routinely to 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 approximately 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. 
EISOPQAM 7 - 7 November 2001

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, purging is not practical or possible, therefore,

no purging is conducted. The sampling device is simply pushed to the desired depth and opened and the

sample is collected and retrieved.

7.2.5 Investigation Derived Waste

Purging generates quantities of purge water or investigation derived waste (IDW), the disposition

of which must be considered. What is appropriate for the disposition of the water is, in part, dependent on

the nature of the investigation. If the IDW is generated at a RCRA facility, it will generally be contained and

disposed on site in an on-site treatment facility. IDW generated during Superfund or other investigations

may, at the discretion of the field project leader or the program manager (remedial project manager), be

discharged to the ground, away from the well, or be containerized for later disposal or other appropriate

action.

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 (turbidity meters).

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 that 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). It may be necessary to use a

secondary container, such as a clean 8 oz. sample jar or a stainless steel scoop, to obtain and transfer samples

from spigots with low ground clearance. Also, refer to the Potable Water Supply discussion in Section 2.2.

All measurements for pH, specific conductance, temperature, and turbidity should be recorded at the time

of measurement.
EISOPQAM 7 - 8 November 2001

7.3.3 Sampling Techniques - Wells without Plumbing 

Following purging, samples should be collected using a peristaltic pump/vacuum jug assembly, a

Teflon®/stainless 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 (1⁄4-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 tube 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 either

gravity drain or be reversed, by the pump, into the sample vials. (Note: When reversing the pump, make sure

the discharge tubing is not submerged in purge water. This will prevent introducing potentially crosscontaminated purge water into the sample.) 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 using the procedures described in Appendix B. Also, refer to the Potable Water Supply discussion,

Section 2.2, for additional information.

When sampling for metals only, it is also permissible to collect the sample directly from the pump

discharge tubing after an adequate purge has been demonstrated. When collecting samples in this manner

there are several considerations to be aware of. The pump head tubing (silastic, etc,) must be changed after

each well and a rinsate blank must be collected of a representative piece of the pump head tubing (only one

blank per investigation). Also, precautions must be taken to ensure that the end of the discharge tubing is

not allowed to touch the ground or other surface to ensure the integrity of the sample collected in this

manner.

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.

Bailers

When bailing, new plastic sheeting should be placed on the ground around each well to provide a

clean working area. New 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.
EISOPQAM 7 - 9 November 2001

7.3.4 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.

7.3.5 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. 

Order of Sampling with Respect to Analytes

In many situations when sampling permanent or temporary monitoring wells, an adequate purge, with

respect to turbidity, is often difficult to achieve. Removal and insertion of equipment after the purge and

prior to actual sampling may negate the low turbidities achieved during purging and elevate turbidity back

to unacceptable levels. For this reason, it is important that special efforts be used to minimize any

disturbance of the water column after purging and to collect the aliquot for metals first.

Filtering

As a 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 any

reason other than geochemical speciation modeling, the following criteria must be demonstrated to justify

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.

3. 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.
EISOPQAM 7 - 10 November 2001

4. 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, particulate-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 μm pore-size filter for the purpose of determining the colloidal constituent

concentrations. A 0.1 μm 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 to 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 grain-size distribution, concentration of colloids and colloidally-associated trace elements, and

concentration of organic matter. Therefore, consistency is critical in the comparison of short-term and longterm results. Further guidance on filtration may be obtained from the following: 1) Metals in Ground Water:

Sampling Artifacts and Reproducibility (3); 2) Filtration of Ground Water Samples 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. Further

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).

7.3.6 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.

7.3.7 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. 
EISOPQAM 7 - 11 November 2001

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 15.5. 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 batterypowered pumps, the rate should be re-checked frequently to ensure accuracy of the pumping rate

calculations.
EISOPQAM 7 - 12 November 2001

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 Metals

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 Evaluating Water 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 Monitoring 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 8 - 1 November 2001

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 pressurization

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. The smaller container should be made

of glass or stainless steel.

 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 - 2 November 2001

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 dechlorinating agent (if used).

When filling any sample container, care should be taken that no 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 chlorination.

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. 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 generally advisable to open several taps during the purge to ensure a rapid and

complete exchange of water in the tanks.

2. Purge the system for at least 15 minutes when possible. After purging for several minutes,

measure the turbidity, pH, specific conductivity, and temperature of the water. Continue to

monitor these parameters until three consistent readings are obtained. If possible, obtain three

consistent readings after the 15 minute purge.

3. After three consistent readings have been obtained, samples may be collected.
EISOPQAM 8 - 3 November 2001

8.3 Reference

1. Sampling for Organic Chemicals and Microorganisms in the Subsurface, United States

Environmental Protection Agency, EPA-600/2-77-176, 1977.
EISOPQAM 9 - 1 November 2001

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 wastewater 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. Rhodamine

WT dye (See Section 15.7 for references) may be used as an aid in determining the most representative sampling locations.

 If 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.

9.2 Site Selection

Where applicable, wastewater samples should be collected at the location specified in the NPDES

permit (if the source has 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 wastewater

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 field notes and the inspection or study report. Recommendations and reasons

for a change in sampling locations should be given to the appropriate permitting authority.
EISOPQAM 9 - 2 November 2001

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.

9.2.2 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”. 

9.2.3 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 which changes the design detention time.

9.3 Sample Types

For NPDES sampling, two types of sampling techniques are used: grab and composite. For these

procedures, the NPDES permit 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 wastewater conditions

at the time of sample collection. The sample volume depends on the type and number of analyses to be

performed. 

9.3.2 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.

Generally, a time composite is acceptable. However in enforcement cases where strict adherence to permit

requirements are necessary or if an investigator knows or suspects that there is significant variability in the

wastewater flow, a flow proportional sample is preferable .

A time composite sample consists of equal volume discrete sample aliquots collected at constant time

intervals into one container. A time composite sample can be collected either manually or with an automatic

sampler. 
EISOPQAM 9 - 3 November 2001

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 should 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, with a flow chart and an automatic sampler capable of collecting discrete samples, or

manually by compositing individual grab samples by volume versus flow chart readings. 

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 and paced 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 mls.

 The automatic sampler should be capable of providing a lift of at least 20 feet and the sample

volume should be adjustable since the volume is a function of the pumping head.

 The pumping velocity must be at least 2 ft/sec 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. 
EISOPQAM 9 - 4 November 2001

 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. 

9.4.2 Conventional Sampling (Inorganic Parameters) 

Conventional sampling includes all inorganic parameters (e.g., BOD5 , TSS, COD, nutrients) that

can be collected using an automatic sampler. 

New tubing (Silastic®, or equal, in the pump and either Teflon® 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-milliliter

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

milliliters 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. 

9.4.3 Metals

When an automatic sampler is used for collecting samples for metals analyses, the entire sampler

collection system should be rinsed with organic/analyte free water, and an equipment blank should be

collected. Approximately one-half 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).

9.4.4 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 organic/analyte free water, and

collection of appropriate blanks for organic compounds analysis. For the organic/analyte free water rinse,

approximately one-half gallons is initially pumped into the composite sample container and discarded. An

additional one and one-half gallons (approximate) 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 November 2001

9.4.5 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.

9.4.6 Automatic Sampler Maintenance, Calibration, and Quality Control

To ensure 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 in the field log book.

Prior to being used, the sampler operation should be checked to ensure proper operation by Field

Equipment Center personnel. This includes operation (forward, reverse, automatic) of at least one purgepump-purge cycle; 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 meter that activates the sampler should be checked to insure that it operates properly.

Upon returning 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 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 in-situ 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

with intermediate collection containers. If the water or wastewater stream cannot be physically reached by

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 ensure the integrity of the 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.
EISOPQAM 9 - 6 November 2001

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 ensure 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 type

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.

9.6.2 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.

9.6.3 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 ensure 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.

9.6.4 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.
EISOPQAM 9 - 7 November 2001

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.

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

facility. 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, and 8,). Completion of the Sacramento Operation of

Wastewater Treatment Plants course is highly recommended for all personnel prior to serving as the project

leader on a Diagnostic Evaluation (6).

9.8 Supplementary Data Collection

While conducting wastewater sampling, the following information will also be obtained (if

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.
EISOPQAM 9 - 8 November 2001

All observations, measurements, diagrams, etc., will be entered in bound field logbooks or attached

thereto (where applicable as specified in Section 3.5).

9.9 Sample Preservation

All sample collection and preservation procedures should comply with the requirements outlined in

40 CFR, Part 136.3 (e), Table 11 (9).
EISOPQAM 9 - 9 November 2001

9.10 References

1. NPDES Compliance Inspection Manual, United States Environmental Protection Agency,

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., October 2000. 

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. “Operation Of Municipal Wastewater Treatment Plants”, Manual Of Practice No.11, Fifth

Edition, Water Environment Federation 1996. 

8. “Design Of Municipal Wastewater Treatment Plants”, Manual Of Practice No. 8, Fourth

Edition, Water Environment Federation and ASCE, 1998.

9. 40 CFR, Part 136 (e), Table 11.
EISOPQAM 10 - 1 November 2001

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

10.2.1 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 the collection of 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.

10.2.2 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.

10.2.3 Peristaltic Pumps

Another device that can be effectively used to sample a water column, such as a shallow pond, 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 - 2 November 2001

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 tube 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.

When metals and organic compounds parameters are of concern, then a double check valve, stainless

steel bailer or Kemmerer sampler should be used to collect the sample.

10.2.5 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 checkvalve 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.

10.2.6 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 11 - 1 November 2001

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 water body, a variety of methods can be used:

 Dredges (Peterson, Eckman, Ponar), 

 Coring (tubes, augers)

 Scoops (BMH-60, standard scoop) and spoons

 Vibracore® (Electronic Vibratory Core Tube Driver)

Regardless of the method used, precautions should be taken to insure that the sample collected is

representative of the water body. These methods are discussed in the following paragraphs.

11.2 Sediment Sampling Equipment

11.2.1 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 body

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 particle size material associated with the bottom of the surface water body. Care

should be taken to minimize the loss of the fine particle sizes. 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. Again, care should be taken to minimize the loss of the fine particle sizes. The sediment is

placed into a glass pan and mixed according to Section 5.13.8 of this SOP.
EISOPQAM 11 - 2 November 2001

If the surface water body has a significant flow and is too deep to wade, a BMH-60 sampler (scoop)

may 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 readily

permit subsampling. 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.

11.2.2 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. It 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.

11.2.3 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 types

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

tubes to electronic vibrational core tube drivers.

Coring devices are particularly useful in 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 permitting 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 tube 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 - 3 November 2001

In shallow, wadeable waters, the direct use of a core liner or tube manufactured of Teflon®, 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 particle 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. Soft 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 by

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.

In deeper, non-wadeable water bodies, sediment cores may be collected from a bridge or a boat

using different coring devices such as Ogeechee Sand Pounders®, gravity cores and vibrating coring devices.

All three devices utilize a core barrel with a core liner tube system. The core liners can be removed from

the core barrel and replaced with a clean core liners, as needed, after each sample. Liners are made of either

stainless steel, Teflon or plastic. The type of core liner, and its composition, to collect sediment cores

should be based on the contaminants to be evaluated.

Ogeechee Sand Pounders® and gravity Cores are hand held devices that use a standard size 2" core

barrel. The core tube and liner are interchangeable between the two units. The Ogeechee® uses a slide

hammer mechanism attached to the core head that allows the sampler to pound the core tube into the

sediment. The Ogeechee® is good for sandy more consolidated sediments. The gravity core uses a guiding

fin mechanism with a built in gravity type check valve. The gravity core is placed in the water and released

at the surface to free fall to the bottom. The fin mechanism keeps the core tube upright and free from

spinning in the water column as it descends. The core tube stabs the bottom forcing the sediment into the

tube. Both coring devices are equipped with removable nose pieces on the core barrel and disposable core

catchers for the liner tubes. The core catchers are designed to cap the liner tube to avoid loss of the core

when retrieved from the bottom. The gravity core can be modified to attach a slide hammer mechanism,

similar to the Ogeechee®, to further pound the core into the sediment further if deemed necessary. 

Sediment cores collected from most hand operated coring devices can suffer from either spreading

or compaction when driven into the sediment, depending on the softness of the sediment. Spreading occurs

s when the sediment is pushed or moved to the side during the advancement of the core tube. Compaction

is when the sediment is being pushed downward as the core tune is advanced. Both phenomenon can effect

the physical integrity of core sample. For instance, the core tube may be advanced through the sediment to

a depth of 36 inches, but upon examination of the recovered core there is only 24 inches of sediment in the

core tube.
EISOPQAM 11 - 4 November 2001

Vibratory Core Tube Drivers (Vibracore®) facilitates sampling of soft or loosely sedimented

saturated soil deposits with minimal compaction or spreading using lined or unlined core tubes. It is designed

for use with core tubes having nominal diameters ranging from 2” to 4” OD. The Vibracore® uses an

electric motor to create vibration ranges from approximately 6,000 RPM to 8,000 RPM (100 Hz to 133 Hz)

depending on the resistance afforded by the soil; the greater the resistance, the higher the frequency. The

actual vibrational displacement of the Vibracore® is on the order of a few tens of thousandths of an inch,

so essentially no mixing of the sediment within the tube occurs. The vibrational energy tends to re-orient

the soil particles at the lower end of the core tube, causing them to move out of the way of the advancing wall

of the core tube and into a more efficient (i.e. denser) packing. This action advances the core tube with

minimal compaction of the sediment.

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 tube such as one made from aluminum, steel or stainless steel is needed to

penetrate the sediment and underlying clay or sands. A coring device can be used to collect an intact

sediment core from water bodies that have soft bottoms which allows several inches of penetration. It is

recommended that the corer have a check valve 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 in 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.

11.3 Special Considerations for Collection of Samples for Volatile Organic Compounds

Samples collected for volatile organic compound analyses must be collected prior to any sample

homogenization, as described in Section 5.13.8. Regardless of the method used for collection, the aliquot

for volatile organic compound analyses must be collected directly from the sampling device, to the extent

practical, using equipment and methods described in Section 12.4. The aliquot should be collected directly

from the device, such as a hand auger bucket or scoop, if possible. If a device such as a dredge is used, the

aliquot should be collected after the sample is placed in the mixing container prior to mixing.

In some cases, the sediment may be soft and not lend itself to collection by plunging Encore or

syringe samplers into the sample matrix. In these cases, it is appropriate to open the sample device, i.e., the

Encore barrel or syringe, prior to sample collection, and to carefully place the sediment in the device, filling

it fully with the required volume of sample.
EISOPQAM 12 - 1 November 2001

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 developing a soil sampling strategy, the appropriate equipment and techniques must be used to conduct

the investigation. This section discusses the various soil sample collection methods, sample handling, and

available sampling equipment which has been shown to be technically appropriate.

12.2 Equipment

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 soil. 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 bore

hole begins to collapse or when the soil is so tight that manual sampling is not practical.

12.2.1 Precautions for Trace Contaminant Soil Sampling

All soil sampling equipment used for sampling trace contaminants should be constructed of inert

materials such as stainless steel where possible. Pans used for mixing should be made of Pyrex® (or

equivalent) glass. In no case will chromium, cadmium, galvanized, or plated equipment be used for soil

sampling when trace levels of inorganic contaminants are of concern. Similarly, no painted or plastic

equipment may be used where trace levels of organic contaminants are of concern. Paint, scaly or heavy

rust and grease must be removed before use, most often by sandblasting the equipment. Ancillary equipment

such as auger flights may be constructed of other materials since this equipment does not come in direct

contact with the samples. The procedures outlined in Section 5.13.7 should be followed.

The procedures outlined in Section 5.13.7 should be followed.
EISOPQAM 12 - 2 November 2001

12.3 Sampling Methodology

This discussion of soil sampling methods reflects both the equipment used to 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 the friction 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.

12.3.1 Manual 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, if constructed of appropriate

materials. Spoons or hand-augers are typically used to collect surface soil samples.

If a thick, matted root zone is encountered at or near the surface, it should be removed before the

sample is collected. The collected soil is placed in a pan, thoroughly mixed, (Section 5.13.8), and placed in

the appropriate sample container(s). Section 12.4 contains specific procedures for collecting and handling

soil samples for volatile organic compounds analysis. 

Shallow Subsurface Soils

Hand augers are the most common equipment used to collect shallow subsurface samples. Typically,

4-inch auger-buckets with cutting heads are pushed and twisted into the ground, then removed as the buckets

are filled. The auger holes are advanced one bucket at a time. The practical depth of investigation using a

hand-auger depends upon the soil properties. In sand, augering is usually easily performed, but the depth

of collection is limited to the depth at which the sand begins to flow. At this depth, the bore hole will usually

collapse and cannot be advanced. Deeper sampling must be accomplished using power equipment. Handaugering may also be of limited use in tight clays or cemented sands. Regardless of the soil type, at depths

approaching 20 feet sidewall friction may become so severe that power equipment must be used.

Power augers such as the Little Beaver® may be used to advance the borehole where hand augers

are impractical. Power augers are a sampling aid, not a sampling device, and can be used to advance a

borehole to approximately 20 feet, depending upon soil conditions.

If power augers are used to advance the borehole, care must be taken that exhaust fumes, gasoline,

and\or oil do not contaminate the borehole. The soil sample may then be collected using a hand auger. After

the sample has been collected, the borehole may again be advanced (if necessary), and additional samples

collected. The auger bucket must be replaced between samples with a properly decontaminated auger bucket.

When a new borehole is advanced, the entire hand auger assembly must be replaced with a properly

decontaminated hand auger assembly.
EISOPQAM 12 - 3 November 2001

If the borehole is advanced using a hand auger, upon reaching the desired sampling depth replace

the bucket with a properly decontaminated bucket. The sample may then be collected. After the sample has

been collected, the borehole may be advanced (if necessary) with the bucket that was used to collect the

sample. Each sample must be collected using a properly decontaminated bucket.

Before the soil is placed in a pan, it is necessary to remove the top several inches of soil to minimize

the possibility of cross-contamination of the sample from fall-in of material from the upper portions of the

hole. Once the soil is placed in a pan, it is thoroughly mixed, (Section 5.13.8), and placed in the appropriate

sample container(s). Section 12.4 contains specific procedures for collecting and handling soil samples for

volatile organic compounds analysis. 

12.3.2 Powered Equipment

Powered equipment may be used to acquire soil samples from any depth (surface, shallow

subsurface, and deep subsurface). When power equipment is used to advance the borehole and collect the

sample, care must be taken that exhaust fumes, gasoline, and\or oil do not contaminate the borehole and the

sample. Among the common types of powered equipment used to collect subsurface soil samples are splitspoon samplers driven with a drill rig drive-weight assembly or pushed using drill rig hydraulics; continuous

split-spoon samplers; direct-push rigs; and back-hoes. The use of each of these is described below.

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.

Split-spoon samplers are usually driven either inside a hollow-stem auger or an open borehole after

the auger(s) have been temporarily removed. The spoon is driven with a 140-pound hammer through a

distance of up to 24 inches and removed.

Continuous split-spoon samplers may be used to obtain five-foot long, continuous samples

approximately 3 to 5 inches in diameter. These devices are placed inside a five-foot section of hollow-stem

auger and advanced with the auger during drilling. As the auger advances, the central core of soil moves into

the sampler and is retained.

Before the soil is placed in a pan, it is necessary to remove the top several inches of soil to minimize

the possibility of cross-contamination of the sample from fall-in of material from the upper portions of the

hole. Once the soil is placed in a pan, it is thoroughly mixed, (Section 5.13.8), and placed in the appropriate

sample container(s). Section 12.4 contains specific procedures for collecting and handling soil samples for

volatile organic compounds analysis. 

Direct Push Rigs

This method uses a standard split-spoon modified with a locking tip which keeps the spoon closed

during the sampling push. Upon arrival at the desired depth, the tip is remotely released and the push

continued. During the push, the released tip moves freely inside of the spoon as the soil core displaces it.

This technique is particularly beneficial at highly contaminated sites, because no cuttings are produced. The

push rods are generally retrieved with very little residue resulting in minimal exposure to sampling personnel

and reduced IDW.
EISOPQAM 12 - 4 November 2001

Before the soil is placed in a pan, it is necessary to remove the top several inches of soil to minimize

the possibility of cross-contamination of the sample from fall-in of material from the upper portions of the

hole. Once the soil is placed in a pan, it is thoroughly mixed, (Section 5.13.8), and placed in the appropriate

sample container(s). Section 12.4 contains specific procedures for collecting and handling soil samples for

volatile organic compounds analysis. 

Geoprobe® Large Bore Soil Sampler

Geoprobe® offers several tools for soil sample collection. Among these are the Macro-Core® Soil

Sampler and the large bore and dual tube soil sampling systems. The Environmental Investigations Branch

utilizes the large bore soil sampling system for collection of surface and subsurface soil samples. The

selection of this system does not preclude the use of the other systems at a future time.

The Large Bore sampler is a solid barrel, piston sealed, direct push device for collecting discrete

interval samples of unconsolidated materials at depth. The sampler is approximately 30-inches (762 mm)

long and has a 1.5-inch (38 mm) outside diameter. The Large Bore sampler is capable of recovering a

discrete sample core 22 inches x 1.0 inches (559 mm x 25 mm) contained inside a removable liner. Sample

volume measures up to 283 ml. The liner is a 24-inch long by 1.15-inch OD (610 mm x 29 mm)

removable/replaceable thin-walled tube that fits inside the Large Bore sample tube. Liners facilitate retrieval

of the sample and may be used for storage, when applicable. The Large Bore soil sampler is pushed with

1.25-inch diameter probe rod.

The following is a step-by-step description of the components and procedures used to collect a soil

sample with the Large Bore sampler.

Assembly of Large Bore Sampler

1. Select a liner tube and push on to cutting shoe (one end of liner should be slightly flared, push

this end on to shoe). 

2. Insert end of tube opposite cutting shoe into sample tube and screw cutting shoe firmly into

sample tube.

3. Thread piston tip onto piston rod then run piston assembly through the end of the sample tube

opposite the cutting shoe, seating the piston tip in the cutting shoe. There should be a short

section of exposed piston rod sticking out of sample tube.

4. Place drive head over exposed end of piston rod and thread into end of sample tube.

5. Install piston stop-pin in top of drive head. This retains the piston rod assembly during the push.

6. The Large Bore sampler is now fully assembled and ready for sample collection.

Sample Collection Using Large Bore Sampler

1. Attach assembled Large Bore sampler to end of probe rod.

2. Attach drive cap to probe rod and push rod into ground.

3. Add additional rods to push Large Bore sampler to target sampling depth.
EISOPQAM 12 - 5 November 2001

4. At the desired target sampling depth, remove the drive cap to access inside of probe rod.

5. Couple extension rods and extension rod handle together and insert into probe rod. Using

handle, turn the extension rods inside probe rod. This should engage the piston-stop pin and

remove it from the drive head attached to the top of the sample tube. Retrieve extension rods

and attached piston-stop pin.

6. Add addition probe rod, if required, reattach drive cap to top of probe rod and push probe rod

and Large Bore sampler 24 inches to fill sampler.

7. Attach pull cap and retrieve tool string.

8. When retrieved, remove the piston rod, with piston tip, and the drive head.

9. Using the Large Bore wrench, unscrew the cutting shoe from the down-hole end of the sample

tube.

10. Remove the cutting shoe and attached liner and sample from sample tube.

11. Sample has now been collected and is contained in the liner. At this time, it can be sub-sampled,

per analytical requirements.

Special Considerations for Large Bore Soil Sampling

Liner Use and Material Selection

Due to the mode of operation, the Large Bore soil sampler must be used with a liner. Liners are

available in the following materials: stainless steel, brass, cellulose acetate butyrate (CAB) and Teflon®.

For the majority of environmental investigations conducted by EIB, either CAB or Teflon® liners are used.

If samples are collected for organic compound analyses, Teflon® liners are required. CAB liners may be

used if metals or other inorganic constituents are the object of the investigation. 

Sample Orientation

When the liners and associated sample are removed from the sample tubes, it is important to maintain

the proper orientation of the sample. This is particularly important when multiple sample depths are

collected from the same push. It is also important to maintain proper orientation to define precisely what

depth an aliquot was collected from. Maintaining proper orientation is typically accomplished using vinyl

end caps. Convention is to place red caps on the top of liner and black caps on the bottom to maintain the

proper sample orientation. Orientation can also be indicated by marking on the exterior of the liner with a

permanent marker.

Back-Hoes

Back-hoes may be utilized in the collection of shallow subsurface soil samples. Samples may be

collected directly from the bucket, or the trench wall (subject to applicable safety procedures).

The bucket must be free of rust, grease, and paint. Only soil which has not been in contact with the

bucket may be sampled, unless the bucket is cleaned according to the procedures described in Appendix B

of this SOP.
EISOPQAM 12 - 6 November 2001

Trenches offer the capability of collecting samples from very specific intervals and allow visual

correlation with vertically and horizontally adjacent material. The sample should be collected without

entering the trench itself, if possible. To collect the sample without entering the trench, use a stainless steel

scoop attached to rigid electrical conduit with a scoop bracket to “dress” (remove surface layer of soil

smeared on the trench wall as the bucket passed) the wall of the trench. Replace the scoop with a

decontaminated scoop. Collect the soil.

The collected soil is placed in a pan, thoroughly mixed, (Section 5.13.8), and placed in the

appropriate sample container(s). Section 12.4 contains specific procedures for collecting and handling soil

samples for volatile organic compounds analysis

12.4 Soil/Sediment Sampling (Method 5035)

The following sampling protocol is recommended for site investigators assessing the extent of

volatile organic compounds (VOCs) in soils and sediments at a project site. Because of the large number

of options available, careful coordination between field and laboratory personnel is needed. The specific

sampling containers and sampling tools required will depend upon the detection levels and intended data use.

Once this information has been established, selection of the appropriate sampling procedure and preservation

method best applicable to the investigation can be made. 

12.4.1 Equipment

Soil\sediment for VOC analyses may be retrieved using the equipment specified in Sections 11 and

12 of this SOP. Once the soil\sediment has been obtained, the EnCoreTM VOC sampler, syringes, stainless

steel spatula, standard 2 oz soil VOC container, or pre-prepared 40 mL vials may be used/required for subsampling collection. The specific sample containers and the sampling tools required will depend upon the

data quality objectives established for the site or sampling investigation. The various methods are described

below.

12.4.2 Sampling Methodology - Low Concentrations

When total VOC concentrations in the soil/sediment are expected to be less than 200 g/kg, the

samples may be collected directly with the EnCoreTM sampler or syringe. If using the syringes, the sample

must be placed in the sample container (40 ml pre-prepared vial) immediately to reduce volatilization losses.

The 40 ml vials should contain 10 ml of organic free water for an un-preserved sample or approximately 10

ml of organic free water and a preservative. It is recommended that the 40 ml vials be prepared and weighed

by the laboratory (commercial sources are available which supply preserved and tared vials). When sampling

directly with the EnCoreTM sampler, the vial must be immediately capped.

A soil/sediment sample for VOC analysis may also be collected with conventional sampling

equipment (as described in Sections 11 and 12 of this SOP). A sample collected in this fashion must either

be placed in the final sample container (EnCoreTM or 40 ml pre-prepared vial) immediately or the sample may

be immediately placed into an intermediate sample container with no head space. If an intermediate

container (usually 2 oz. soil jar) is used, the sample must be transferred to the final sample container

(EnCoreTM or 40 ml pre-prepared vial) as soon as possible not to exceed 30 minutes.
EISOPQAM 12 - 7 November 2001

NOTE: After collection of the sample into either the EnCoreTM Sampler or other container, the sample must

immediately be stored in an ice chest and cooled.

Soil\sediment samples may be prepared for shipping and analysis as follows:

EnCoreTM Sampler - the sample may simply be capped, locked and secured in a plastic bag.

Syringe - Add about 3.7 cc (approximately 5 grams) of sample material to 40 ml pre-prepared

containers. Secure the containers in a plastic bag. Do not use a custody seals on the container,

place the custody seal on the plastic bag. Note: When using the syringes, it is important that no air

is allowed to become trapped behind the sample prior to extrusion, as this will adversely affect the

sample.

Stainless Steel Laboratory Spatulas - Add between 4.5 and 5.5 grams (approximate) of sample

material to 40 ml containers. Secure the containers in a plastic bag. Do not use a custody seal on

the container, place the custody seal on the plastic bag.

12.4.3 Sampling Methodology - High Concentrations

Based upon the data quality objectives and the detection level requirements, this high level method

may also be used. Specifically, the sample may be packed into a single 2-oz. glass container with a screw

cap and septum seal. The sample container must be filled quickly and completely to eliminate head space.

Soils\sediments containing high total VOC concentrations may also be collected as described in Section

12.4.2, and preserved using 10 ml methanol. 

12.4.4 Waste Samples

Collect an un-preserved sample into a single 2 – oz glass container. Handle waste samples in

accordance with Section 14 of this SOP.

12.4.5 Special Techniques and Considerations

Effervescence

If low concentration samples effervesce from contact with the acid preservative, (see Sec. 12.4.2)

then either a test for effervescence must be performed prior to sampling, or the investigators must be

prepared to collect each sample both preserved or un-preserved as needed, or all samples must be collected

un-preserved.

To check for effervescence, collect a test sample and add to a pre-preserved vial. If preservation

(acidification) of the sample results in effervescence (rapid formation of bubbles) then preservation by

acidification is not acceptable, and the sample must be collected un-preserved.

If effervescence occurs and only pre-preserved sample vials are available, the preservative solution

may placed into an appropriate hazardous waste container and the vials triple rinsed with organic free water.

 An appropriate amount of organic free water, equal to the amount of preservative solution, should be placed

into the vial. The sample may then be collected as an un-preserved sample. Note that the amount of organic

free water placed into the vials will have to be accurately measured.
EISOPQAM 12 - 8 November 2001

Sample Size

While this method is an improvement over earlier ones, field investigators must be aware of an

inherent limitation. Because of the extremely small sample size, sample representativeness for VOC’s may

be reduced compared to samples with larger volumes collected for other constituents . The sampling design

and objectives of the investigation should take this into consideration. 

Holding Times

Sample holding times are specified in Appendix A. Field investigators should note that the holding

time for an un-preserved VOC soil/sediment sample is 48 hours. Arrangements should be made to ship the

soil/sediment VOC samples to the laboratory by overnight delivery the day they are collected so the

laboratory may preserve and\or analyze the sample within 48 hours of collection.

Percent Moisture

Samplers must ensure that the laboratory has sufficient material to determine percent moisture in the

VOC soil/sediment sample to correct the analytical results to dry weight. If other analyses requiring percent

moisture determination are being performed upon the sample, these results may be used. If not, a separate

sample (minimum of 2 oz.) for percent moisture determination will be required.

Safety

Methanol is a toxic and flammable liquid. Therefore, methanol must be handled with all required

safety precautions related to toxic and flammable liquids. Inhalation of methanol vapors must be avoided.

Vials should be opened and closed quickly during the sample preservation procedure. Methanol must be

handled in a ventilated area. Use protective gloves when handling the methanol vials. Store methanol away

from sources of ignition such as extreme heat or open flames. The vials of methanol should be stored in a

cooler with ice at all times.

Shipping

Methanol and sodium bisulfate are considered dangerous goods, therefore shipment of samples

preserved with these materials by common carrier is regulated by the U.S. Department of Transportation and

the International Air Transport Association (IATA). The rules of shipment found in Title 49 of the Code of

Federal Regulations (49 CFR parts 171 to 179) and the current edition of the IATA Dangerous Goods

Regulations must be followed when shipping methanol and sodium bisulfate. Consult the above documents

or the carrier for additional information. Shipment of the quantities of methanol and sodium bisulfate used

for sample preservation falls under the exemption for small quantities. A summary of the requirements for

shipping samples follows. Refer to the code for a complete review of the requirements.

1. The maximum volume of methanol or sodium bisulfate in a sample container is limited to

thirty30) mls.

2. The sample container must not be full of methanol.

3. The sample container must be stored upright and have the lid held securely in place. Note that

the mechanism used to hold the cap in place must be able to be completely removed so weight

is not added to the sample container, as specified in Method 5035.

4. Sample containers must be packed in a sorbent material capable of absorbing spills from leaks

or breakage of the sample containers.
EISOPQAM 12 - 9 November 2001

5. The maximum sample shuttle weight must not exceed 64 pounds.

6. The maximum volume of methanol or sodium bisulfate per shipping container is 500 mls.

7. The shipper must mark the sample shuttle in accordance with shipping dangerous goods in

acceptable quantities.

8. The package must not be opened or altered until no longer in commerce.

12.4.6 Summary

The following summary table lists the options available for compliance with SW846 Method 5035.

The advantages and disadvantages are noted for each option. SESD’s goal is to minimize the use of

hazardous material (methanol and sodium bisulfate) and minimize the generation of hazardous waste during

sample collection.

OPTION PROCEDURE ADVANTAGES DISADVANTAGES

1 Collect 2 - 40 mL vials with ~5

grams of sample and 1 - 2 oz.,

glass w/septum lid for screening

and % moisture

Screening conducted by

lab

Presently a 48 hour

holding time for

unpreserved samples

2 Collect 3 EncoreTM; and 1- 2 oz.,

glass w/septum lid for screening

and % moisture

Lab conducts all

preservation/preparation

procedures

Presently a 48 hour

holding time for

preparation of samples

3 Collect 2 - 40 ml vials with 5

grams of sample and preserve

w/methanol or sodium bisulfate

and 1 - 2-oz., glass w/septum lid

for screening and % moisture

High level VOC samples

may be composited

Longer holding time

Hazardous materials 

used in field

4 Collect 1 - 2-oz., glass w/septum

lid for analysis and % moisture

Lab conducts all

preservation/preparation

procedures

May have significant

VOC loss 
EISOPQAM 13 - 1 November 2001 

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 260-265. 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

that 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. 

Sampling equipment contaminated during waste sampling investigations should be 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 5.15 and should

be specified in the site-specific study plan.

13.1.2 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. 

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.
EISOPQAM 13 - 2 November 2001 

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, (PPE) 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. 

13.2.1 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 Part 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 holding, storage, settling and aeration pits, ponds, and lagoons."

One of the distinguishing features between waste piles and surface impoundments is the state of the

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.).

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. 

13.2.2 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 in an attempt

to characterize the unit. The following are definitions of types of closed waste units described in 40 CFR

Part 260.10: 
EISOPQAM 13 - 3 November 2001 

 Container -- any portable device in which a material is stored, transported, treated, disposed, or

otherwise handled. Examples of containers are drums, overpacks, pails, totes, and roll-offs. 

 Tank -- a stationary device, designed to contain an accumulation of hazardous waste which is

constructed primarily of non-earthen materials which provide structural support. 

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. 

 Ancillary equipment (tank) -- 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

hazardous waste from its point of generation to a storage or treatment tank(s), between

hazardous waste storage and treatment tanks to a point of disposal on-site, or to a point of

shipment for disposal off-site.

 Sump -- any pit or reservoir that meets the definition of a tank and those troughs/trenches

connected to it that serve to collect hazardous 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 (PPE) is suitable for the site conditions. 

Samples collected from different waste units should not be composited into one sample container

without additional analytical and/or field screening data to determine if the materials are compatible and will

not cause an inadvertent chemical reaction.

13.3 Equipment

Selecting appropriate equipment to sample wastes is a challenging task due to 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

characteristics 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 some waste units, 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. 
EISOPQAM 13 - 4 November 2001 

13.3.1 Waste Sampling Equipment

Waste sampling equipment should be made of non-reactive materials that will neither add to nor 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.

Another reference for selecting sampling equipment is the ASTM, Standard Guide for Selection of Sampling

Equipment for Wastes and Contaminated Media Data Collection Activities, D 6232-98.

13.3.2 Ancillary Equipment for Waste Sampling

In addition to the equipment listed in Table 13.3.1 which provides the primary device used to collect

various waste samples, ancillary equipment 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 that these types of ancillary equipment may have on the data should be evaluated and reported as

necessary.
EISOPQAM 13 - 5 November 2001 

TABLE 13.3.1

SAMPLING EQUIPMENT for VARIOUS WASTE UNITS

Equipment Waste Units/Phases Limitations

scoop with

bracket/conduit 

impoundments, piles,

containers, tanks/liquids,

solids, sludges

Can be difficult to collect deeper phases in

multiphase wastes. Depth constraints. 

spoon impoundments, piles,

containers/solids, sludges

Similar limitations as the scoop. Generally

not effective in sampling liquids.

push tube piles, containers/cohesive

solids, sludges 

Should not be used to sample solids with

dimensions >1⁄2 the diameter of the tube. 

Depth constraints.

auger impoundments, piles, containers/solidsCan be difficult to use in an impoundment or

a container, or for solidified wastes.

sediment sampler impoundments, piles/

solids, sludges

Should not be used to sample solids with

dimensions >1⁄2 the diameter of the tube.

ponar dredge impoundments/solids,

sludges

Must have means to position equipment to

desired sampling location. Difficult to decon.

COLIWASA or drum

thief

impoundments, containers,

tanks/liquids

Not good with viscous wastes. Devices 7'

require 2 samplers to use effectively.

DipstickTM /

MucksuckerTM 

impoundments, containers,

tanks/liquids, sludges 

Not recommended for tanks >11 feet deep.

Devices 7' require 2 samplers to use

effectively.

bacon bomb impoundments, tanks/

liquids

Not good with viscous wastes.

bailer impoundments, tanks/

liquids

Only if waste is homogeneous. Not good

with viscous wastes.

peristaltic pump

with vacuum jug

assembly

impoundments, tanks/

liquids

Cannot be used in flammable atmospheres.

Not good with viscous wastes.

back-hoe bucket piles/solids, sludges May be difficult to access desired sampling

location. Difficult to decon. Can lose

volatiles. 

split-spoon piles/solids Requires drill rig or direct push equipment.

roto-hammer piles, containers/solids Physically breaks up sample. May release

volatiles. Not for flammable atmospheres.
EISOPQAM 13 - 6 November 2001 

13.4 Waste Sampling Procedures

13.4.1 Waste Piles

Waste piles vary in 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. 

13.4.2 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 13.3.1. 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).

13.4.3 Drums

Drums are the most frequent type of containers sampled by field investigators for chemical analyses

and/or physical testing. 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:

 pressurization (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 accessibility.

Drums showing evidence of pressurization and crystals should be furthered assessed to

determine if remote drum opening is needed. If drums cannot be accessed for sampling, heavy

equipment is usually 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 - 7 November 2001 

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 in

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, Drum Data Form or Drum Data Table. 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 meet the

study’s objective(s). 

7. Place oil wipe (as necessary), 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 COLIWASA 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 container. 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 container(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 5.15, and Region 4's Contaminated Media Policy. 
EISOPQAM 13 - 8 November 2001 

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:

1) OVERPACK: 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 / 3⁄4 / 1⁄2 / 1⁄4 / EMPTY

5) PHYSICAL APPEARANCE OF DRUM CONTENTS:

COLOR: VISCOSITY: LOW / MED / HIGH

PHASED: Y / N ; DESCRIPTION: 

OTHER: 

6) AIR MONITORING RESULTS:

PID ppm EXPLOS _____%O2 %LEL 

FID ppm HALOGEN Yes No 

CN ppm pH 

RAD Mrem 

7) FLASH POINT SAMPLE COLLECTED: YES / NO

FLASH RESULTS AT 140o

F: YES / NO

HOT WIRE TEST FOR HALOGEN: POS / NEG

8) SAMPLE COLLECTED: YES / NO TIME: 

COLLECTOR(S): 
EISOPQAM 13 - 9 November 2001 

13.4.4 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 compartmentalized 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 valving 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 meet the

study’s objective(s). 

8. Place oil wipe (as necessary), sampling equipment, and sample containers near tanks(s) to be

sampled.
EISOPQAM 13 - 10 November 2001 

AIR MONITORING FOR TOXIC VAPORS, EXPLOSIVE GASES AND OXYGEN

DEFICIENT ATMOSPHERES SHOULD BE CONTINUOUS DURING TANK SAMPLING.

Liquids -- Slowly lower the bailer, bacon bomb, DipstickTM, 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 container. Repeat the procedure until a

sufficient sample volume is obtained.

Solids/Semi-Solids - Use a push tube, bucket auger, screw auger, MucksuckerTM, 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

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, and Region 4's Contaminated Media Policy.

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, smooth 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 a solvent; methylene chloride, hexane,

isopropanol or analyte free water depending on the parameters to be analyzed. The laboratory performing

the analyses can provide the appropriate solvent. 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. Typically, 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 goal is to systematically wipe the whole

area. The wipe is then folded with the sample side inward and 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 wipe 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 pan as

specified in Section 5.13.8. The shredded, homogenized material is then placed in sample containers. 
EISOPQAM 13 - 11 November 2001 

13.6 Waste Sample Handling Procedures

When collecting samples of concentrated wastes for laboratory analyses, field personnel are required

to screen the waste materials to ensure safe handling and transportation of the samples. Safety procedures,

sampling and screening methods used to collect the samples must comply with those procedures/methods

described in this manual. It should be noted that waste samples should not be preserved because of the

potential for an inadvertent chemical reaction with the preservative. Additionally, concentrated waste

samples are not required to be cooled to 4C.

After samples have been collected and containerized, the outside of the sample containers should

be cleaned with water, paper towels and/or oil wipes to remove any spilled material from the exterior of the

container. It should be noted that each sample container should be tagged and sealed, placed in a plastic bag,

and the bag securely closed. Samples collected from materials that did not demonstrate any hazardous

characteristics during the screening process may be placed in coolers and handled as non-hazardous samples

in accordance with Appendix A.

Field investigators will use knowledge gained of site practices and processes, labels and marking on

waste containers, field screening results, and personal observations made during their investigation to

determine the hazard potential of a sample. Samples considered to be hazardous by the field investigators

will be placed in secondary containment for transport to the SESD laboratory and for subsequent handling

upon arrival. The tagged, sealed and bagged samples will be placed in a 6-quart plastic pail, packed with

vermiculite, and sealed with a tight fitting lid. The project number for the sampling investigation and the

specific sample station number will be marked on the secondary container in indelible ink. A standard SESD

Hazard Communication Label will be affixed to the side of the secondary container. The appropriate

hazard(s) for the sample (Health, Flammability, and/or Reactivity) will be indicated with an “X”.

Additionally, an “X” will be placed in the “Protective Equipment” section.

All secondary containing pails will be secured in the vehicles while transporting the samples from

the field to the laboratory for analyses. In addition, each pail should indicate when protective equipment is

recommended to handle the actual waste/sample material.

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 particle 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 chain-ofcustody 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. 
EISOPQAM 13 - 12 November 2001 

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 the 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 - 13 November 2001 

13.8 REFERENCES

1. Title 40 Code of Federal Regulations, Parts 260-265, US-EPA, July 1, 2000.

2. ASTM, Standard Guide for Selection of Sampling Equipment for Wastes and Contaminated

Media Data collection Activities, D 6232-98, 1998.

3. ASTM, Standard Guide for Sampling Stategies for Heterogeneous Wastes, D 5956-96, 1996.

 

4. Test Methods for Evaluating Solid Waste - Physical/Chemical Methods (SW-846), Third

Edition, Draft Update IVB, US-EPA, Office of Solid Waste and Emergency Response,

Washington, D.C., November, 2000.

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 1 -Site 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.

8. Federal Register,Volume: 55, Issuse 26, Page: 26990, Friday, June 29, 1990. 
EISOPQAM 14 - 1 November 2001

SECTION 14

AMBIENT AIR MONITORING

 PERFORMANCE OBJECTIVE:

  To present the standard operating procedures and sample collection methodologies for

conducting air monitoring in ambient air.

  To collect an air sample that is representative of conditions as they existed at the site. 

  To Take measures to avoid introducing contamination as a result of poor sampling and/or

 handling technique.

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. Criteria pollutants mean air pollutants which National Ambient Air

Quality Standards have been established.

14.2 Criteria Pollutant Monitoring (Reference/Equivalent 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 System, Volume II: Part 1, Ambient Air Quality Monitoring

Program, Quality System Development, US EPA, Office of Air Quality Planning and Standards, Research

Triangle Park, NC, (commonly referred to as the "Red Book.").

 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 (25oC and 760 mm Hg).

 Chain-of-custody must be maintained at all times.
EISOPQAM 14 - 2 November 2001

Monitoring Procedure

Monitoring will be conducted using the procedure as described, and in accordance with 40 CFR Part

50, APPENDIX A:

 Procedures detailed in the approved instrument manual will be used for installation, calibration,

QA checks, maintenance, and repairs. 

 Monitors will be calibrated at the beginning and end of each study, and at least quarterly during

the study. Calibration procedures detailed in the approved instrument manual will be used for

all calibrations. 

 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 Part 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 inspection, maintenance,

and repair prior to storage. All field documentation will be retained by the Air Monitoring Staff. 

14.2.2 Monitoring Carbon Monoxide in Ambient Air

The following is a synopsis of procedures which should be strictly adhered to for the monitoring of

carbon monoxide in air. This summary is adapted from 40 CFR Part 50, Appendix C - Measurement Principle

and Calibration Procedure for The Measurement of Carbon Monoxide in The Atmosphere (Non-Dispersive

Infrared Photometry), and The Quality Assurance Handbook for Air Pollution Measurement System, Volume

II: Part 1, Ambient Air Quality Monitoring Program, Quality System Development, US EPA, Office of Air

Quality Planning and Standards, Research Triangle Park, NC, (commonly referred to as the "Red Book.").

 Calibration systems will meet 40 CFR Part 50, Appendix C specifications. 

 Calibration systems will be verified/calibrated before use in accordance with procedures detailed

in the calibration instrument manual. 

 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/authoritative standard. Flows will be

corrected to EPA standard temperature and pressure (25oC and 760 mm Hg).

 Chain-of-custody must be maintained at all times.
EISOPQAM 14 - 3 November 2001

Monitoring Procedure

Monitoring will be conducted using the procedure as described, and in accordance with 40 CFR Part

50, APPENDIX C:

 Procedures detailed in the approved instrument manual will be used for installation, calibration,

quality assurance (QA) checks, maintenance, and repairs. 

 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 QA check shows an out-ofcontrol 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 Part 58, Appendix A will be conducted

quarterly, or at least once for short duration studies.

 Data telemetry systems not equipped with electronic strip chart capability will be run in parallel

with strip chart recorders. Strip charts (electronic or paper) will serve as a permanent record and

diagnostic tool. 

After completion of the study, all monitoring equipment will be returned for inspection, maintenance,

and repair prior to storage. All field documentation will be retained by the Air Monitoring Staff. 

14.2.3 Monitoring Nitrogen Dioxide in Ambient Air

The following is a synopsis of procedures which should be strictly adhered to for the monitoring of

carbon monoxide in air. This summary is adapted from 40 CFR Part 50, Appendix F - Measurement Principle

and Calibration Procedure for The Measurement of Nitrogen Dioxide in The Atmosphere (Gas Phase

Chemiluminescence), and The Quality Assurance Handbook for Air Pollution Measurement System,

Volume II: Part 1, Ambient Air Quality Monitoring Program, Quality System Development, US EPA, Office

of Air Quality Planning and Standards, Research Triangle Park, NC, (commonly referred to as the "Red

Book.").

 Calibration systems will meet 40 CFR Part 50, Appendix F specifications. 

 Calibration systems will be verified/calibrated before use in accordance with procedures detailed

in the calibration instrument manual.

 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/authoritative standard. Flows will be

corrected to EPA standard temperature and pressure (25oC and 760 mm Hg).

 Chain-of-custody must be maintained at all times.
EISOPQAM 14 - 4 November 2001

Monitoring Procedure

Monitoring will be conducted using the procedure as described, and in accordance with 40 CFR Part

50, APPENDIX F.

 Procedures detailed in the approved instrument manual will be used for installation, calibration,

quality assurance (QA) checks, maintenance, and repairs. 

 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 QA check shows an out-ofcontrol 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 Part 58, Appendix A will be conducted

quarterly, or at least once for short duration studies.

 Data telemetry systems not equipped with electronic strip chart capability will be run in parallel

with strip chart recorders. Strip charts (electronic or paper) will serve as a permanent record and

diagnostic tool. 

After completion of the study, all monitoring equipment will be returned for inspection, maintenance,

and repair prior to storage. All field documentation will be retained by the Air Monitoring Staff. 

14.2.4 Monitoring Sulfur Dioxide in Ambient Air

The following is a synopsis of procedures which should be strictly adhered to for the continuous

monitoring of sulfur dioxide in air. This summary is adapted from the Federal Register equivalent method

designation, 40CFR Part 53, and The Quality Assurance Handbook for Air Pollution Measurement System,

Volume II: Part 1, Ambient Air Quality Monitoring Program, Quality System Development, US EPA, Office

of Air Quality Planning and Standards, Research Triangle Park, NC. (commonly referred to as the "Red

Book.").

 Calibration systems will meet Federal Register equivalent method specifications. 

 Calibration systems will be verified/calibrated before use in accordance with procedures detailed

in the calibration instrument manual.

 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/authoritative standard. Flows will be

corrected to EPA standard temperature and pressure (25oC and 760 mm Hg).

 Chain-of-custody must be maintained at all times.
EISOPQAM 14 - 5 November 2001

Monitoring Procedure

Monitoring will be conducted using the procedure as described, and in accordance with Federal

Register equivalent method specification.

 Procedures detailed in the approved instrument manual will be used for installation, calibration,

quality assurance (QA) checks, maintenance, and repairs. 

 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 QA check shows an out-ofcontrol 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 Part 58, Appendix A will be conducted

quarterly, or at least once for short duration studies.

 Data telemetry systems not equipped with electronic strip chart capability will be run in parallel

with strip chart recorders. Strip charts (electronic or paper) will serve as a permanent record and

diagnostic tool. 

After completion of the study, all monitoring equipment will be returned for inspection, maintenance,

and repair prior to storage. All field documentation will be retained by the Air Monitoring Staff. 

14.2.5 Sampling of Particulate Matter in Ambient Air as PM2.5

The following is a synopsis of procedures which should be strictly adhered to for the sampling

of particulate matter as PM2.5 in air. This summary is adapted from 40 CFR Part 50, Appendix L- Reference

Method For the Determination of Fine Particulate Matter as PM2.5 in the Atmosphere, EPA Implementation

Plan: PM2.5 Federal Reference Method Performance Evaluation Program, EPA Quality Assurance Guidance

Document 2.12, EPA Quality Assurance Document: Quality Assurance Project Plan for the Performance

Evaluation Program, EPA Quality Assurance Guidance Document: Method Compendium, Field Standard

Operating Procedures for the PM2.5 Performance Evaluation Program, and EPA Quality Assurance

Document: Method Compendium, PM2.5 Mass Weighing Laboratory Standard Operating Procedures for the

Performance Evaluation Program. These documents are available in hardcopy format and as a PDF file on

the Ambient Monitoring Technology Information Center (AMTIC) Internet Bulletin Board under the PM2.5

QA area (http://www.epa.gov/ttn/amtic/pmqa.html).

• EPA, OAQPS National Filter Distribution Program will send filters to the Regions 4 East Coast

PM2.5 Filter Weighing Laboratory

• Prior to use the filters will be checked for deformities, equilibrated at 20 - 23C ± 2C and 30 -

40 % ± 5 % relative humidity for a minimum of 24 hours, labeled, pre-weighed ( auto-entry into

PEP database), loaded into cassettes, and prepared for packaging and shipping.

• Region 4 Filter Weighing Laboratory will ship the pre-weighed filters and chain-of- custody

(COC) forms to the field scientists in Regions 1, 2, 3, 6, and 10.
EISOPQAM 14 - 6 November 2001

• Filters and COC forms for Region 4 are passed directly to the field scientists

• After sampling, filters will be transported to the Filter weighing Laboratory, logged into the

database, refrigerated until a batch is completed, moved to the laboratory, unloaded from the

cassettes, equilibrated for at least 24 hours, and post-weighed.

• Region 4 East Coast Filter Weighing Laboratory will equilibrate and weigh the exposed filters,

validate data, and upload information to AIRS.

• Chain-of-custody must be maintained for all samples.

Sample Collection

Samples will be collected using the following:

• Field scientists will take the filters, field data sheets, and COC to the State/local agency

monitoring site and setup the portable samplers.

• Air flow, barometric pressure and two temperature measuring devices will be verified prior to

each sampling event. All flow, barometric pressure and temperature standard devices are

annually calibrated and traceable to a primary standard.

• Internal and external leak checks will be performed.

• Within 8 to 16 hours following the sampling event the exposed filters will be collected and

prepared for transport to the Filter Weighing Laboratory.

• Field scientists will return the exposed filter, data diskettes, field data sheets and COC to the

appropriate laboratory (as well as keep a set of the data records).

After sample collection, all filters will be stored in petri-slides, boxed, and archived for one (1)

year at  4C and two (2) years at ambient room temperature  25C.

14.2.6 Sampling of Particulate Matter in Ambient Air as PM10

The following is a synopsis of procedures which should be strictly adhered to for the sampling of

particulate matter as PM10 in air. This summary is adapted from 40 CFR Part 50, Appendix J - Reference

Method for The Determination of Particulate Matter as PM10 In the Atmosphere, and The Quality Assurance

Handbook for Air Pollution Measurement System, Volume II: Part 1, Ambient Air Quality Monitoring

Program, Quality System Development, US EPA, Office of Air Quality Planning and Standards, Research

Triangle Park, NC, (commonly referred to as the "Red Book.").

 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 15o

C - 30oC ± 3oC, 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 re-weighed as a quality assurance check. For batches less than ten, one

filter will be re-weighed.
EISOPQAM 14 - 7 November 2001

 After sampling, filters will be desiccated as previously described.

 Chain-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, and Red Book Sections 2.10, and 2.11.

 All flow calibration orifices will be traceable to a primary standard Rootsmeter. Flows will be

corrected to EPA standard temperature and pressure (25oC 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 PM10 samplers. Flows will be determined using

a calibrated orifice and a digital manometer. 

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 and a calibrated orifice.

 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 Chain-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 transport to the Region 4 laboratory for final weighing

of filters.

14.3 Non-Criteria Pollutant Monitoring for Air pollutants for which National Ambient Air Quality

Standards have not been established.

14.3.1 Formaldehyde Sampling With Dinitrophenylhydrazine Cartridges Using Method TO-11A

The following is a synopsis of procedures which should be strictly adhered to for the handling and

field use of dinitrophenylhydrazine (DNPH) cartridges for formaldehyde sampling. This summary is adapted

from METHOD TO-11A 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, latex, 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).
EISOPQAM 14 - 8 November 2001

 All padding material shall be either clean tissue paper or polyethylene-air bubble padding.

Never use polyurethane foam, cardboard, or newspaper as padding material. DNPH cartridges

which have been properly prepared for shipment should be shipped in coolers with eutectic salt

packs (Blue Ice).

 Chain-of-custody shall be maintained for all samples.

 A minimum of one trip blank shall be transported per one to ten samples collected.

Due to shelf life limitations, only the number of DNPH cartridges needed for a maximum of 180

days (including trip blanks and extra DNPH cartridges for breakage) should be ordered at any one

time.

 On the date of shipment or when loading out for a study, the Air Monitoring Staff will remove

the capped DNPH cartridges from the refrigerator in the Air Laboratory.

 An appropriate amount of packing material shall be placed in the shipping container to prevent

breakage of the glass DNPH tubes. The DNPH tubes should be shipped in coolers containing

eutectic salt packs (e.g., Blue Ice) to maintain a temperature of approximately 4oC. The DNPH

cartridges shall be shipped the same day they are packed.

 At each sampling location the cooler will be opened and one plugged DNPH cartridge will be

removed (wearing clean polyethylene, latex, or nylon gloves) and the two end plugs will be

removed from each end of the DNPH cartridge which will be immediately placed on the

sampling train. (If it is the SKC brand, the glass ends of the tubes must be broken off. A trip

blank will be placed in a sampler enclosure at one of the sites for the duration of the sampling

event.

The sampler will be manually turned on and allowed to run for five 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 five 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 train (wearing clean

polyethylene, latex or nylon gloves). The two end caps will be placed on the ends of the DNPH

cartridge. The DNPH cartridge will be placed back into the cooler. The same procedure is to

be followed at each sampling site. 

 At the end of each day on which the samples are collected, the exposed DNPH cartridges shall

be either placed in a refrigerator for storage overnight or stored in the cooler. The cooler will

be used to transport the samples to the laboratory. The duration of the non-refrigerated period

shall be kept to a minimum but absolutely not more than two days (including the sampling

event).

Laboratory

Upon arrival of the DNPH cartridges at the laboratory, the samples shall be stored in the a

refrigerator until extraction.
EISOPQAM 14 - 9 November 2001

14.3.2 Volatile Organic Compounds (VOC) Sampling with SUMMA® Electropolished Stainless Steel

Canisters or Silcosteel Canisters Using Method TO-15A

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-15A 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.

 All new Summa®/Silcosteel® 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 >100o C. These parts should then be assembled and flushed with nitrogen1 for at least

8 hours prior to use in the sample train or in the canister cleanup apparatus.

 Each canister's valve and fitting 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.

 Chain-of-custody must be maintained for all samples.

1. (The nitrogen should be certified 99.999% pure by the manufacturer. A molecular sieve scrubber should be attached

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®/Silcosteel® 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:

 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®/Silcosteel® canister should be capped, an

EPA pre-numbered tag should be completed and attached to the canister, 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®/Silcosteel® canister, the

canister inlet valve should be fitted with a pre-cleaned stainless steel particulate filter. At the sample

collection location, the main 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 main valve of the Summa® canister

should be closed and capped.
EISOPQAM 14 - 10 November 2001

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®/Silcosteel® 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:

 Cleaning and Adjustment

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 and

verified by the laboratory to be free from contamination. 

 Sample Collection

Prior to sampling the flow controller will be calibrated a mass flow meter. The flowrate should

be adjusted so that at the end of the sampling interval the ending pressure of the canister is

approximately 0.9 atm. The final canister vacuum should be between 5 inches and 1 inch of Hg.

The final flowrate should be at least 1 scc/min.

After sample collection, all canisters should be tagged with 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.

14.3.3 Sampling for Semi-Volatile Organic Compounds (SVOC) Analysis with High Volume PUF

Samplers Using Methods TO-4A & TO-13A

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 polychlorinated biphenyls. This summary is adapted

from Method TO-4A (pesticides and PCBs) and TO-13A (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.

 Chain-of-custody shall be maintained for all samples.

PUF Cleaning

The Air Monitoring Staff 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.
EISOPQAM 14 - 11 November 2001

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. After

the plugs are cut, they should be rinsed with tap water and followed by a rinse with analyte-free water. 

Finally, the excess water should be squeezed out.

The PUF/XAD cartridges are assembled using a modified glass sleeve containing an extra-extra

coarse frit to retain the XAD resin in the following manner. A 3/4-inch layer of XAD resin is poured on

top of the frit followed by a 11⁄2-inch PUF plug to retain the XAD resin.

The assembled PUF/XAD 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 cartridges. The cleaned PUF/XAD cartridges should be wrapped in aluminum foil

and packed in metal cans cushioned by new polyethylene bubble wrap to prevent breakage during shipment.

Prepared PUF/XAD 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 frozen eutectic

salt packs (Blue Ice) to maintain a temperature of less than 15C. 

Sample Collection

The following procedures will be followed for all High Volume PUF/XAD sampling.

Latex gloves will be used when handling all PUF/XAD cartridges and quartz particulate pre-filters.

Assure that the red silicon upper and lower gaskets, located in the cartridge housing, are in place. Then

remove the PUF/XAD cartridge from the shipping can, remove from the foil and insert the cartridge into the

High Volume 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 sampler enclosure until the sample

is collected.

The High Volume 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/XAD cartridge should be removed, and the quartz pre-filter folded and placed in the top of the

PUF/XAD cartridge. The PUF/XAD 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

sheet and Chain-Of-Custody 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 ~ 15o 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.
EISOPQAM 14 - 12 November 2001

14.3.4 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 Particulate Matter In The Atmosphere (High

Volume Method), and 40 CFR, PART 50, APPENDIX G - Reference Method For The Determination Of

Lead In Suspended Particulate Matter Collected From Ambient Air.

The following procedures must be followed in preparation for collecting samples for metals analyses

with the High Volume sampler.

 All quartz 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 15o

C - 30oC, ± 3oC, and

less than 50 percent relative humidity, ± 5 percent, for at least 24 hours. 

 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 filter

matrix. The number of filter blanks will be determined based on a minimum of one blank for

each ten samples collected.

 Chain-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 (25oC 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 Staff 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 Chain-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 Staff and transported

to the laboratory for analysis.
EISOPQAM 14 - 13 November 2001

14.3.5 Standard Operating Procedure for Mercury Analysis of Air Using the Tekran Mercury Vapour

Analyzer model 2537A. 

The following is a synopsis of procedures which should be strictly adhered to for continuous

monitoring of gaseous mercury in ambient air.

Instrument operation

The Tekran Vapour Analyzer 2537A is designed to “continuously” analyze air for total

gaseous mercury. The Tekran 2537A uses Cold Vapour Atomic Fluorescence Spectrophotometry

(CVAFS) for the detection of mercury. In addition to being much more sensitive than atomic absorption,

CVAFS is linear over a much wider range and not as subject to positive interferences. The design of the

2537A minimizes the likelihood of negative interference. The adsorption step uses a patented pure gold

matrix as the adsorbent. This material is highly specific to mercury, eliminating interferences. The

instrument has been shown to be linear from 0.1 ng/M3 to ~1500 ng/M3.

Although the instrument can handle samples with high concentrations, the user must avoid

exposing the instrument case and parts to high levels of mercury. Mercury contamination residing on the

instrument’s components could skew both analyses and calibrations.

References 

1) The Tekran Vapour Analyzer 2537A User Manual

2) The Tekran Model 2505 Mercury Vapour Calibration Unit User Manual

Procedure 

The Tekran Vapour Analyzer 2537A continuously samples ambient air for gaseous mercury. It

performs the analysis periodically as determined by the method entered by the operator into the on-board

computer. The frequency of analysis (and thus the duration of the sample collection) can be varied from

about every 4 minutes to 15 minutes. The analysis begins when air is drawn into the instrument through

the Sample Air Inlet. The instrument’s on board computer switches a set of valves that introduces sample

into one of two gold matrix cartridges at a time. As the sample passes through the cartridge, the mercury

in the air amalgamates onto the encased gold mesh screen. While one cartridge samples the air, the

onboard computer analyzes the other cartridge. At the start of the analysis cycle, the instrument sweeps

the cartridge with argon gas, then heats the cartridge. Mercury that was adsorbed onto the gold matrix is

released during heating in argon. The mercury is then swept into the detector by the flow of the argon

carrier gas. U.V. light at 253.7 nm excites any mercury atoms present, which fluoresce and re-radiate at

the same wavelength. A UV detector views the cell at right angles to the incident light. Direct light from

the source is not seen, however, the fluorescence produced by the mercury in the cell is observed by the

UV detector. The intensity of the fluorescence is directly proportional to the amount of mercury in the

cell. Once the mass of mercury present is known, the on-board computer calculates the concentration of

mercury as the mass of mercury divided by the volume of air sampled. The on-board computer sends the

analysis results to a display screen and to a data-collecting computer. Although the instrument switches

between chambers instantaneously, the analysis of the mercury within the chamber and calculations

involved require an unavoidable lag time before the results are available. When the instrument is used

for onsite sampling/analysis, the analyst must take care to link the readout to the appropriate sample.
EISOPQAM 14 - 14 November 2001

Safety 

The instrument itself presents few Health & Safety concerns. However, the instrument is

typically used in areas where mercury contamination is suspected. The individual responsible for

sampling the air should use personal protective equipment (PPE) stipulated by the site safety officer. 

The manufacturer includes a tube filled with activated charcoal that can be placed on the vents to absorb

the mercury vented from the instrument. The mercury lamp emits UV radiation; never look directly into

the lamp, and avoid exposing skin and eyes to the UV rays.

Interferences 

Due to the unique design of the Tekran, there are no known chemical interferences. The only

materials that enter the instrument are gases and vapors, and the only material that is retained by the gold

screen is mercury. All other materials pass through the cartridge. The mercury is desorbed and analyzed

with no other materials present to interfere with the fluorescence detection.

Required Equipment

 The Tekran 2537A

 The Tekran Model 2505 Mercury Vapor Calibration Unit. This item is used only at the

SESD base laboratory. Although this item is transportable, movement can disrupt the

internal mercury bead. If any of the internal mercury adheres to the syringe during

calibration, the actual amount of mercury present in the sample will be drastically

underreported, leading to an inflated response factor.

 Teflon® prefilter. A 5 47mm Teflon® prefilter should be used on the inlet end of the

sample line to prevent contamination of the sample line from the inlet to the instrument. The

instrument has two additional 47mm Teflon® filters on its ambient air inlet and the zero air

inlet.

 1⁄4” O.D. Teflon® tubing. The tubing is used to collect the sample and should be long enough

to reach the most distant sample location, but not longer than 100 feet.

 A computer to record the data. (Must be capable of running in DOS mode and running the

Telix data capture program supplied by Tekran).

 A scrubber tube filled with activated carbon, to attach to the vents.

 10, 25 or 50μL syringes. The syringes should be gas tight, with Teflon® tipped barrels. 

Tekran recommends using syringes with side venting needles because they are less likely to

plug on extracted septum material. Read the User’s Manual to learn how to condition the

syringes for use with the primary standard.

Reagents & Standards

 High Purity Argon to act as the carrier gas.

 Compressed zero air or high purity Nitrogen to act as the Zero Air.

 Elemental Mercury ( <5ml) for use in the Tekran 2505 Cold Vapor Calibrator as a primary

standard.
EISOPQAM 14 - 15 November 2001

Calibration

A mercury permeation tube is housed in a temperature control chamber within the Tekran 2357A for

routine calibration of the instrument. This tube is maintained at 50 

C. The permeation tube constantly

emits mercury at a low rate that does not vary as long as the temperature remains stable and as long as

there is carrier flow over the permeation tube. This mercury can be directed to the cartridges and sets the

response factor of the instrument automatically. The analyst can initiate an internal calibration in three

different ways. First, the method for the on-board computer can be programmed to start the calibration at

a specific time. Next, the analyst may use the keyboard to start the calibration from two different

operating modes. Finally, the instrument will start a calibration when an electric circuit switch on the

back panel is closed from a remote device. 

The permeation rate of the mercury permeation tube is only constant once the permeation tube has

reached a constant temperature and has reached equilibrium. Upon instrument startup, the calibration

source should be allowed to stabilize for 12-hours with power applied and carrier gas connected before a

calibration is attempted. Typically, the method stored in the on-board computer will be set to perform

one calibration per 24-hour period following this warm up period. Different study requirements may

require different calibration intervals.

The User’s Manual provides much more detail than this document. The analyst should read and

understand the manual for a complete description of the calibration process. The automated calibration

is initiated using the front panel control. The steps are outlined as follows:

• From the MAIN MENU screen, use the arrow keys to highlight CALIBRATE and press

<Enter> to start the calibration.

• From the CALIBRATE MENU screen, highlight TYPE and press <Enter>

• Select the SOURCE option

• From the CALIBRATE MENU screen, highlight CALIB and press <Enter>

• From the CALIBRATE CYCLE screen, highlight FULL and press <Enter>

• From the CALIBRATE:CALIB screen, highlight BOTH and press <Enter>

It is important to routinely verify the permeation rate of the Tekran 2357A’s internal permeation

tube. A manual calibration procedure must be performed to certify the internal permeation rate. The

manual calibration procedure utilizes the well documented vapor pressure of mercury to produce a

“primary standard”. When elemental mercury is enclosed in a sealed chamber at a fixed temperature, it

reaches equilibrium and a gaseous concentration of mercury of fixed concentration is present. The

amount of mercury contained per unit volume at a given temperature is a well known function that is

available in tables. To simplify this calibration, the Tekran model 2505 mercury vapor calibration unit is

used. It is typically operated at 15 C (it should be maintained at least two degrees below ambient to

prevent condensation of mercury on the syringes) 

The User’s Manual provides much more detail than this document. The analyst should read and

understand the manual for a complete description of the manual calibration process. The manual

calibration is initiated using the front panel control. The steps are outlined as follows:

• From the MAIN MENU screen, use the arrow keys to highlight CALIBRATE and press

<Enter> to start the calibration.

• From the CALIBRATE MENU screen, highlight TYPE and press <Enter>

• Select the INJECT option and press <Enter>

• From the CALIBRATE MENU screen, highlight CALIB and press <Enter>

• From the CALIBRATE CYCLE screen, highlight FULL and press <Enter>

• From the CALIBRATE: CALIB screen, highlight BOTH and press <Enter>
EISOPQAM 14 - 16 November 2001

The calibration begins with the Clean Cartridge A cycle, and proceeds to the Clean Cartridge B

cycle, followed by the Zero Cartridge A, Zero Cartridge B, Span Cartridge A, and finally Span Cartridge

B cycle. During the Span cycles, the instrument will prompt the analyst when it is time to inject the

primary standard. The amount of standard required is calculated and preset during method development. 

After a successful calibration, the instrument will calculate the results for both cartridges, including their

Blank Correction (Blcorr) and Response Factor (Respfctr). The operator should ensure that the response

factor does not change more than ±10% between calibrations or corrective maintence may be necessary. 

Now the instrument is ready to measure samples.

Analysis & Operation

 Once the instrument is calibrated, the operation is straightforward. From the main menu screen,

highlight RUN and press <Enter>. The instrument will start sampling and analyzing the air following

the method stored in memory. The results are displayed on screen, but can also be sent to an attached

computer.

Calculations

The instrument’s on-board processor calculates the concentrations automatically. The user need not

perform any calculations during routine sampling and analysis.

Flowrate checks

The sample flowrate of the Tekran is controlled by an electronic mass flow controller which in turn

is controlled by the on-board computer. Since the mercury permeation tube used to calibrate the

instrument emits a constant mass of mercury per unit time, changes in sample flowrate won’t always be

apparent during calibrations. However, changes in flowrate would result in direct errors in the

quanitation of the ambient air samples. So, it is important to periodically check the flowrate to verify

that the electronic flow controller is working properly. Sample flowrate is best checked against a

primary flow calibrator such as a soap-film bubble meter or a positive displacment calibrator such as a

Dry Cal®. The calibration is conducted by attaching the calibrator to the inlet and measuring the

flowrate. If the flowrated doesn’t match the flowrate stated on the instrument display, the mass flow

controller should be recalibrated as per the Tekran manual.

Records Management & Documentation

The data sent to the attached computer will stored for on the computer but backup copies of the data

should be placed onto removable discs and stored for record keeping.

14.3.6 Sampling for Dioxin And Dibenzofuran Analyses with High Volume PUF Samplers

Using Method TO-9A

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 polychlorinated dibenzop-dioxins and dibenzofurans analyses. This summary is adapted from Method TO-9A of the

COMPENDIUM OF METHODS FOR THE DETERMINATION OF TOXIC ORGANIC COMPOUNDS

IN AMBIENT AIR.

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 month’s

notice prior to sampling should be given to obtain a contract laboratory program (CLP) contract for any

dioxin and dibenzofuran analysis. It is important that the contract specify a number of details to assure

accurate results:
EISOPQAM 14 - 17 November 2001

 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 dioxin and

dibenzofuran surrogates as a check of the accuracy of the method. 

 Each set of PUF 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.

 Chain-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

dioxins and dibenzofurans analyses.

Nylon or latex gloves will be used when handling all PUF cartridges and quartz particulate prefilters. 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

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 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 ~ 4o 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.

14.3.7 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, latex 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).
EISOPQAM 14 - 18 November 2001

 Pre-cleaned mercury sampling traps which have been prepared for longer than 60 days

shall not be used.

 Chain-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 Staff

The Air Monitoring Staff 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 Staff

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 Staff 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 plastic 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 train. 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. 

 At the end of each study, the samples will be transported to the laboratory.
EISOPQAM 14 - 19 November 2001

14.3.8 Standard Operating Procedure for Chlorofluorocarbon (CFC) Refrigerant Field Screening

using the Neutronics Model RI-2002PA Portable Automotive Refrigerant Identifier and

liquid CFC sample collection.

The Neutronics Model RI-2002PA is designed to identify vapor gas samples taken directly from

CFC refrigerant storage cylinders. The Neutronics Model RI-2002PA 2537A uses Multiple Sensor, NonDispersive Infrared (NDIR) technology to perform the analysis. 

The Neutronics Model RI-2002PA 2537A identifies the percentage, by weight, of R12, R134a, R22

and hydrocarbons (HC) in a sample of refrigerant. The unit will flash the measured percentages of R12,

R134a, R22 and HC on the display if their concentrations are greater than zero. Samples will be

identified with air concentrations up to 90% by weight. The Neutronics Model RI-2002PA 2537A

eliminates the effect of air when determining the concentration of a gas because air is not considered a

contaminate and can be removed during the recycling process. The instrument detects and indicates

either R12 orR134a if the sample is at least 98 % pure. The Neutronics Model RI-2002PA has an

accuracy of ± 1 % the concentration of contaminates in the 0-5 % range and ± 2 % the concentration of

air after a 30 minute warm-up period. If a hydrocarbon refrigerant is detected in a mixture sufficient to

constitute a potential flammability problem, a horn will sound and a hydrocarbon LED will light.

The instrument is designed to sample gas concentrations. If the liquid phase is sampled by mistake

and contains lubricating oil the pre-filter will turn red and the instrument may need to be returned to the

manufacturer for repair. 

References 

The Neutronics Model RI-2002PA Portable Automotive Refrigerant Identifier Operation &

Instructions Manual

Field Screening Procedure

The operator of the Neutronics Model RI-2002PA should be familiar with the detailed procedures

as described in the Neutronics Model RI-2002PA Portable Automotive Refrigerant Identifier Operation

& Instructions Manual. The following Quick Instructions are from page 9 of the manual and give a brief

description of how to operate the instrument.

1. Read and follow the Safety Messages on pages 3 and 4 of the Neutronics Model RI2002PA Portable Automotive Refrigerant Identifier Operation & Instructions Manual

2. Connect the correct hose (R12 or R134a) to the RI-2002PA Sample Inlet. DO NOT

connect the service end of the hose to the cylinder at this time.

3. Plug the power cord into a three prong standard wall outlet (110/220 vac 60/50 Hz.).

4. After warm and auto cal, connect the supplied calibrated sample hose to the vapor port of

the cylinder.

5. 9-15 psig will register on the system pressure gauge. The unit is ready to take a sample as

indicated by the flashing green LED. Push the ENTER button. Wait for the identification

mode.
EISOPQAM 14 - 20 November 2001

6. The RI-2002PA will indicate a PASS status with an R12 or R134a LED, or FAIL status

with a fail LED and the detected refrigerant concentrations . The display will scroll

through and indicate the percent by weight concentrations for R12, R134a, R22 and HC if

their concentrations are not zero. If the gas is determined to be potentially flammable ,

the hydrocarbon LED will illuminate and the horn will sound. Press the Horn Mute

button to silence the horn, and follow the safety messages.

 After Identification, a flashing yellow LED will indicate that the unit is ready to purge. 

DISCONNECT THE SAMPLE HOSE FROM THE CYLINDER. Be sure the system

pressure gauge registers 0 psig, and press the ENTER button. Allow the unit to purge then

connect the hose to the next cylinder. Go to Quick Instructions Step2.

Safety 

The instrument itself presents few health & safety concerns. However, the instrument is used to

sample refrigerant containers that have internal pressures exceeding 150 psi. The refrigerants may cause

skin or eye injury from low temperature, if allowed to vent. The individual responsible for sampling

should use personal protective equipment (PPE) stipulated by the site safety officer.

Interferences 

Due to the unique design of the Neutronics Model RI-2002PA, there are no known chemical

interferences. The only materials that enter the instrument are gases and vapors. The instrument will

analyze and report the presence of hydrocarbons and water.

Required Equipment

  The Neutronics Model RI-2002PA 2537A

 Calibration Standards

 Spare Disposable Filter Assembly (Neutronics part # RI-2002PA1) 

 Parallel Port Printer to record the data

 Appropriate fittings

Calibration

The RI-2002 PA is factory tuned and does not require any further adjustments in the field. The

instrument also features automatic self calibration. However, the instrument’s calibration is verified by

analyzing R-12, R-22 and R-134a standards. Standards are run in the same fashion as a sample. The

standard is followed by a room air purge to verify the system is cleaning itself after a high concentration

of analyte. Standards for air and hydrocarbons are not analyzed. 

Calculations

The instrument’s on-board processor calculates the concentrations automatically. The user need not

perform any calculations during routine sampling and analysis.
EISOPQAM 14 - 21 November 2001

Records Management & Documentation

The instrument will only store data from the last analysis performed. Therefore, to maintain a hardcopy record of sampling runs the data will be sent to the printer and will immediately be printed out. 

Liquid CFC Sampling

The following is a synopsis of procedures which should be strictly adhered to for the cleanup and

use of canisters for sampling refrigerants for analysis. This summary is adapted from Method TO-15A of

the COMPENDIUM OF METHODS FOR THE DETERMINATION OF TOXIC ORGANIC

COMPOUNDS IN AMBIENT AIR. 

 All new canisters must be individually checked for contamination by the laboratory

before use. One of each batch of 10 canisters that are subsequently cleaned must be

analyzed to check for contamination.

 All sampler fittings, must be solvent washed in hexane and heated to >100o

 C. These

parts should then be assembled and flushed with nitrogen1 for at least 8 hours prior to use

in the sample train or in the canister cleanup apparatus.

 Each canister's inlet port fitting will be inspected for damage before cleaning. Any

damaged fitting will be replaced with a previously cleaned (see procedure above) fitting. 

After replacing any fitting, the canister will be cleaned and analyzed to verify that it is

free of contamination.

 Chain-of-custody must be maintained for all samples.

1. (The nitrogen should be certified 99.999% pure by the manufacturer. A molecular sieve scrubber should be

attached to the nitrogen line after the regulator to remove any trace impurities).

Sample Collection

The canister is connected to the liquid port of the refrigerant container. NOTE: Some refrigerant

containers will need to be rolled or inverted to collect a liquid sample depending on their

construction. 

• Connect the pre-evacuated sampling canister to the refrigerant container using the

appropriate tubing (e.g. 1/4 inch outside diameter, thick wall, Teflon® tubing) and fittings.

• Open the sampling canister valve. 

• Slowly open the refrigerant valve. Verify liquid CFC flowing through the tubing. Fill the

sampling canister approximately one-half full. Close the refrigerant container valve while

the sampling canister is still filling. Then close the canister sampling valve. This will

prevent CFCs venting during the sampling process.

• After the sample has been collected, the canister should be capped, an EPA pre-numbered

tag should be completed and attached to the canister, and the canister valve sealed with

EPA sample custody tape.

• A Chain-Of-Custody Record should be completed detailing time of sampling, refrigerant

container identification and signed by the person collecting the sample. 

• The samples are returned to the SESD laboratory for analysis.
EISOPQAM 15 - 1 November 2001

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 art 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

surveying 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 treated separately in Section 15.3. This Section

discusses the standard procedures, techniques, and methods used to survey, or locate sample points 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 sample points or various site features during site

investigations. Traditional traverse methods utilize horizontal angle or direction (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
EISOPQAM 15 - 2 November 2001

point, thus making a closed loop. During a traverse for site control, sample points or site features may be

located by employing various techniques at the traverse control points, i.e., 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 US Department of Defense has established. Measurements of the

horizontal sample locations or site features by GPS technology is actually based on the same principles used

in traditional surveying methods. However, with space-based GPS, hand held receivers and data loggers

measure the distances to three or more noncoincident points or satellites of known positions and triangulate

the position of the sample 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 its

National Geodetic Survey (NGS) (formerly U.S. Coast and Geodetic Survey and National Ocean Survey).

The old horizontal datum, called the North American Datum of 1927 (NAD27), is currently being replaced

with the newer datum of 1983 (NAD83). The NAD27 system of horizontal control points, have established

geographic latitude and longitude positions, and provided the basis for the State Plane coordinate grid

systems used by many States. If the original geographic positions or coordinates are from the old NAD27

datum, then the resulting positions or coordinates should be converted to the new NAD83 datum. The

official computer program, developed by the NGS, 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 built in as a subroutine).

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 from an isogonic map, the

declination for the area of work. Isogonic maps may be found in basic surveying and field geology textbooks

referenced above.

Sources of existing information on horizontal control stations or coordinate grid data and their

“exact” locations may be obtained from local, state or federal departments or agencies. However, the best

place to obtain a horizontal control point data, is from the website www.ngs.noaa.gov . Typically, the

engineering or public works departments of counties, cities or towns may have data on file that is near the

particular site being investigated. Several state or federal agencies which are also 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 Geodetic Survey

 United States Geological Survey

 Corps of Engineers, Department of the Army

 Soil Conservation Service

 Tennessee Valley Authority

 Bureau of Land Management
EISOPQAM 15 - 3 November 2001

When the exact locations of sampling points or other physical features at a site are needed, surveying

methods must be based on existing control data. If necessary, the site property boundary survey, legal

description, and any physical property corners or monuments must be located by a professional Registered

Land Surveyor (RLS). Often, before or when the surveyor is at a site, the registered surveyor could be

requested to set control data points for latter use. At a minimum, the registered land surveyor would be asked

to establish at least two control points upon which the elevation and the State Plane coordinates are set. The

data on control points shall be of at least third-order accuracy. The 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, two arbitrary 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.

The point where the instrument is first set should be the starting point and it is recommended that the

arbitrary coordinates for this point be 10,000 north and 10,000 east or (10000,10000). This is so all other

points relative to the starting point will hopefully, be positive. Note that when listing points such as

10000,10000 or latitude and longitude that the order is usually y,x or northing and eastings. Also recall, from

geometry, that movement to the north or east is in a positive direction. The second arbitrary point, called

the back sight, should be tied or referenced to a bearing or azimuth so the other points will truly be spatially

relative. However, the coordinates for those points (and, therefore all other points) should be determined

at a later date. As with all field work, the location of all control data used and all field measurements shall

be recorded in the field logbook as outlined in Section 3.5.

15.2.2 Equipment Available

The following equipment is available for field use in conducting horizontal surveys in support of site

investigations:

 Topcon GTS-2, total station theodolite/electronic distance meter (EDM)

 Trimble Pathfinder Pro XR 12 channel or Geoexplorer II GPS receivers

 tripod(s)

 reflector prism(s)

 prism pole

 steel tape

 cloth tape

 right angle prism

 compass

15.2.3 Specific Equipment Quality Control Procedures

All field surveying methods using the above equipment shall be made only by those personnel who

have been trained to use them. All professional staff and field technicians must be trained and checked out

in surveying procedures by qualified staff before using this equipment.

Each piece of field equipment (as appropriate) shall be numbered, and a log book shall be kept

containing all maintenance and calibrations made on the equipment. The following specific maintenance

and calibration procedures shall be used for all surveying equipment:

Theodolite -- This equipment shall:

 be serviced and calibrated by a qualified private service shop annually or sooner if damaged

or suspected to be in error;
EISOPQAM 15 - 4 November 2001

 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 shall:

 be serviced and calibrated by the manufacturer if damaged or suspected to be in error; (See

References 4 and 5).

 be checked out using procedures outlined in the appropriate users manuals before use; (See

References 4 and 5); and,

 be cleaned and maintained using procedures outlined in the appropriate users manuals

during field use and before being returned to storage (See References 4 and 5).

Steel and Cloth Measuring Tapes -- The following procedures shall be used for all measuring tapes:

 All measuring tapes will be calibrated against an Invar steel surveyors chain or the

theodolite/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 shall be discarded.

 Tapes shall be checked to see that they are not damaged and are clean before and after use.

Compass -- All compasses shall:

 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 tube level. If the horizontal level bubble on the

clinometer does not rest at the center, the compass is opened as described above and the

clinometer level vial is 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 is

opened as previously described and the interior is dried using a toothpick and a piece of soft

cloth or soft paper. They should not be used, exposed to or stored in strong electrical fields

(Reference 3). 

Prism Poles and Reflector Prisms -- All of this equipment shall:

 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 90intervals. The bulls eye bubble will

be reset as appropriate; and

 be cleaned daily after use and before being returned to storage.
EISOPQAM 15 - 5 November 2001

Example 1: Figure 15.2.1. Map view

showing horizontal angle C-A-B.

15.2.4 Procedures for Traversing

When traverse methods are used, at least two stations or control points of known horizontal location

(expressed in terms of an arbitrary, local, State Plane or Universal Transverse Mercator coordinate system)

must be in the site vicinity. These horizontal control points can usually be set for the specific site by a

governmental agency or registered land surveyor.

The total station theodolite, often called the instrument, 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 by 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 bulls eye bubble is centered, the theodolite

is rotated 90 degrees at a time and the horizontal level bubble is checked and brought level using the threescrew 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 location is desired, the rodman holds the range pole

vertically by means of centering the bulls eye 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 are used to horizontally locate sampling points or other site features.

EXAMPLE 1, Horizontal Angles:

Figure 15.2.1 illustrates that while the

instrument is at point A (a control point),

one reads the back sight angle (azimuth or

bearing) to point C, then turns and measures

the foresight angle (azimuth or bearing) to

point B. The difference between the two

angles is the interior angle included at the

intersection of line AC and line AB, or the

horizontal angle (H). The field notation

for the measurement of the angle above

would be represented as angle C-A-B.

Typically, the first column to the left in the

field book is labeled: (BS -  - FS), which

stands for Backsight - Instrument - Foresight, or the column will simply be labeled Station 

and the second column is labeled H (see Example 5, Field Notation).
EISOPQAM 15 - 6 November 2001

Example 2: Figure 15.2.2. Side view

showing vertical angle B-A-X

and zenith angle Z-A-X.

EXAMPLE 2, Vertical or Zenith

Angles: After the horizontal angle is

determined, the vertical angle (V) is

measured, in Figure 15.2.2, from point B to

point X to determine the angle between the

line of sight AX 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 15.2.2 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 and the point in question. For example: a zenith angle of 90is 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 X, measure the slope distance (Ds) with the electronic distance

meter from A to X. Using the theodolite or transit, measure the vertical angle between line AX and AB or

the zenith angle. The height of point X 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 point 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).
EISOPQAM 15 - 7 November 2001

Example 3: Figure 15.2.3. Compass

rose showing conversion

between azimuths and

bearings.

EXAMPLE 3, Azimuths and Bearings:

When surveying, personnel should be able to

convert bearings to azimuths or azimuths to

bearings as shown in Figure 15.2.3. An azimuth is

an angular direction based on the compass rose

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 counterclockwise, 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 45West.

 The following are examples of conversions:

BEARING TO AZIMUTH AZIMUTH TO BEARING

N25E 25135S45E

S15E 165280N80W 

N8953'57"W 27006'03" 35306'49" N0653'11"W

S1018'W 19018' 0635' N0635'E

EXAMPLE 4, Coordinates: When the local State 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 in location between the north and east coordinates (from JORDAN88 to

SONIA93), respectively, are:

N = -491.05 E = 100.90
EISOPQAM 15 - 8 November 2001

Example 4: Figure 15.2.4. Map view showing

change in direction from JORDAN88

to SONIA93.

The negative symbol for N indicates the relative movement from JORDAN88 to SONIA93

downward (-) along the y axis (Figure 15.2.4.). The positive symbol for E indicates relative movement

from JORDAN88 to SONIA93 to the right (+) along the x axis. Solving for the formula (Pythagorean

theorem):

c2 = a2 + b2

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 in east:

tan-1 (N ÷ E) = -78.3886

This is the negative angle, expressed in decimal degrees, and is measured from the (x) axis into the

southeast quadrant. The azimuth from JORDAN88 to SONIA93 is obtained, in this case, by changing the

sign (- to +) and adding 90which would give 168.3886 degrees. Converting to degrees, minutes, and

seconds is the next task and the degrees are already done. Since there are 60 minutes in one degree, take the

.3886 degrees and multiply by 60 and obtain 23.3160 minutes. Likewise there are 60 seconds in one minute,

take the .3160 minutes and multiply by 60 and obtain 18.96 seconds. The resulting azimuth from

JORDAN88 to SONIA93 is 16823'19". Note: The trigonometric formula above always gives the angle

measured from the east-west (x) axis. When using this procedure, it is wise to make a sketch, as shown

above, (Figure 15.2.4.) that indicates 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. If the inverse tangent result was positive and pointed in the northeast quadrant direction, the

azimuth would be subtracted from 90and converted to degrees, minutes, and seconds. Likewise, when the

inverse tangent result points in the southwest quadrant direction, the negative angle would be subtracted from

270and a positive inverse tangent result pointing in the northwest quadrant would be added to 270and

then converted to degrees, minutes, and seconds.
EISOPQAM 15 - 9 November 2001

 Example 5: Figure 15.2.5. Traverse field notation with site map

showing traverse points used to locate monitoring wells.

 Example 5 (continued): Figure 15.2.6. Second page of traverse

field notation.

EXAMPLE 5, Traverse Field Notation: The following is an example of the field notation for a

traverse to horizontally locate sampling points. Figures 15.2.5 and 15.2.6 show the field notation, on the left

hand side of the field log book and the physical features, sampling points, and traverse control points

sketched on the right hand side of the field log book. The coordinates for each point are determined and

usually entered in red ink after the traverse is finished.
EISOPQAM 15 - 10 November 2001

15.2.5 Procedures for Differential GPS

Differential GPS involves the use of two or more multichannel receivers. One or more are used as

the rover receiver(s) and usually only one is used as the base station. The base station and the rover(s) should

be within 200 to 300 miles of each other in order to increase the accuracy of the measurements (accuracy

increases as separation between base and rover decreases) and have a clear view of the sky. The base is set

up on a control point of known horizontal location (usually expressed in terms of latitude, longitude and

elevation).

Trilaterated coordinate positions from the satellites are recorded at the base, which will be compared

to the actual horizontal 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

satellite’s clocks, data must be recorded or logged by both receivers at the exact same time in order for the

correction factor to be applicable. Often times, base station data will be obtained via modem, disk or internet

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 (See Reference 4).

The procedures to follow when using GPS to locate horizontal positions of site features are quite

simple and relatively easy to conduct. The GPS receiver/data logger is turned on and a predefined point, line

or area feature to be mapped is selected from a data dictionary within the data logger. Once the feature is

logged, the receiver/data logger user closes the feature, moves to the next feature for logging and so forth

until all site features are logged. The data files are then downloaded, differentially corrected, if necessary,

and exported to GIS applications for mapping and display of the features logged. Navigation to predefined

points (called waypoints) is accomplished by selecting the waypoint from within the data logger, and

proceeding in the direction displayed in the data logger until you arrive at the waypoint desired.

However, depending on which GPS receiver/data logger is used (Pathfinder Pro XR or Geoxplorer

II), different types of GPS processing measurements can be made: Code Pseudorange or Carrier Phase. With

these different processing measurements comes different accuracy. When code pseudorange is employed,

the autonomous position measurements (without differential correction) will be within about 10 meters using

either receiver/data logger listed above. When code pseudorange is used with differential GPS (this is either

real time or post processed), the position measurements will be less than 1 meter for both the Pathfinder Pro

XR or Geoexplorer II. Note: the Pathfinder Pro XR is capable of real time differential GPS (i.e., it has a

beacon receiver built in), while the Geoexplorer II is not. When carrier phase is employed, both receiver/data

loggers can obtain sub meter accuracy for points to be logged only (not waypoint navigation), and it is

necessary to occupy each point feature a minimum of 5 minutes. So, although the basic procedures are

simple and easy, some thought must be put into the planning of the data collection effort in order to define

the features to be logged, capitalize on the accuracy and to meet the objectives of the project.

All professional staff and field technicians must be trained in the use of the GPS equipment by

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 within the Region. The following templates list the methods and

procedures to be considered and performed if differential GPS procedures will be used to data log GPS

positions or horizontally locate sampling points or other site features (See Reference 5).
EISOPQAM 15 - 11 November 2001

TEMPLATE 1. Planning To Capture GPS Data.

 Training in the use of GPS equipment is critical to the success of a field project.

 The objectives and accuracy requirements should be established and factors that might limit the

use of the GPS equipment should be assessed.

 Check the availability of the GPS equipment and test it prior to going in the field in order to

ensure that it works properly and meets the requirements of the field project.

 Decide what features (points, lines, or areas) and their attributes at a site that locational

information will be captured with GPS equipment and create a Data Dictionary on the PC with

Pathfinder Office software. Transfer the Data Dictionary to Asset Surveyor on the Data logger.

 Check the availability of horizontal control point data at or near the site for GPS equipment

precision and accuracy check. If none exists, remember to log at least four points that surround

the site and that can be seen in aerial photographs or topographic maps for checking and GIS

georeferencing.

 Check the availability of base station coverage if the project is not dependant on collecting real

time data.

TEMPLATE 2. Creating A New Data Dictionary.

 In Pathfinder Office software on the PC select Data Dictionary Editor from the Utilities menu.

 Select New to generate a new dictionary.

 Enter the name of the new data dictionary, and any comments (optional), then click Ok.

 Select New Feature. Enter the name of the feature and under Feature Classification choose

Point, Line or Area depending on what the feature is on a map, then click Ok.

 Select New Attribute. Enter the type of attribute Menu, Numeric, Text, Date, Time, File Name

or Separator, click Ok and fill in the requested Attribute Name information, click Ok, then click

Close when finished with that attribute.

 Add more features and attributes as necessary. Many attributes can be listed for one feature.

Attributes can be menus, numbers, character strings, dates or times. Numeric values require a

minimum, maximum, and default value. Character strings require a maximum string length.

Dates and times can be set for automatic generation in the field.

 Consider putting features that are most commonly used at the beginning of the dictionary and

any existing GIS database that may require specific character string lengths. At the end of all

data dictionaries that are created, a generic point, line, or area is also generated. This is in case

while in the field, a feature not listed in the data dictionary may be tagged and identified. The

following is an example of the data dictionary used by the region.

"COC_GIS", Dictionary, "Chain of Custody/GIS Data Dictionary"

"Surfsoil", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Subsoil", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Potwater", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Muniwsupply", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Indwell", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Waste", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Surfwater", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Sediment", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Groundwater", point

 "Sample_ID", text, 30

 "Station_ID", text, 30
EISOPQAM 15 - 12 November 2001

"Precipitation", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Other_unknown", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Other_biota", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Munipwater", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Indprocwater", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Wipesample", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"FIshsample", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Vegetation", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Macroinvertibrates", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Wastewater", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Sludgenonrcra", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Uicinjectionwells", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Petrotanks", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Ambair", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Indoorair", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Munieffwater", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Indeffwater", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Periphyton", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Tissue", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Lithology", point

 "Sample_ID", text, 30

 "Station_ID", text, 30

"Fence", line

 "Type", text, 30

"Road", line

 "Name", text, 30

"Railroad", line

 "Name", text, 30

"Stream", line

 "Name", text, 30

"Structure", area

 "Type", text, 30

TEMPLATE 3. Data Dictionary Transfer To Data Logger or Geoexplorer II.

 Connect the GPS unit to the COM1 port of the PC using the appropriate cable that is attached

to the COM1 port of the data logger or in the case of the Geoexplorer II attached to the input

port.

 Select File Transfer in the data logger Asset Surveyor software main menu, or Data Transfer

in the Geoexplorer II main menu.

 In Pathfinder Office software on the PC, select Utilities, then Data Transfer. Note: Device

should be set to GIS Data logger and Data Type should be set to Data Dictionary. Under

Available Files, highlight the data dictionary name and under Selected Files, choose Add. Under

Direction, choose Send. Then click Transfer.

 Once the data dictionary has been transferred, Close the Data Transfer window and exit the data

logger or Geoexplorer II.

 Note: Several data dictionaries can be uploaded to a data logger, but only one can be uploaded

to a Geoexplorer II. Subsequent uploaded data dictionaries to the Geoexplorer II will delete

previous ones.
EISOPQAM 15 - 13 November 2001

TEMPLATE 4. Default Configuration Of The Data Logger And Geoexplorer II For Data Capture.

 In Asset Surveyor software on the data logger, choose Config or Configuration in the

Geoexplorer II and set the following.

Logging Intervals

Point Feature 1 second

Line and Area Feature 5 seconds

Not in Feature All

Velocity All

Minimum Positions (point feature) 20 (data logger)

120 (Geoexplorer II)

Position Mode Overdet. 3D (data logger)ODS 3D (Geoexplorer II)

Note: Manual 3D is the minimum for both.

Elevation Mask 15(data logger and Geoexplorer II); 10(base)

Signal-to-noise ratio mask 6 (data logger); 5 (Geoexplorer II)

PDOP mask and switch 6

Dynamics Code Land (for terrestrial work), Sea or Air (for obvious

reasons)

Template 5. Data Capture File Name Convention.

 Default file name convention is recommended.

 Assists with identifying files by time and date for matching up base station file if differential

correction is needed.

 The following describes the parts of a file with the name: A021514A

GPS UNIT MONTH DATE HOUR (UTC) FILE LETTER

A 02 15 14 A

 When multiple GPS units are at the same site data logging, each unit will be given a different

letter identification.

 UTC stands for Universal Time Coordinated, which used to be known as Greenwich Mean Time

(GMT), i.e., the local time at the Greenwich meridian (zero degrees longitude). For the

conversion between Eastern Standard Time (EST) or Eastern Daylight Time (EDT), use the

following formula.

EST = UTC - 5 hours (note that this is fall and winter)

EDT = UTC - 4 hours (spring and summer)

Template 6. Data Capture Logging And Considerations.

 Choose Data Capture from the main menu.

 Select Create rover file in the data logger (choose Open Rov. File in the Geoexplorer II) or

Reopen rover file when appending to a previous file.

 The Create file screen has three fields: File, Data Dict. and Free Space. Press Enter on the Data

Dict field to choose your data dictionary.

 Press Ok to start the current file selected.

 Scroll through Start feature in the data logger or scroll to Select Feature in the Geoexplorer II

and press Enter. A list of features in the data dictionary associated with the current file is

displayed.
EISOPQAM 15 - 14 November 2001

 Select the appropriate feature by pressing Enter. Then type the appropriate attribute value(s).

 After the minimum number of positions are attained (see Template 4 above), press Ok to accept

and store the feature and all of its attributes values (in the Geoexplorer II, scroll to Close Feature

to accept and store the feature and all of its attributes).

 Proceed to the next site feature and continue this operation for all site features. Note that while

collecting positions for one feature, for example the positions along a road, you can Nest other

features, for example wells or other sample points on one side of the road or the other, then press

Ok to accept and store the wells or other sample points feature and attribute values and continue

logging the road. When finished, press Esc to exit Data Capture and return to Main Menu (in

the Geoexplorer II, scroll to Close File and select Yes to return to Main Menu).

CONSIDERATIONS

 Check the horizontal control point data at or near the site for GPS equipment precision and

accuracy. To obtain a nearby National Geodetic Survey (NGS) control point, search the website

www.ngs.noaa.gov and click “NGS Products and Services” then go into “Data Sheets” until

“NGSmap” is found. This is an interactive NGS data sheet retrieval tool that will produce a map

of up to 32 control points near the site. Use the data sheets to find the horizontal control point

and record a separate point generic feature data file at the control point as a check of the

manufacturers specifications for the GPS unit.

 When collecting GPS locational information, keep in mind the available maps or areal

photographs of the site. Note: The GIS group has electronic georeferenced coverage of most of

the region with USGS Topographical Maps or Aerial Photography. One of the best websites to

obtain aerial photographs of a site is: http://rsori.rtpnc.epa.gov/ which is EPA’s remote sensing

home page. If only maps are available, collect enough site feature information to improve the

existing maps. Collect at least four GPS points surrounding the site that can be seen in the field

and on the existing maps and/or areal photographs (intersections of roads, manhole covers, etc.)

so the existing maps and/or areal photographs can be georeferenced and rectified to the same

coordinate system, datum, and projection back in the office with GIS techniques.

Template 7. Data Logger Files To PC.

 Connect the data logger to COM1 of the PC using the appropriate cable that is attached to the

COM1 port of the data logger, or, in the case of the Geoexplorer II, attached to the input port.

 In Pathfinder Office software on the PC, select the appropriate project, then Utilities, then Data

Transfer. Note: Device should be set to GIS Data logger and Data Type should be set to Data.

Under Available Files, highlight the files to be downloaded and under Selected Files, choose

Add or Add All

 Under Direction choose Receive. Then click Transfer. The data file(s) will be converted to files

with a .ssf extension.

 Once the data files have been transferred, Close the Data Transfer window and exit the data

logger.

Template 8. Differential Correction.

 If a real time GPS unit was used for data capture, the data file(s) must be checked to see if all

positions were differential corrected through the real time broadcast signal. If any portion of a

data file was not corrected with the real time broadcast signal, a base station file must be

obtained in order for all positions in the file to be differentially corrected.
EISOPQAM 15 - 15 November 2001

 In Pathfinder Office software on the PC, select File then Open. Select the data file(s) to look

at then Ok. After a brief scan of the features, one by one, identify the features and file name(s)

that need a base station file for differential correction then Close the file(s).

 Obtain base station file(s) from a base station as close to the site as possible and that match the

month, date and UTC hour of the data file(s) exactly and place in the Base subdirectory of the

Project directory in Pathfinder Office software on the PC (C:\Pfdata\(Project)\Base). These can

be obtained through modem, internet, email, or disk via regular mail. As in Template 5 with

data files, the base station files use a similar file naming convention and will identify the month,

date, and UTC hour that the base station file was collected. The following is the base station

file naming convention.

 CITY YEAR MONTH DATE HOUR (UTC)

A 9 02 15 14

 These websites are good starting points for base station files and cover our entire region:

http://www.ngs.noaa.gov/CORS/cors-data.html

http://www.fs.fed.us/database/gps/clickmap/cbsmap.htm

ftp://ftp.dep.state.fl.us/pub/

 Once base sation files are obtained that match the month, date, and UTC hour, in the data files

as indicated above (and also in the same year), in Pathfinder Office software on the PC, select

Utilities then Differential Correction.

 Select the rover file(s) (more than one may be selected) to be differentially corrected. If the base

station files were placed in the Base subdirectory as mentioned above, select Local Search and

the base station files that match the data files will be highlighted. Select Ok.

 The differentially corrected files will be placed in the Project directory with a .cor extension and

the processing should be set to Smart Code and Carrier Phase Processing. After all of the

above procedures are followed, select Ok to start the differential correction process.

 To view the corrected files, select File then Open and the corrected files should be highlighted.

Select Ok to view then scan through the features to make sure all positions were differentially

corrected.

Template 9. Export to ARC/INFO Arcview GIS.

 In Pathfinder Office software on the PC, select Utilities, then Export.

 Select the Input Files for export (highlighted).

 By default the Output Folder where files are exported is C:\Pfdata\(Project)\Export.

 In Choose an Export Setup, select Sample Arcview Shapefile Setup then click Properties.

 Data: Type of data to export: Features - Positions and Attributes and pulldown Export All

Features.

 Position Filter: Filter by GPS Position Info; Minimum Satellites: 3d (4 or more Svs), Maximum

PDOP: Any, Check Realtime Differential and Differential.

 Output: Output Files Combine all input files and output to the project export folder and System

File Format DOS Files.

 Coordinate System: Use export Coordinate System: Latitude/Longitude, Datum: NAD 1927

(Conus).

 Attributes: Export Menu Attributes As: Attribute Value, Generated Attributes: check Feature

Name.

 Arcview Shapefile: Theme Options: Skip this screen.

 Units: Use Export Units: Change, then select the approprioate units (metric or english).

 Select Ok when finished with Change Setup Options, then Ok to export.
EISOPQAM 15 - 16 November 2001

 Three types of files are generated. Each named feature, (where feature is one of the features

listed in the Data Dictionary that was created in Template 2) will have the extensions: .dbf, .shp,

and .shx.

 Transfer all of the .dbf, .shp, and .shx files to the appropriate directory on the R4ESD LAN

G:\user\shared\ drive so they may be transfered by FTP or other means to the appropriate

directory and work space in the GIS UNIX boxes. The GIS group (on their UNIX Boxes) or

Project Leader (on the PC) will use these files in Arcview. Any conversions between

coordinate systems and datums that may be necessary should be done by the GIS group.

 Open Arcview and add the coverages as themes.

Template 10. GIS to Realtime Differential GPS Waypoint Navigation.

 After the collection of site features, (i.e., wells, site structures, roads, etc), with GPS techniques,

and/or after the site areal photographs or maps are georeferenced and rectified, specific samples

locations can be picked out of the GIS coverages, and generated into waypoints. These

waypoints can then be transferred back into the realtime GPS Data logger and used to layout a

soil sampling grid or other locations of interest at the site.

 Waypoint files created in ARC/INFO must be in the following ASCII format for importing into

Pathfinder Office software on the PC:

xcoordinate,ycoordinate,zcoordinate,”waypointnameornumber” Note: the zcoordinate is optional

and may be left blank with a space (i.e., x,y,,”waypoint”).

 Once waypoint files are generated and in the proper format, in Pathfinder Office software on the

PC, select File, Waypoints, then ASCII Import. Select the waypoint file to be imported and click

Ok.

 Next, connect the GPS unit to the COM1 port of the PC using the appropriate cable that is

attached to the COM1 port of the data logger.

 Select File Transfer in the data logger Asset Surveyor software main menu.

 In Pathfinder Office software on the PC, select Utilities, then Data Transfer. Note: Device

should be set to GIS Data logger and Data Type should be set to Waypoints. Under Available

Files, highlight the waypoint file name and under Selected Files, choose Add. Under Direction,

choose Send. Then click Transfer.

 Once the waypoint file has been transferred, Close the Data Transfer window and exit the data

logger.

 Upon returning to the site, select Navigation in the data logger Asset Surveyor software main

menu. Move the curser to the waypoint listed and press Enter. Move in the direction indicated

by the data logger until the waypoint is reached. Waypoints can also be edited on the fly and/or

added to the list in the field and transferred back to Pathfinder Office software on the PC for

updating and/or exporting back to GIS.

15.3 Vertical Location (Elevation) Surveys

15.3.1 Introduction

The field 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 field geology textbooks (See References

1, 2, and 3).
EISOPQAM 15 - 17 November 2001

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 sea level and is

referred to as the datum or datum plane. The datum for vertical control (elevation) is called the 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 obtained from local,

state, or federal departments or agencies. Typically, engineering or public works departments of counties,

cities, or towns may have data on file that is near the particular site being investigated. State or federal

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/National Ocean Survey

 United States 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 could

be requested to set at least two third-order accuracy vertical control points or benchmarks. The vertical

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 wingwall, 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

site sketch map and all field measurements should be recorded in the field logbook as outlined in 

Section 3.5.

15.3.2 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
EISOPQAM 15 - 18 November 2001

Trigonometric Leveling

 Topcon GTS-2, total station theodolite/electronic distance meter (EDM)

 tripod(s)

 reflector prism(s)

 prism pole

 cloth or steel tape

 compass

15.3.3 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.

15.3.4 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 threescrew 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 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 instrument 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.
EISOPQAM 15 - 19 November 2001

Example 1: Figure 15.3.1. Field notation for differential leveling.

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 × (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.

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.
EISOPQAM 15 - 20 November 2001

Example 2: Figure 15.3.2. Trigonometric level notation showing side view when elevation of

point desired is above instrument.

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 (VCAB) of 530', the difference in

elevation between point C and point B is computed using the trigonometric formula:

elevation difference = distance AB × sin(V)

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. × sin(530') = 31.04 ft.

The elevation of point B is: 105.92 ft. + 31.04 ft. - 5.23 ft. = 131.73 ft.
EISOPQAM 15 - 21 November 2001

Example 3: Figure 15.3.3. Trigonometric level notation showing side view when elevation of

point desired is below instrument.

Example 4: Figure 15.3.4. Spot elevation

differences using law of sines.

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 (VFDE) of -530', the difference in

elevation between point F and point E is computed by substituting in the trigonometric formula:

elevation difference = 323.88 ft. × sin(-530') = -31.04 ft.

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.

The elevation of point E is: 105.92 ft. + (-31.04 ft.) - 5.23 ft. = 69.65 ft.

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:
EISOPQAM 15 - 22 November 2001

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:

Note that this method above only accounts for the relative difference in 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.I. 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.

15.4 Hydrological Studies

15.4.1 Scope and Applicability

Hydrological studies are an important component of virtually all Branch field studies and include

activities such as time-of-travel studies, current/circulation studies, dye dilution surveys, flow measurement

and stage/discharge relationship development. Time-of travel surveys are frequently required as part of water

quality model calibration surveys or as a component of other activities such as reaeration measurements. Dye

dilution studies are extremely useful for evaluating the mixing of effluents with receiving waters. Activities

such as water quality enforcement studies, NPDES permit compliance monitoring, water quality survey

monitoring, reconnaissance surveys, and research rely on accurate flow measurement. For example, NPDES

permit limits often limit the mass loading of a particular pollutant that may be discharged. Stage

measurement and the determination of stage-discharge relationships are also important hydrological data

collected by the Branch. For example, stage-discharge studies are extremely useful for determining flow in

conjunction with TMDL storm event sampling efforts. As much attention and care should be given to

hydrological measurements in the design of a sampling program as to the collection of samples and

subsequent laboratory analysis. 

15.4.2 Methods

15.4.2.1 Surface Water Stage/Tape Down

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 site to provide a reference and check on the recorder trace. Water stage should be recorded to the

nearest 0.01 foot where possible.
EISOPQAM 15 - 23 November 2001

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 0.01 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, clarifier

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, in 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, Wastewater Flow Measurement).

15.4.2.2 Time-of-Travel

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 study.

Tracer dyes provide a direct and highly accurate method of determining time-of-travel. This is the

preferred method if resources are available.

Floats

Surface floats may be followed downstream and timed for known distances to determine time-ofwater-travel. This requires the use of considerable judgment, for floats tend to travel into quiet or eddy 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.
EISOPQAM 15 - 24 November 2001

Cross Section Measurements

The measurement of cross sectional velocities at frequent longitudinal intervals and the calculation

of average velocity in 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.

 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, Rhodamine WT

dye is the most common tracer used. Rhodamine WT is water soluble and 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 instream dispersion.

If Rhodamine 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-sectional

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" (12) and "Fluorometric Procedures for Dye Tracing" (10).

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 to every 60 minutes or more, depending on the duration of the dye cloud 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 time-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. Readings directly from the fluorometer scale or conversion to dye concentration

can be manually plotted against time. 
EISOPQAM 15 - 25 November 2001

A version of the grab sampling technique would be to use an automatic water sampler which

discharges into separate bottles. The samples collected at preset intervals are analyzed and the

concentrations are plotted against time. 

Ideally, dye 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. Where it is infeasible to

continue monitoring to the stream background concentration, the trailing edge of the dye cloud should at least

be monitored until the in stream 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.

Rhodamine WT concentrations in the dye cloud should be maintained below 10 ppb at water supply intakes.

Commercially available Rhodamin WT is a 20% solution.

15.4.2.3 Dilution

A great deal of the previous section (time-of-travel studies) applies to this section and USGS

publications provide references to appropriate techniques, in particular "Measurement of Discharge by Using

Tracers". ( 11)

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. Rhodamine WT provides an adequate tracer for most

investigations. This dye is slightly photoreactive. Decay rates (ekt where k=0.034/day for exposure to full

sunlight) are reported in the literature. Due to limited light penetration, actual rates are normally

insignificant or can be established through on-site 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 methods valuable assessment tools.

The principal of superposition as developed by Kilpatrick et al. (13) of the USGS is a reliable method

to determine dilution levels of wastewaters in receiving estuaries. A tracer dye is metered into the

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 any tracer

photo decay, the dilution levels of the discharge can be produced for selective points in the estuary.
EISOPQAM 15 - 26 November 2001

Calculation Procedure:

Cw = (Ct)(ekt)(Vw)

 Vt

Where:

Cw = Ultimate concentration of wastewater at point of interest

Ct = Ultimate concentration of tracer (by superposition) at point of interest

t = Tidal days to ultimate concentration

ekt = Photo decay of tracer

Vw = Wastewater discharge per tidal day

Vt = Volume dye released in tidal day

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 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

 (C1) (q1) = (C2) (Q2 + q1)

Q2 = (C1) (q1) - (C2) (q1)

C2

Where:

Q2 = pipe flow rate

C2 = tracer concentration after mixing

q1 = tracer injection rate

C1 = 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.
EISOPQAM 15 - 27 November 2001

It is suggested that at least three injection rates and resulting mixed tracer concentration

measurements be used to calculate the discharge rate.

EPA’s Technical Support Document also provides guidance for conducting a “quick saltwater

dilution assessment” using a dye tracer (15).

15.4.3 Current Measurement

Current measurements may be made by either an axial-flow, ducted impeller recording current meter

(Endeco 174) or an Acoustic Doppler Current Profiler (ADCP). Both meter types may be programmed via

appropriate connection to a PC prior to deployment, deployed in an unattended mode, and interrogated for

data download by PC following data collection. Likewise, the meters may be used for real-time data

collection in profiling applications. For unattended applications, deployment in and out times/dates should

be recorded in the field record. The field record should also include the location and depth(s) of the

deployment and serial number or other appropriate identifier of the meter(s) used in the deployment.

For unattended applications, the impeller-type meters are deployed on a weighted tether line with

a subsurface float (to keep the tether line taut) and a surface float (for locating the meter). Multiple meters

can be deployed at any depth(s) on the tether. For a non-stratified system, one meter will generally be

deployed at mid-depth. For a stratified system, a meter will generally be deployed at the mid-depth of each

strata. Anticipated deployment depths for a given application should be provided in the Quality Assurance

Project Plan. 

Care should be taken during deployment of the impeller-type meters to prevent tangling of the tether

line around the meter and/or floats. The meter should also be checked for level deployment in the water.

Lead weights attached at the nose and tail ends of the meter should be added or removed as needed to ensure

the meter is axially deployed (horizontal) in the water column. Meters should be deployed in a way that

minimizes potential equipment damage or interference from ship traffic or other obstructions.

ADCP meters may be mounted in a variety of ways; however, for unattended current measurements,

these meters will typically be deployed in upward facing configuration with the meter mounted to a weighted

platform specifically designed to minimize potential impacts from drag lines or nets. The meter may also

be boat mounted in a downward facing configuration for real-time data collection and profiling. 

15.4.4 Equipment

The following equipment is available for surface water stage/tape down measurements:

 Model F Stevens Stage Recorder(s) (mechanical, horizontal drum system);

 Model A-71 Stevens Stage Recorder(s) (mechanical drum system);

 Stevens Model GS-93 Endcoders and Loggers;

 Stevens AxSys System (pressure transducer);

 Model 1870, 2870, 3210, 3230, and 4210 ISCO flow meter(s) and Recorder(s)

(pressure transducer, bubbler, and ultrasonic reflection systems)

 USGS staff gage(s); and

 Weighted steel tape-down systems
EISOPQAM 15 - 28 November 2001

The following equipment is available for time-of-travel and dilution studies:

 Turner 10-AU and Turner 10-005 fluorometers,

 Rhodamine WT dye tracer and standards,

 ISCO automatic samplers,

 Peristaltic, submersible, and metering pumps,

 recorders,

 flow meters, and

 floats

The following equipment is available for flow/current measurement:

 cup-type current meters (pygmy/price),

 impeller-type current meters (Endeco),

 sounding (depth) equipment, and

 ADCP

15.4.5 General Quality Assurance Procedures

No field investigator shall make flow measurements until they have had at least six months of actual

field experience and have performed these measurements under the supervision of a senior field investigator.

Wastewater flow shall be expressed in million gallons per day (MGD) or the metric equivalent

(m3

/day). Stream flow shall be expressed in cubic feet per second (cfs) or the metric equivalent (m3/sec).

Current velocities shall be expressed in feet per second (fps) or the metric equivalent (m/sec). Time records

associated with hydrological studies shall be (1) kept in local time, (2) recorded in 24 hour military format,

and (3) recorded to at least the nearest five minutes. 

All field equipment shall be operated, calibrated, and maintained according to manufacturer’s

specifications. All equipment shall be visually inspected prior to deployment to ensure proper operation. 

15.4.6 Data/Records Management

All hydrological measurements shall be thoroughly documented in field records. All measurements

shall be traceable to the personnel making the measurements and the equipment utilized. 

15.5 Ground Water Level Measurements

15.5.1 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 measurement 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. 
EISOPQAM 15 - 29 November 2001

15.5.2 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.

Penlight 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 inert 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 in

contact with water. Distance to 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 not 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.

15.5.3 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 the well. 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.

15.5.4 Equipment Available

The following equipment is available for ground water level and total well depth measurements:

 weighted steel measuring tapes

 electronic water level indicators.
EISOPQAM 15 - 30 November 2001

15.5.5 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.

15.6 Surface Geophysical Studies 

15.6.1 General (17)(18)

The science of geophysics can be defined as the study of the earth's physical properties. Surface

geophysical studies are investigations which use indirect measurement instrumentation and techniques to

evaluate these properties from points on or above the earths surface. Many of the surface geophysical

methods used today for hazardous waste site investigations found their start almost exclusively in

geophysical prospecting for oil, gas and minerals. Geophysical methods typically obtain and provide data

measurements in a one or two dimensional pattern. It is sometimes possible, using data output from some

of the two dimensional patterns, to generate three dimensional interpretations of the data, clearly showing

the locations and relative intensities of the anomalies. These techniques provide a much more rapid, safe

and economical way to investigate the subsurface at hazardous waste sites, as compared to direct sampling

techniques such as monitoring well installation and subsurface soil sampling. Measurements obtained from

available geophysical instrumentation can be used to locate buried materials or areas of disturbance, to

characterize the geologic setting, or to locate a contaminant plume. 

When planning a hazardous waste site investigation, strong consideration should be given to

incorporating the use of geophysical methods in the investigation. Geophysical equipment can be used to

screen a site for the presence of metallic or conductive material in a short period of time with fairly accurate

results. Surface geophysical methods are also valuable aids in determining sampling locations in areas where

drilling or direct sampling would be too time consuming and costly, or would create a dangerous situation.

Often times, it is these geophysical data measurements that can assist in guiding the latter phases of an

investigation.

When selecting the geophysical method(s) best suited for a study, certain site factors should be

considered. They include: the type of soils, the depth to ground water, general ground surface conditions

(wet, dry, frozen), large surface or subsurface ore bodies, depth to bedrock, type of topography, large surface

metallic objects (building, tanks, pipes, etc.), power lines and underground cables, buried drums, and/or

contaminant plumes, etc. Once site conditions are known and evaluated, then the instrument(s) have to be

selected that will be most applicable to the specific site.

Geophysical techniques available for site investigations by Branch personnel can be placed into two

categories, electrical and magnetic. The electrical methods include metal detection, electromagnetics (EM),

and VLF (very low frequency). The magnetic method is referred to as magnetometery. These will be

described in further detail later in this section. Other geophysical techniques and methods, such as ground

penetrating radar (GPR), resistivity, seismic refraction and reflection, gravity, temperature, and radioactive

methods are available from EPA contractors. Depending on site conditions and study objectives, one or more

of these methods might be used in a hazardous waste site investigation.

Several practical tips, listed below, should be considered prior to using geophysical equipment during

an investigation.

  Becoming familiar with the instrument and it's principle of operation before attempting a geophysical

survey is extremely important.
EISOPQAM 15 - 31 November 2001

  Normally, at least a two-person team is adequate for a small-scale geophysical study. However,

some surveys may require more personnel due to the size of the site.

  Prior their use during a study, all geophysical equipment shall be inspected to ensure it is in good

working condition and/or calibrated according to the manufacturer's procedures included with each

instrument. Battery voltage should be monitored closely, especially in cold weather.

  Ancillary information shall be recorded in a field book as to the date and times calibrated, team

members, and a complete chronological description of what transpired during the study.

  As a general rule, the locations of any geophysical anomalies detected during a surface geophysical

study shall be documented using standard surveying techniques. At a minimum, a key coordinate

or coordinates in the grid should be spatially identified (azimuth and distance), relative to obvious

and permanent landmarks, for future reference. A typical coordinate grid where the station and line

numbers are all defined as positive and which extend from the grid origin in the north (Y) and east

(X) directions, eliminates confusion while recording and processing data.

  Review data, as much as possible, while it is being recorded for erroneous readings. Reoccupy

station locations to verify data if necessary.

15.6.2 Specific Surface Geophysical Methods

The following is a brief description of the electromagnetic and magnetic geophysical instruments

used by Branch personnel, their capabilities, and some of their limitations.

Electrical Methods

Metal Detection

Metal detectors are used to detect changes in electrical conductivity caused by the presence of

metallic materials, both ferrous and non-ferrous. Metal detectors: (1) are generally limited to shallow depths

(1 to 3 meters); (2) can detect large metallic objects such as buried ferrous material and/or metallic laden

wastes at depths of 3 to 6 meters; (3) are insensitive to soil moisture and small metallic objects; and, (4) are

light weight and economical.

Several different metal detectors are available for use. These are described below.

  Standard "Treasure Seeker" Metal Detector - This is the typical hand held unit with a disk that

is swept across the ground surface. It is useful for locating items of small mass that are located

at or just below the ground surface or items of moderate or large mass that are located relatively

close to the ground surface.

  Pipe and Cable Locator - These instruments are much more sensitive than the treasure seekertype instruments. They generally are capable of detecting decreasing smaller mass objects at

increasingly greater depths, as compared to the treasure seekers. Three instruments are available

under this broad category, the TRACER Pipe Seeker 5 Metallic Pipe and Line Locator, the

Fisher M-SCOPE TW-6 Pipe and Cable Locator and the Schonstedt MAC-51B Heliflux

Magnetic and Cable Locator. Each of the three can be used in simple survey mode or can be

used in the conductive mode, where low current electrical signals are induced into cables and

traced from the surface. 
EISOPQAM 15 - 32 November 2001

The basic operating principle of the typical pipe or cable locator is as follows. A small AC voltage,

at an audio frequency, is sent through the transmitter coil causing a current to flow. The transmitter on the

metal detector generates an alternating magnetic field around the transmitter coil. The primary magnetic

field is canceled or nulled at the receiver coil by orienting the planes of the transmitter and receiver coil

perpendicular to one another. Eddy currents, induced from the primary field, in a metallic object within the

range of the instrument, produces a secondary field. This secondary field interacts with the primary field

causing the canceled or nulled condition to become upset. This results in an output in the form of a meter

deflection and/or audio signal.

Electromagnetic Induction (EM) (17)(18)(19)(20)(21)(22)(23)

EM induction instruments measure true soil conductivity in uniform, homogeneous subsurface

conditions and can also measure apparent soil conductivity in layered soils or other geologic material. The

EM data measurements have also been called ground or terrain conductivities or reciprocal resistivities. EM

units are very effective for rapid site reconnaissance and detection of buried drums, pipes, metallic type

conductors or trenches were the conductivity of the disturbed soil would differ from the native soil. EM

induction instruments are not limited by frozen ground, or wet or dry soils.

Two EM instruments available for use by Branch personnel are the EM31-D and the EM34-3. The

EM31-D is a fixed coil separation instrument with an intercoil separation of 3.66 meters and is capable of

providing both terrain conductivity and metal detection data. The effective depth of investigation with the

EM31-D is approximately 5 to 5.5 meters (15 to 18 feet), depending on location relative to the ground

surface. The EM31-D can be connected to a data logger for logging EM data during surveys. This data can

later be down-loaded into a PC for post-processing. The EM34-3 utilizes variable coil spacing, however, and

is capable of providing a much greater depth of investigation, though only for terrain conductivity. With

intercoil spacings of 10, 20 and 40 meters, depths of investigation may reach 15, 30 or 60 meters (45, 90 or

120 feet), respectively. The EM34-3 does not allow electronic data logging. Both instruments may also be

operated with the coil dipoles in different orientations, effectively providing for a different investigation

depth at each measurement point.

The principle of operation of EM instruments is as follows:

A small AC voltage, at an audio frequency, is sent through the transmitter coil causing a current to

flow. The transmitter coil on the EM-31D generates an alternating magnetic field that directs

induced electrical current loops into the ground, which produce primary and secondary magnetic

fields. These magnetic fields are then sensed or detected by the receiver coil, and then amplified and

stored on a data logger. The ratio of the primary and secondary fields are incorporated into the

design of the EM instruments such that the meter readings are true or apparent ground (soil)

conductivities.

Very Low Frequency (VLF) (17)(24)

VLF geophysical instruments utilize the long distance, high power, very low frequency radio

transmissions that the military has developed for submarine communications. At least 15 VLF transmitters

are at various locations around the world and continuously operate at 15-30 kHz. VLF transmitters can be

used at distances up to 10,000 kilometers (6,214 miles) from a powerful transmitter.

The ABEM Wadi is the VLF instrument available for use by Branch personnel. It is a hand-held

instrument, complete with a belt-mounted battery supply and radio signal receiver. Information necessary

to define a profile line or survey grid is input into the hand-held unit. After a transmitter is selected, the

operator occupies a measurement point and presses the measurement keypad. At any time during the survey,

the instrument will interpret any anomalies that are identified. The complete data may also be post-processed

to create anomalie maps.
EISOPQAM 15 - 33 November 2001

Primary electromagnetic radio waves are generated by the VLF transmitters. The Wadi measures

the vertical and horizontal in-phase and out-of-phase components of the secondary electromagnetic field,

which is induced in the more conductive geological structures (water-filled faults, fractures, etc.). The

measurements are displayed as the vertical in-phase field expressed as percentage of the horizontal field and

recalculated as current density.

Magnetic Method - Magnetometry (17)(18)(25)(26)

The science of magnetism is called magnetics. The earth's magnetic field has both direction and a

magnitude or intensity. Generally, magnetometers have been designed to detect and accurately measure

changes in the earth's magnetic field. The magnetic field of the earth resembles the characteristics of a bar

magnet. The magnetic south pole is located near the geographic north pole. Magnetic field lines always

move from the north pole to the south pole outside of a magnet. This explains why the charged pole of a

compass needle is attracted to the north (geographic) or magnetic south pole. The units of the earth's

magnetic field intensity are nanoTesla (nT), which is numerically equal to gamma, the common unit seen

in publications and maps.

Branch personnel have two different magnetometers available for conducting magnetic surveys.

These are the EG&G Geometrics Unimag II Portable Proton Magnetometer Model G-846 and the EG&G

Geometrics Model G-856 Proton Precession Magnetometer. The G-856 is the newer unit and, compared to

the G-846, is capable of providing greater resolution of magnetic field data (0.1 nT vs. 1.0 nT for the G-846)

and is capable of logging 1,000 stations of data for subsequent retrieval and post-processing.

A magnetometer's primary design function is detection of magnetic objects such as buried ferrous

materials or large bodies of ore which alter the earth's magnetic field. Individual drums can be detected at

depths up to 6 meters whereas large masses of drums may be detected at depths of 6 to 20 meters.

Magnetometers are susceptible to noise from many different sources and therefore should not be calibrated

or used in or around buildings, near powerlines, or directly on the ground. The total magnetic field

measurements from a proton precession magnetometer are based upon an atomic constant, and do not depend

on temperature, humidity, and sensor orientation.

The proton magnetometer operates by applying a voltage to a coil around a vessel containing a

hydrocarbon fluid such as decane. The resultant magnetic field orients the protons in the fluid. The protons

reorient or precess and line up with the earth's magnetic field when the voltage is removed. Through nuclear

precession, a signal is generated and the precession frequency of this signal is proportional to the strength

of the total magnetic field. The magnetometer amplifies this precession frequency signal and electronically

translates the signal into nanoTeslas or Gammas. The presence of ferrous metals creates variations in the

local strength of the magnetic field, permitting their detection with a magnetometer.

15.6.3 Instrument Operations

All personnel trained in the use of any of the above described surface geophysical instrumentation

will retain in their possession, copies of operations manuals for each of the instruments. In addition, a copy

of each of the manuals will be maintained by a designated person within the Hazardous Waste Section. All

instruments will be used consistent with the instructions contained within these manuals, with respect to

preliminary instrument operational and sensitivity checks, as well as actual operation during data collection.
EISOPQAM 15 - 34 November 2001

15.6.4 Specific Instrument Quality Control Procedures

All geophysical instruments used by Branch personnel or EPA contractors shall be calibrated in

accordance with the manufacturers' specified calibration procedures, and shall only be calibrated by

personnel that have been trained to do so. The calibration shall be checked periodically to insure accurate

readings, especially on re-entering the study area after having left for a period of time. All calibration

procedures and pertinent information shall be documented in the field logbook as outlined in Section 3.5.

Personnel using the geophysical equipment shall be trained in the use and maintenance of such

equipment, and shall be able to interpret and present the gathered data in an easily understood manner in

charts, graphs, maps, and formal reports. It is the responsibility of each project leader to insure that the

personnel designated to use the geophysical equipment are qualified in the calibration and use of the

equipment, and able to gather and interpret the data.

Training on the calibration and use of geophysical equipment that is currently available will be

conducted by qualified Branch personnel and will be given to other Branch personnel during in-house

training sessions scheduled throughout the year.
EISOPQAM 15 - 35 November 2001

15.7 References

1. Breed, C. B. and G. L. Hosmer, The Principles and Practices of Surveying Volume I, Elementary

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. Trimble Navigation Limited - Operations Manuals for the following:

Geoexplorer II (1996), P/N 28801-00, Revision B, Ver 2.11

Pathfinder Pro XR (1996), P/N 31172-00, Revision A

TSC1 Asset Surveyor Operation Manual and Software Users Guide (1998), P/N 34182-00-

ENG, Revision A, Ver 4.02

Pathfinder Office Getting Started Guide (1999), P/N 34231-25-ENG, Revision A, Ver 2.50

Mapping Systems General Reference (2000), P/N 24177-01, Revision C

6. Water Measurement Manual, Second Edition, Revised, United States Department of

Interior, Bureau of Reclamation, 1981.

7. NPDES Compliance Inspection Manual, United States Environmental Protection

Agency, September 1984.

8. Stevens Water Resources Data Book, Third Edition, Leopold Stevens, Inc. Beaverton,

Oregon, 1978.

9. “Discharge Measurement at Gaging Stations”, Applications of Hydraulics, Book 3,

Chapter A8, United States Department of Interior, Geological Survey, 1969.

10. “Fluorometric Procedures for Dye Tracing”, Applications of Hydraulics, Book 3, Chapter

A12, United States Department of Interior, Geologic Survey, Revised, 1986.

11. “Measurement of Discharge Using Tracers”, Applications of Hydraulics, Book 3, Chapter

A16, United States Department of Interior, Geologic Survey, 1985.

12. “Measurement of Time of Travel in Streams by Dye Tracing”, Applications of Hydraulics,

Book 3, Chapter A9, United States Department of Interior, Geologic Survey, 1989.

13. Simulation of Soluble Waters Transport and Buildup in Surface Waters Using Tracers,

United States Geological Survey, Open File Report 92-457, 1992.
EISOPQAM 15 - 36 November 2001

14. Discharge-Measurement System Using an Acoustic Doppler Current Profiler with

Applications to Large Rivers and Estuaries, Water Supply Paper 2395, United States

Geological Survey, 1993.

15. Technical Support Document for Water Quality-based Toxics Control, US EPA, Office of

Water, EPA/505/2-90-001, March 1991.

16. SESD/Ecological Investigations Branch Standard Operating Procedures.

17. Benson, Richard, Robert A. Glaccum and Michael R. Noel, Geophysical Techniques for Sensing

Buried Wastes and Waste Migration, National Water Well Association, Dublin, Ohio, 1988.

18. Milson, John, Field Geophysics, Halsted Press, 1989.

19. Operating Manual for EM31-D Non-Contacting Terrain Conductivity Meter, Geonics, Ltd,

Missassauga, Ontario, Canada, June 1984.

20. EM34-3 Operating Instructions, Geonics, Ltd, Missassauga, Ontario, Canada, February 1987.

21. McNeill, J. D., Technical Note TN-8, EM34-3 Survey Interpretation Techniques, .Geonics, Ltd,

Missassauga, Ontario, Canada, January 1983.

22. McNeill, J. D., Technical Note TN-5, Electrical Induction of Soils and Rocks, .Geonics, Ltd,

Missassauga, Ontario, Canada, October 1980.

23. McNeill, J. D., Technical Note TN-6, Electromagnetic Terrain Conductivity Measurements at

Low Induction Numbers, .Geonics, Ltd, Missassauga, Ontario, Canada, October 1980.

24. ABEM WADI Instruction Manual, Atlas Copco, Bromma, Sweden.

25. Breiner, S., Applications Manual for Portable Magnetometers, Geometrics, Sunnyvale, CA,

1973.

26. Model G-856 Proton Precession Magnetometer Operators Manual, EG&G Geometrics,

Sunnyvale, CA.
EISOPQAM 16 - 1 November 2001

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/instrument(s) and by properly calibrating or verifying each instrument

16.1 Introduction

Temperature, specific conductance (conductivity), hydrogen-ion concentration (pH), turbidity,

dissolved oxygen (DO), chlorine, salinity, flash point, and the halogen test are discussed in this section. The

order in which the measurements are made may be important in some field investigations. The parameters

will be discussed in the most applicable order. References for each parameter can be found at the end of the

section. 

Numerous meters/instruments are commercially available. Some meters are capable of multiple

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 ensure consistency. 

Quality Control

All equipment should be maintained and operated in accordance with the manufacturer's instructions.

Regardless of the meter used, it should be properly calibrated or verified prior to use. All field meters with

thermistors are verified against a National Institute of Standards and Technology (NIST) traceable

thermometer, the Hanna Instruments CheckTemp 1 or equivalent, at least semi-annually. This includes, but

is not limited to, the pH, conductivity, and DO meters. These verification checks are documented in a

logbook and maintained at the Federal Equipment Center (FEC). Labels are placed on the field instruments

to indicate when the next verification check is required. Additionally, the CheckTemp 1 is NIST Certified

at least annually and documented. 

The thermistors for all pH, conductivity, and DO meters should be verified in the field with one of

the NIST traceable Fisher brand stem-type digital thermometers. All data for the field verifications should

be documented in the inspector’s logbooks. 

The turbidimeter is calibrated with Formazin Primary Standards semi-annually and a record of the

calibration is maintained on file at the FEC. The Gelex secondary standards will be standardized against the

Formazin Primary Standards by the FEC. The turbidimeter should be verified with the Gelex secondary

standards before each use. These verifications should be documented in the inspector’s logbook.

Standard Methods requires that the conductivity meter’s electrode cell be verified by comparing

against a laboratory meter with a platinum-electrode type conductivity cell. The FEC will perform and

document this quality control check at least annually, especially if the meter is used for NPDES monitoring

activities. A label will be placed on the field instruments to indicate when the next verification check is

required.
EISOPQAM 16 - 2 November 2001

16.2 Temperature

Normally, temperature measurements may be made with any good alcohol-filled thermometer or a

NIST traceable digital thermometer. As a minimum, the thermometer should be capable of reading or have

a scale marked in 0.1 C. For field operations with glass thermometers, a thermometer having a metal case

to prevent breakage should be used. 

Calibration:

Calibrate any temperature measurement device by checking annually against a National Institute of

Standards and Technology (NIST) certified thermometer. Clearly indicate whatever correction must be

applied to the thermometer. 

Note: Thermistors should be checked against a NIST traceable thermometer prior to use and

should agree within ± 4.0 C. Corrections must be applied for measurements up to ± 4.0

C, but the instrumentation must be repaired or replaced beyond that range.

Inspection:

All thermometers should be inspected for leaks, cracks, and/or function prior to use.

Procedures: (Make measurements in-situ when possible)

1. Clean the probe end with de-ionized water and immerse into sample.

2. Swirl the thermometer in the sample for mixing and equilibration.

3. Allow the thermometer to equilibrate with the sample for at least one minute.

4. Suspend the thermometer away from the sides and bottom to observe the reading.

5. Record the reading in the log book. Report temperatures readings to the nearest 0.5 C 

for most applications.

Note: Always clean the thermometer prior to storage and/or use.

Units:

Degrees Celsius (C) or Degrees Fahrenheit (F)

Conversion Formulas:

F = (9/5 C) + 32 or C = 5/9 (F - 32)
EISOPQAM 16 - 3 November 2001

16.3 Conductivity (Specific Conductance)

Conductivity is a measure of the ability of an aqueous solution to conduct an electric current.

Conductivity is customarily reported in micromhos per centimeter (mhos/cm) at 25 C. It is important to

note that if the conductivity measurements are for NPDES reporting purposes, the meter and conductivity

cell should be verified by comparing against a laboratory meter with a platinum-electrode type conductivity

cell. 

Equipment available:

 Orion Model 140 conductivity meter 

Calibration:

 The meter is calibrated in accordance with the manufacturer's instructions by the FEC before it is

taken into the field. A two-point calibration verification should be used to ensure the accuracy of the meter.

The cell constant of the 014000 series cell is automatically set (0.0609/cm) by the meter. All field

conductivity meters are verified against a National Institute of Standards and Technology (NIST) traceable

thermometer, the Hanna Instruments CheckTemp 1 or equivalent, at least semi-annually. These verification

checks are documented in a logbook and maintained at the Federal Equipment Center (FEC). Labels are

placed on the conductivity meters to indicate when the next temperature verification check is required. 

 Conductivity is affected by temperature; therefore, temperature should be read first so that

appropriate adjustments can be made in accordance with the manufacture’s instructions and the method.

Fresh standards should be obtained and used for each field trip. Discard standard solutions after each

calibration verification.

1. Make sure the meter is warmed up as per manufacturer’s directions. Verify the meter’s internal

temperature sensor against a NIST traceable Fisher brand stem-type digital thermometer, or

equivalent, and note any differences in your logbook. If the temperature readings agree within

± 4  C, apply any necessary correction factor and proceed with measuring the temperature of

the standard solutions within 0.5 C. If the temperatures do not agree within ± 4  C, the unit

must be repaired or replaced. Substitute the NIST traceable thermometer for temperature

readings and apply necessary corrections. Check and record the temperatures of the standards

and the samples.

2. Rinse the probe with de-ionized water and blot dry before immersing it in the standard solution.

One standard should be close to 1412 mhos/cm (0.01 M KCL) and the other standard should

be in the expected range of the samples being measured.

3. Immerse the probe in the first standard solution (0.01 M KCL) and record the results. The

difference between the standard and the measured result is how the cell constant is determined.

Document the measurement in the logbook to calculate the cell constant to be used in the

calculations if necessary. 

4. Rinse the probe, blot dry and immerse it into the second standard solution and record results.

If the meter is not accurate to within ± 10% of the second standard, the cell should be repaired

or replaced if possible. If this is not possible, the cell constant can be adjusted by pressing the

C.TC.C key until the cursor in right LCD display indicates “TC”. Adjust TC to 0.00 by using

the up/down scroll keys. Press the C.TC.C key to select the C mode. Immerse cell into a

solution of known conductivity (e.g, 445 mhos/cm @ 25 C). Press the up/down scroll keys

until the meter indicates the known conductivity of the solution in the left LCD display. The

new cell constant will now be shown in the meter C display (right LCD display). Document the

readings before proceeding. 
EISOPQAM 16 - 4 November 2001

Procedures:

1. Collect the sample, check and record its temperature. If possible, allow the sample to come to

room temperature (23 to 27 C).

2. Correct the instrument’s 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 center portion of the probe be wetted by the sample. 

4. Allow meter to stabilize. Record the results in a log book.

5. Rinse probe with de-ionized water.

Units:

The Orion Model 140 conductivity meter has automatic temperature compensation and will read out

directly in mhos/cm corrected to 25 C. If another meter is used that is not temperature correcting, a

correction must be applied. If the sample temperature is below 25 C, add 2% of the reading per degree.

If the temperature is above 25C, subtract 2% of the reading per degree. Results should be reported to the

nearest ten (10) units for readings below 1,000 mohs/cm @ 25C and to the nearest one hundred (100) units

for reading above 1,000 mohs/cm @ 25C. 

16.4 Hydrogen Ion Concentration (pH)

The pH is defined as the negative logarithm of the effective hydrogen-ion concentration. For routine

work use a pH meter accurate and reproducible to 0.1 pH unit with a range of 0 to 14 and equipped with a

temperature-compensation adjustment. 

Meter(s) available:

 Orion Model 230A or 290A

 Hydrolab Surveyor II

 YSI 3530, 3500 Water Quality Monitoring System

Calibration: Because of the wide variety of pH meters and accessories, detailed operating instructions

cannot be incorporated into this method. Each analyst should become acquainted with the operation of the

meter used and follow manufacturer's instructions. The following calibration guidelines are minimum

requirements. 

The meter is calibrated in accordance with the manufacturer's instructions by the FEC before it is

taken into the field. A two-point calibration verification should be used to ensure the accuracy of the meter.

All field pH meters are verified against a National Institute of Standards and Technology (NIST) traceable

thermometer, the Hanna Instruments CheckTemp 1 or equivalent, at least semi-annually. These verification

checks are documented in a logbook and maintained at the FEC. Labels are placed on the pH meters to

indicate when the next temperature verification check is required. 
EISOPQAM 16 - 5 November 2001

Note:

1. Make sure the meter is warmed up as per manufacturer’s directions. Verify the meter’s

internal temperature sensor against a NIST traceable Fisher brand stem-type digital

thermometer, or equivalent, and note any differences in the logbook. If the temperature

readings agree within ± 4  C, apply any necessary correction factor and proceed with

measuring the temperature of the standard solutions within 0.5 C. If the temperatures do

not agree within ± 4  C, the unit must be repaired or replaced. Substitute the NIST

traceable thermometer for temperature readings and apply necessary corrections. Check and

record the temperatures of the standards and the samples.

2. 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, calibrate the pH

meter with the two buffers that bracket the expected pH range. Select either pH 4 and 7 or

pH 7 and 10 buffer solutions.

3. Rinse the probe with de-ionized water, blot dry and immerse it into the first buffer (pH 7)

and calibrate the meter to read the correct pH.

4. Rinse the probe with de-ionized water, blot dry and immerse it into the second buffer and

calibrate the meter to read the correct pH. Record the buffer values / temperatures used to

calibrate the meter.

5. Rinse the probe with de-ionized water, blot dry and immerse it into the original buffer (pH

7) and read as a sample. If the meter reads within ± 0.1 pH unit of the known value of the

buffer, record the value returned by the meter.

6. Rinse the probe with de-ionized water, blot dry and immerse it into the second buffer used

(pH 4 or 10) and read as a sample. If the meter reads within ± 0.1 pH unit of the known

value of the buffer, record the value returned by the meter.

7. Rinse the probe with de-ionized water and store it in the manufacturer’s recommended

storage solution. Leave the meter on until all sample measurements are performed and the

results are recorded. It is recommended that the meter be checked periodically against the

known buffer values if used for extended periods (> 4 hrs).

8. If the meter is turned off, it must be recalibrated.

Procedures:

1. Collect a sample. Measure the temperature prior to measuring the pH.

Note: When the pH meter response is slow, unstable, or non-reproducible, it 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 mls of sample. Recheck the pH and

record.

2. Immerse the probe in the sample keeping it away from the sides and bottom of the sample

container. Allow ample time for the probe to equilibrate with the sample while gently

stirring the sample.
EISOPQAM 16 - 6 November 2001

3. While suspending the probe away from the sides and bottom of the sample container, record

the pH.

4. Rinse the probe with de-ionized water and store it in a de-ionized water filled container until

the next sample is ready.

Operational check:

1. While in use, periodically check the pH by rinsing the probe with de-ionized water, blot dry

and immerse it into the pH 7 buffer solution.

2. Perform a post calibration verification at the end of the day and record all measurements.

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  11.0) of the scale, the pH measurements should be

made by a qualified analyst using laboratory quality equipment to control the sample at

25C +1oC.

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 2100P Portable Turbidimeter

Calibration:

1. The turbidimeter is calibrated with Formazin Primary Standards semi-annually by the FEC and

a record of the calibration is maintained on file at the FEC. Labels are placed on the

turbidimeters to indicate when the next calibration is required. The turbidimeter should be

verified with the Gelex secondary standards in the field before each use. The Gelex Secondary

Standards are supplied with the instrument, but must be assigned values before use after the

formazin calibration. If the instrument readings do not agree within ± 10 % of the Gelex

standards, the unit must be recalibrated, repaired or replaced. These verifications should be

documented in the inspector’s logbook.

2. Turn the meter "ON".

3. Rinse the sample cell 3 times with organic free or de-ionized water.

4. Fill the cell to the fill line with organic free or de-ionized water and then cap the cell.

5. Use a non-abrasive lint-free paper or cloth (preferably lens paper) to wipe off excess water and

streaks.
EISOPQAM 16 - 7 November 2001

6. Open the cover and insert the cell (arrow to the front) into the unit and close the cover.

7. Press "READ" and wait for the 'light bulb' icon to go off. Record the reading.

8. Using the Gelex standards, repeat steps 4, 5, and 6. Record all measurements (note anomalies).

Procedures:

1. Collect a representative 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 (about

15 mL) and replace the cap on the cell.

2. Wipe off excess water and any streaks with a soft, lint-free cloth (lens paper). 

3. Press I/O and the instrument will turn on. Place the meter on a flat, sturdy surface. Do not hold

the instrument while making measurements.

4. Insert the sample cell in the in the instrument so the diamond or orientation mark aligns with the

raised orientation mark in the front of the cell compartment. Close the lid.

5. Select manual or automatic range selection by pressing the range key. 

6. Select signal averaging mode by pressing the Signal Average key. Use signal average mode if

the sample causes a noisy signal (display changes constantly).

7. Press Read. The display will show ---- NTU. Then the turbidity in NTU. Record the result after

the lamp symbol turns off. 

8. Rinse the cell with de-ionized water.

9.. For the next sample, repeat Steps 1-8.

Operational check:

1. Periodically check the turbidity meter during the day by using the gelex secondary standards

provided.

2. Preform a post calibration at the end of the day and record all measurements.

Units:

Turbidity measurements are reported in nephelometric turbidity units (NTUs). It is important to note

that if the turbidity measurements are for NPDES reporting purposes, all values above 40 NTU must be

diluted with turbidity free water and calculated by multiplying by a dilution factor. 
EISOPQAM 16 - 8 November 2001

16.6 Salinity

Salinity is the measure of salts of the alkali metals or of magnesium found in water. This

measurement 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. Salinity is the total amount of salts (in grams)

in 1 Kg of sea water expressed as parts per thousand.

Meters available:

 Beckman Model RS5-3 Portable Salinometer

 Hydrolab Surveyor II

 Scout

 Datasone Salinometer

Calibration/Maintenance:

 Follow the manufacturer’s 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 at 1%

full scale conductance at ± 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 in the nearest tenth of a ppt (0.1 ppt).

16.7 Dissolved Oxygen (DO)

Meter available:

 YSI Models 55, 57 or 58 membrane-covered electrode (ME) DO meter

Membrane-covered electrode systems utilize a sensing element that is protected by an oxygenpermeable membrane that serves as a diffusion barrier against impurities. The meters for

determining the DO in water are dependent upon electrochemical reactions. Under steady-state

conditions the current is directly proportional to the DO concentration. 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 probe 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 water prior to calibration of the meter.
EISOPQAM 16 - 9 November 2001

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 calibrated against the Winkler method as a QC check 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/l and record the measurement.

To Collect a Sample:

1. When possible, measure the DO in-situ with a field probe; otherwise,

2. Collect the sample by completely filling a 300-ml BOD bottle, stopper and measure the DO

with a laboratory type probe.

Note: Special care should be exercised to avoid entrainment 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.

4. If a Kemmerer sampler is used, the BOD sample bottle should be filled to overflowing by

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/l.

Units:

Units should be reported in mg/l.

Limitations:

 Dissolved inorganic salts are a factor with the performance of DO probes.

Note: Make note if inorganic salts are present in levels that may represent possible

interferences.

 Dissolved oxygen ME probes are temperature sensitive, and temperature compensation is

normally provided by the manufacturer (see manufacturer’s instructions).
EISOPQAM 16 - 10 November 2001

16.8 Total Residual Chlorine

Meter(s) available:

 Pocket colorimeter

8. Specific ion electrode

 Hach DR-100 Colorimetric (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 preprinted 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 (4-5) 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 depending upon concentration range of the sample.

Inspection:

 Each meter should be visually inspected before and after each use. Report any problems 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 residual chlorine powder packets.

Note: The packets deteriorate in the presence of moisture or high temperature. The packets

should be discarded if they have caked or have turned brown.

Always wear gloves when handling the DPD oxalate. Do not ingest the DPD oxalate.

If accidentally spilled on skin, rinse off immediately.

 Chlorine demand-free water (See Standard Methods, Method 4500 Cl for directions in preparing

the ASTM Standard D1193 "Consumption of Potassium Permanganate").
EISOPQAM 16 - 11 November 2001

 Potassium permanganate stock -- Prepare a stock solution containing 891 mgs/1000 mls. Keep

stock cool and store in the dark.

 Potassium permanganate intermediate stock 10 ppm – Prepare intermediate stock solution

containing 10 mg/l KMnO4 by diluting 10 mls of stock solution to 1 liter. 

Note: The intermediate stock should be stable for approximately 5 days if kept cool and

away from light.

 Potassium permanganate calibration standards -- Prepare calibration standards from the

intermediate stock solution and/or KMnO4 calibration standard solutions for each day of use.

The calibration standards are good for about 2 hours and will fade rapidly (within 15 minutes)

if chlorine demand-free water is not used.

Calibration Standard (mg/l) mls of Intermediate Stock/100 mls

 0.05 10.0 of 0.5 mg/l std.

 0.10 10.0 of 1.0 mg/l

0.5 5.0 of 10 mg/l

1.0 10.0 of 10 mg/l

2.0 20.0 of 10 mg/l

Procedures: for total chlorine concentrations ranging between 0 - 2 mg/l

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

sulfuric acid or 1N 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 particles 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 manufacturer’s instructions for reaction times). The reaction times for standards and

samples should be as close to each other as possible.

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 November 2001

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. If measuring high levels, use the

1 cm cell.

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/l:

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 ± 0.05 mg/l for the lower range

(0.5 mg/l), and agree within 0.2 mg/l for the mid-range (0.5 - 2.0 mg/l) and agree within 

0.4 mg/l for the high range(2.0 - 3.5 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 g/l MnO4  g/l Cl2).

 Colored matrices may also interfere.
EISOPQAM 16 - 13 November 2001

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 reproducibility for this instrument are in accordance with the respective

standards:

 p-xylene 78.0 ± 1.0F

 n-butanol 97.9 ± 1.7F

 n-undecane 145.4 ± 2.0F

 n-hexadecane 270.5 ± 2.0F

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 (140F for determining ignitability

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.

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.
EISOPQAM 16 - 14 November 2001

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.

16.10 Halogen Test

This method is used to qualitatively screen wastes for the presence of halogenated compounds.

Test 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  to 1⁄2 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 1⁄2 to 1 minute).
EISOPQAM 16 - 15 November 2001

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 tip 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.

Note: A bright green flame indicates the presence of halogenated material.
EISOPQAM 16 - 16 November 2001

16.11 References

Temperature

1. Standard Methods for the Examination of Water and Wastewater, 18th Edition p. 2-59, Method 2550

B (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. 2-43, Method

2510B (1992).

4. Annual Book of ASTM Standards, Vol. 11.1, "Water," Standard D1125-91A, 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. YSI Model 3560 Water Quality Monitoring System Instructions, July, 1988.

Hydrogen Ion Concentration (pH)

9. Standard Methods for the Examination of Wastewater, 18th Edition, p. 4-65, Method 4500-H+

(1992).

10. Instruction Manual for Models 399 A/F, 399 A/L Analog pH 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 System for the Model 3530 pH Electrode

Assembly.

13. Annual Book of ASTM Standards, Part 31, "Water", Standard D1293-78(B).

14. Methods for Chemical Analysis of Water and Wastes, US-EPA, 150.1 (1983).

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.

Turbidity

17. Operating procedures for the Hach 2100P Turbidimeter

Dissolved Oxygen
EISOPQAM 16 - 17 November 2001

18. Standard Methods for the Examination of Water and Wastewater, 18th Edition, p. 4-100, Method

4500-0C (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 Springs

Instrument Company.

Chlorine - (DPT Colorimetric)

23. Annual Book of ASTM Standards, "Water," Standard D 1253-86(92).

24. 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- CL G (1992).

28. Instruction Manual, DR 100 Colorimeter, Model 41100-02, DPD Method for Chlorine, Hach

Company, June 1983.

Salinity

29. Standard Methods for the Examination of Water and Wastewater, 18th Edition, p. 2-47 Method 2520

B (1992).

30. Instruction Manual, RS5-3 Portable Salinometer, Beckman Instruments, Inc., Revised March 1973.

Flash Point

31. Rapid Tester Model RT-1 Technical Manual, Operations and Service, November 1, 1989.
EISOPQAM 17 - 1 November 2001

SECTION 17

AIR MONITORING SAFETY EQUIPMENT

CALIBRATION PROCEDURES

17.1 Introduction 

This section gives specific procedures to be followed when calibrating air monitoring

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 to 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 flamability or toxic exposure limits. 

 Gas cylinders will not be sent to the field if they contain less than one-fifth of their full capacity.

Cylinders below the required volume will be utilized in the warehouse for equipment check-out

and maintenance.

Calibration mixtures and approximate concentrations for specific air monitors will be as follows:

CALIBRATION GASES

MONITOR GAS MIXTURE CONCENTRATION

Combustible Gas Pentane in Air ~ 0.75%

Flame Ionization Methane in Air ~ 75 ppm

Photo-Ionization Detector Toluene in Air ~ 100 ppm

Calibration Equipment

All calibrations will consist of introducing a gas of known concentration into the monitor at

atmospheric pressure. Under no circumstances will it be acceptable to attempt calibration when the monitor

is measuring gas concentrations below or above atmospheric pressure.

 
EISOPQAM 17 - 2 November 2001

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 fittings. The Teflon® bag is

omitted for calibration of the OVA. 

The calibration gas cylinder will be connected to the "T" fitting with Teflon® tubing so that the gas

will flow directly through the top of the "T" into a Teflon® bag. 

The "T" fitting and tubing will be purged with calibration gas prior to connection of the Teflon® bag.

The bottom 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

It 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

Battery Check Response

Alarm Response

Instrument Response

Calibration Gas Concentration

Fuel Level (FID)

Operator's Initials
EISOPQAM 17 - 3 November 2001

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 warn

the user when pre-determined 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 grain 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 fitting and the

water drop-out bottle fitting for tightness.

2. Place the monitor's "ON-OFF" switch in the "HORN OFF" position. 

 Note that 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" button and record the battery reading from the "% LEL" meter.

5. Set the "% OXYGEN" meter to read 20.8% using the "CALIBRATE O2" 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 by 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 17 - 4 November 2001

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 that the function switch is in the "ON" position and that the green flow indicator is

steadily illuminated.

4. Attach the probe to the probe line.

17.3 Photovac Microtip Photoionization Detector

Note: Some Microtips are NOT instrinscially safe

Introduction

The detector is capable of measuring concentrations down to about 1 ppm sensitivity for certain

compounds. It cannot be used to identify unknown substances, it can only quantify them. Wind 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 be used to detect aromatic compounds such as benzene, toluene,

and styrene; aliphatic amines such as diethylamine; and chlorinated unsaturated compounds such as vinyl

chloride and trichloroethylene. 

 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 NONINTRINSICALLY SAFE MICROTIP IN CONFINED SPACES

UNLESS CLEARED WITH AN EXPLOSIMETER
EISOPQAM 17 - 5 November 2001

Operational Information

Turn the instrument on by 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

information will appear on the display: 

Instrument Status

Ready

Current Detected

Concentration

2000 ppm

008

Event Number

10:15 Feb 15

Time Date

The Microtip then operates automatically. The user reads the concentration directly from the display.

The display updates itself each half second.

The following describes the procedure for setup and calibration of the MicroTip. Consult the manual

for other information and instructions.

SETUP

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 output. Use the up and down arrow keys to select the 20,200 or

2,000 parts per million (ppm) range.

3. Next the Cal memory is selected. The instrument has five Cal Memories for regular operation

and one for High Sensitivity 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 values for the current time. Press ENTER after each value.

5. Enter the numerical values for the day, month, and year. Again press ENTER after each

selection.

The instrument is now set for operation.
EISOPQAM 17 - 6 November 2001

ALARM

1. Press ALARM.

2. The current alarm is displayed. If the value is correct (5 ppm) wait for the display 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.

CAL

Clean outdoor air is suitable as Zero Gas. Toluene is used as the calibration gas.

1. Press SETUP and check all display information. Select a Cal Memory (usually #1) with the

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 (typically ambient air).

Press ENTER and the zero point is set.

5. The instrument then asks for the Span Gas concentration. Enter the known concentration from

the toluene gas cylinder (e.g. 97.3 ppm) and press ENTER.

6. Connect the span gas bag to the sample inlet.

7. Press ENTER and wait until the display reverts to normal..

8. The instrument is calibrated and ready for use.

17.4 Toxic Vapor Analyzer (TVA 1000B)

Introduction

The Toxic Vapor Analyzer (TVA 1000B) is a portable inorganic/organic vapor monitor. This

analyzer uses both a flame ionization detector (FID) and a photoionization detector (PID) to sample

and measure concentrations of gases. 

Hydrogen Tank for the FID

When the TVA 1000B leaves the Field Equipment Center (FEC), the hydrogen tank will be full and

the battery will be charged. Ensure that any extra hydrogen tanks taken to the field are filled also.

Note that you must always screw the hydrogen tank into the unit when taking the TVA out 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. 
EISOPQAM 17 - 7 November 2001

Operating Procedures

The TVA 1000B is user friendly/menu driven. Pressing the “EXIT” key will take you to the

previous menu.

To operate the TVA 1000B, follow the procedures listed. The instrument must be on and warmed

up for approximately 30 minutes prior to calibration. The pump must be ON, the PID lamp must

be ON, and the FID must be ignited throughout the warm-up period.

NOTE: If only one of the 2 detectors is desired, calibrate only that detector.

INSTRUMENT STARTUP PROCEDURES

1. Ensure that internal battery is charge.

2. Connect sample probe.

3 Fill/install the hydrogen tank, (left handed thread, turn counter-clockwise until resistance is felt).

4. Turn red H2 Supply valve to ON position if using FID.

5. Press ON

6. Press CONTROL

7. Press 1=Pump on

8. Press CONTROL

9. Press 2=FID on

10. Press CONTROL

11. Press 3=Ignt

12. Press CONTROL

13. Press 4=PID on

Allow instrument to warm up for approximately 30 minutes.

INSTRUMENT SETUP

While instrument is warming up, check the following:

ALARMS

1. From Main Menu press 2=Setup

2. Press 2=Alarm

3. Press 1=STEL, if needed
EISOPQAM 17 - 8 November 2001

Press 1=Both

Enter STEL value, press Enter=Accept

4. Press 2=Low Ceiling

Press 1=Both

Set level at 5.0 ppm, press Enter=Accept

5. Press 3=High Ceiling

Press 1=Both

Set level at 200 ppm, press Enter=Accept

6. Press EXIT

OTHER

1 Press 6=Other

2. Press 2=Date to verify date, change if needed

3. Press 3=Time to verify time, change if needed

Other settings should not need to be changed.

4. Press EXIT

CALIBRATION CONFIGURATION

1. Press 1=Calib

2. Press 1=Cfg

3. Press 1=Number span pt

Verify that value is 1 for both detectors

4. Press EXIT

5. Press 2=Background correct

Select background correction option, 1=Both, 2=None, 3=PID or 4=FID

6. Press EXIT

7. Press DOWN arrow

8. Press 1=Accept Mode

9. Choose 1=Manual or 2=Auto

Auto - Instrument analyzes the gas sample until values stabilize and then stores the final value.

Manual - User monitors gas sample measurements (in counts) and presses ENTER to store the

value.

10. Press EXIT
EISOPQAM 17 - 9 November 2001

11. Press 2=Save Mode

12. Choose 1=Manual or 2=Auto, User choice, but Manual is recommended.

13. EXIT

14. Press DOWN arrow

15. Press 1=RF calc mode

Press 1=Factor

16. Press EXIT

SPAN CONCENTRATION

1. Press 2=SpanConc

DOWN arrow will change units of measure, select ppm with 1 decimal point

2. Press 2=PID and enter concentration of toluene (e.g. 97.3ppm)

3. ENTER=Accept

4. Press 2=SpanConc

DOWN arrow will change units of measure, select ppm with 1 decimal point

5. Press 3=FID and enter concentration of methane (e.g. 76.5ppm)

6. ENTER=Accept

RESPONSE FACTOR

1. Press 5=RF

Select RF0: DEFAULT (Response Factor will be 1)

2. ENTER=Accept

CALIBRATION PROCEDURE

If the instrument has been warmed-up for approximately 30 minutes, continue with calibration.

Fill appropriate teflon bags with calibration gases:

Toluene - PID

Methane - FID

Zero Air - Both

1. From Calib Menu Press 3=Zero

2. Press 1=Both

3. Connect Zero Air bag to probe

4. Press Enter=Start

In Manual mode, after “counts” stabilize press Enter=Accept.

In Auto mode, instrument will accept value automatically.
EISOPQAM 17 - 10 November 2001

5. Press 4=Span

6. Press 2=PID

7. Connect Toluene bag to probe

8. Press Enter=Start

In Manual mode, after “counts” stabilize press Enter=Accept.

In Auto mode, instrument will accept value automatically.

9. Press 4=Span

10. Press 3=FID

11. Connect Methane bag to probe

12. Press Enter=Start

In Manual mode, after “counts” stabilize press Enter=Accept.

In Auto mode, instrument will accept value automatically.

Calibration Complete

1. Press EXIT

2. From MAIN MENU press 1=Run

3. Check response of each detector by applying the appropriate calibration gases to the instrument.

Methane for the FID and Toluene for the PID. Record responses.

4. Instrument is ready to use. To power down the instrument press and hold the OFF key. Also

turn the red H2 supply handle to the OFF position.

5. For more information on multi-point calibration, logging and data transfer, consult manual.
EISOPQAM 17 - 11 November 2001

TVA 1000B DISPLAY MENU STRUCTURE

RUN SETUP INFO PCLINK/MEMORY

 

CALIBRATION PC LINK

  CONFIG  CHANGE TYPE

   NUMBER SPAN PTS   ESTABLISH LINK

   BACKGROUND CORRECT 

   ACCEPT MODE  CLEAR ROUTE &

   SAVE MODE LOGGING MEMORY

   RF CALC MODE

  SPANCONC (Enter Span Gas Conc)

  ZERO (CALIB)

  SPAN (CALIB)

  RESPONSE FACTOR

   CHANGE

    NAME

    VALUE

   ACCEPT

  BACKGROUND (CONC UPDATE)

ALARMS

 STEL

 LOW CEILING

  HIGH CEILING

LOG

 NONE

 AUTO

 VOC/FE

  VOC

   FE

  CUSTOM

PASSCODE

 NEW PASSCODE

 ENABLE

  DISABLE

HARDWARE

 PROBE DISPLAY

  BASIC

   ENHANCED

  BARCODE READER

 SELECT READER

  NONE

  HP SMART WAND

   PSC LASER

  INITIALIZE READER

 OTHER

 USER ID

 DATE

 TIME

  USER OPTIONS

 KEY CLICK

  DISPLAY DELAY

1 2 3 4
EISOPQAM 17 - 12 November 2001

17.5 Toxic Vapor Analyzer (TVA 1000A)

Introduction

The Toxic Vapor Analyzer (TVA 1000A) is a portable inorganic/organic vapor monitor. This

analyzer uses both a flame ionization detector (FID) and a photoionization detector (PID) to sample

and measure concentrations of gases. 

Hydrogen Tank for the FID

When the TVA 1000A leaves the Field Equipment Center (FEC), the hydrogen tank will be full and

the battery will be charged. Ensure that any extra hydrogen tanks taken to the field are filled also.

Note that you must always screw the hydrogen tank into the unit when taking the TVA out 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

The TVA 1000A is user friendly/menu driven. Pressing the “EXIT” key will take you to the

previous menu.

To operate the TVA 1000A, follow the procedures listed. The instrument must be on and warmed

up for approximately 30 minutes prior to calibration. The pump must be ON, the PID lamp must

be ON, and the FID must be ignited throughout the warm-up period.

NOTE: If only one of the 2 detectors is desired, calibrate only that detector.

INSTRUMENT STARTUP PROCEDURES

1. Ensure that internal battery is charge.

2. Connect sample probe.

3 Fill/install the hydrogen tank, (left handed thread, turn counter-clockwise until resistance is felt).

4. Turn red H2 Supply valve to ON position if using FID.

5. Press ON key

6. Wait for self-test diagnostic to complete.

7. Press CONTROL

8. Press 1=Pump on

9. Press CONTROL

10. Press 2=Ignite

11. Press CONTROL
EISOPQAM 17 - 13 November 2001

12. Press 3=Turn PID On

Allow instrument to warm up for approximately 30 minutes.

INSTRUMENT SETUP

While instrument is warming up, check the following:

ALARMS

1. From Main Menu press 2=Setup

2. Press 2=Alarms

3. Press 1=STEL, if needed

Press 1=Both

Enter STEL value, press Enter=Accept

4. Press 2=Low Ceiling

Press 1=Both

Set level at 5.0 ppm, press Enter=Accept

5. Press 3=High Ceiling

Press 1=Both

Set level at 200 ppm, press Enter=Accept

6. Press EXIT

INFO

1. From Main Menu press 3=Info

2. Press the UP or DOWN arrows to scroll through information about instrument.

Pressing the UP arrow once will show screen with battery status.

3. Press EXIT

OTHER SETTINGS

1. From Main Menu press 2=Setup

2. Press 5=Othr

3. Press 2=Time to verify time, change if needed, if not, press “EXIT”

4. Press 3=Date to verify date, change if needed, if not, press “EXIT”

5. Press 4=User Options

6. Press 1=Key Click

7. Press 1=On or 2=Off, User choice
EISOPQAM 17 - 14 November 2001

8. Press 2=Display Delay

9. Press 1=Short

10. Press 3=Calib Mode

11. Press 1=Manual or 2=Auto, User choice, but Manual recommended

Auto - Instrument analyzes the gas sample until values stabilize and then stores the final value.

Manual - User monitors gas sample measurements (in counts) and presses ENTER to store the

value.

12. Press EXIT

Other settings should not need to be changed.

13. Press EXIT again to return to SETUP MENU

CALIBRATION MENU

SPAN CONCENTRATION

1. Press 1=Calibration

2. Press 4=GasConc

3. Press 2=PID

DOWN arrow will change units of measure, select ppm with 1 decimal point.

Enter concentration of toluene (e.g. 97.3ppm)

4. Press Enter=Accept

5. Press 4=GasConc

6. Press 3=FID

DOWN arrow will change units of measure, select ppm with 1 decimal point.

Enter concentration of methane (e.g. 76.5ppm).

7. Press Enter=Accept

RESPONSE FACTOR

8. Press 5=Response Factor

9. Press 1=Both and enter value of 1.00.

10. Press Enter=Accept
EISOPQAM 17 - 15 November 2001

CALIBRATION PROCEDURE

If the instrument has been warmed-up for approximately 30 minutes, continue with calibration.

Fill appropriate teflon bags with calibration gases:

Toluene - PID

Methane - FID

Zero Air - Both

1. From Calibration Menu Press 1=Zero

2. Press 1=Both

3. Connect Zero Air bag to probe

4. Press Enter=Start

In Manual mode, after “counts” stabilize press Enter=Accept.

In Auto mode, instrument will accept value automatically.

5. Press 2=Background

6. Press 1=Both

7. Press Enter=Start

In Manual mode, after “counts” stabilize press Enter=Accept.

In Auto mode, instrument will accept value automatically.

8. Press 3=Span

9. Press 2=PID

10. Connect Toluene bag to probe

8. Press Enter=Start

In Manual mode, after “counts” stabilize press Enter=Accept.

In Auto mode, instrument will accept value automatically.

9. Press 3=Span

10. Press 3=FID

11. Connect Methane bag to probe

12. Press Enter=Start

In Manual mode, after “counts” stabilize press Enter=Accept.

In Auto mode, instrument will accept value automatically.

Calibration Complete

1. Press EXIT

2. Press EXIT again.
EISOPQAM 17 - 16 November 2001

3. From MAIN MENU press 1=Run

4. Check response of each detector by applying the appropriate calibration gases to the instrument.

Methane for the FID and Toluene for the PID. Record responses.

5. Instrument is ready to use. To power down the instrument press and hold the OFF key. Also

turn the red H2 supply handle to the OFF position.

6. For more information on multi-point calibration, logging and data transfer, consult manual.

17.6 Century Model OVA-128 Organic Vapor Analyzer

Introduction

The Century Model OVA-128 Organic Vapor Analyzer (OVA) is designed to detect organic

compounds in air.

 It uses a hydrogen flame ionization detector (FID) as its detection principle. This detector

allows the monitor to respond to a wide variety of organic compounds, but limits its sensitivity

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 fittings 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 by 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 "X10" position.

 6. Use the "CALIBRATE" knob to set the readout to a reading of 6. Using the Alarm Level

Adjustment Knob on the back of the readout, obtain an audible response to the reading of 6.

 7. Set the "Calibration Switch" to the "X1" position.

 8. Use the "CALIBRATE" knob to set the readout to a reading of 0, and check to insure that the

flame-out alarm is audible.

 9. Place the "PUMP" switch in the ON position and observe that the "SAMPLE FLOW RATE"

indicator shows flow.

 10. Open the "H2 TANK VALVE" and the "H2 SUPPLY VALVE" one turn each. Allow fuel to flow

 for about 1 minute.
EISOPQAM 17 - 17 November 2001

 11. Press ignitor button and hold until readout unit indicates ignition.

 12. Use "CALIBRATE" knob to 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.

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 "X1" position before entering the site.

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 volt GeigerMueller Tube (GMT) measurement of beta and gamma radiation. The range of the meter is from 0 to 200

milliroentgen per hour. It is important that the operator realizes that this meter will not respond to most alpha

radiation.

 THE LACK OF A RESPONSE ON THIS METER DOES NOT GUARANTEE THAT THE

ENVIRONMENT IS SAFE.

Operational Checks

1. Place the multifunction switch in the "BAT" position and note the meter's reading.

2. Place the multifunction switch in the "X0.1" 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 flat against the casing of a certified Sr90 standard.

3. Adjust the multifunction switch until the meter reading remains on scale.
EISOPQAM 17 - 18 November 2001

4. Read and record the meter's response.

5. Calculate the detector's efficiency as follows:

E = Meter Reading - Background

Activity

6. Check to insure that the calculated efficiency is within + 0.1 of the efficiency rating placarded

on the meter.

7. Set the multifunction switch to "X0.1" before entering the site.

17.8 MiniRAE 

Introduction

The MiniRAE (RAE) is a programmable photoionization detector (PID) that measures organic

vapors in hazardous environments. It incorporates a sampling pump and data download capabilities for

continuous toxic monitoring, site survey, and leak detection. The RAE can measure double-bonded organic

vapors with its supplied 10.6 eV gas 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-set. The

keys you will need to press will generally deal with calibration. 

 The battery on the RAE drains slowly even when turned off. If the unit has not been charged

for 4-5 days, the battery voltage will be low. If the unit is left to charge overnight, it will

automatically shut itself off when fully charged. 

 Only operate the RAE in the survey mode. The RAE has been pre-set to automatically start in

the survey mode. 

Operating Procedures

1. Power On/Off

To Turn On the RAE press the [on] key. The audio buzzer will beep once and the display will

show "HG-x.xx" or "Su-x.xx" to indicate the operating mode and software version number. The

unit will then go through a self-diagnostic routine to check the key components of the unit.

A ".diag.." message will be displayed with a red back light turned on while the self-diagnostic

routine is executing. The red LED and back light will flash once and the buzzer will beep once

to ensure that they are functional. The sampling pump will be turned on and start to draw air

sample. 

To turn Off the RAE press the [on] key. The message "off" will flash on the LED display;

press the [enter] key to confirm and the unit will be turned off. Pressing any other key will

return the unit to normal operation. 
EISOPQAM 17 - 19 November 2001

2. The RAE can display five different readings: instantaneous gas concentration, STEL, TWA, and

peak and battery voltage. Most of these functions have either been pre-set or do not apply to

most Branch surveys. Only press [enter] to scroll through each display. 

3. Alarm Signal - The built-in microcomputer constantly updates and monitors real time gas

concentrations and compares it with the programmed alarm limits. Whenever the

concentration exceeds any of the preset limits (5 ppm), the alarm buzzer and red flashing

LED will be activated immediately to warn the user of the alarm condition. 

Whenever the battery 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. 

In the Survey Mode, the alarm signal is proportional to the level of the gas concentration.

Therefore, when the gas concentration exceeds preset limits (5 ppm), the alarm signal may 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 signal

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] key. When the

back light is already on, pressing the [up] key will turn it off. 

5. Charging the RAE - On the back side of the RAE is a battery charging jack which is normally

covered by a protective rubber cover. Open the rubber cover and connect the AC adapter (or 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 - battery 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 the 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 may re-calibrate the RAE. This is a two-point calibration process using

Zero Gas and a Standard Reference Gas. 

1. First, a zero gas which contains no detectable organic vapors is used to set the zero point (CO).

2. Second, a standard reference gas is used to set the second point of reference (C1). 

Zero gas Calibration

Use a gas bag (1 liter) and zero concentration gas from your air box.

1. 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.
EISOPQAM 17 - 20 November 2001

2. Attach the gas bag to the inlet tube and open the bag so that the instrument can begin pumping

the zero concentration gas. The display should be reading zero. 

3. If this reading is not zero, press the [enter] key to zero it. If the reading still shows a small value

after a few seconds, press the [enter] key again to zero it. Repeat this process until the reading

is stabilized around zero or 0.1 ppm. This completes the zero gas calibration. Press the [menu]

key to exit zero gas calibration while the bag is still on the instrument. 

Enter Standard Calibration Gas Value

1. 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 displayed value,

press [enter] key 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 displayed

value, the user needs to enter the new value. Starting from the left most digit of the displayed

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 now. 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] key, the display should show CAL.... for about 30 seconds while the instrument

performs calibration. Afterwards, the display shows C1 xxx.x where C1 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 reading should be very 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 that

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 accordingly. 

3. Press the [menu] key to exit the standard gas calibration procedure and move to next menu item.

4. Disconnect the calibration gas bag.
EISOPQAM 18 - 1 November 2001

SECTION 18

WASTEWATER FLOW MEASUREMENT

18.1 Introduction

The measurement of flow with surface water and wastewater sampling is essential to almost all water

pollution control activities. Activities such as water quality enforcement studies, NPDES permit compliance

monitoring, water quality monitoring, municipal operation and maintenance investigations 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

calculations of mass loadings are also frequently necessary for water quality studies and other purposes. As

much attention and care should be given to 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 quality

surveys;

 present acceptable, commonly 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

beyond the scope of this section. However, most of the commonly used techniques are covered in general

terms. A comprehensive list of references is included at the end of this section, and a detailed discussion of

flow measurement techniques may be found in the references.

18.2 Wastewater Flow Measurement

18.2.1 Introduction

The USDI Water Measurement Manual (1) 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.

18.2.2 Site Selection

It is the field investigator's responsibility to ensure that the wastewater flow measurement 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 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.
EISOPQAM 18 - 2 November 2001

18.2.3 Flow 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 heart of a typical continuous flow measurement 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

wastewater through it. Examples of such devices include weirs and flumes which relate water depth (head)

to flow, Venturi and orifice type meters relate the differential pressure to flow, and magnetic flow meters

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

measurement 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 generally converted using mechanical, electro mechanical, or electronic

systems into units of flow which are recorded directly on a chart or transmitted into a data system. Systems

which utilize a recorder are generally equipped with a flow totalizer which displays the total flow on a real

time basis.

Studies that need continuous flow measurements require a complete system. Instantaneous flow

measurements do not necessarily dictate the use of any portion of such a system. Techniques which are

described later in 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

primary flow device is utilized for making instantaneous measurements, only the installation of a portable

field sensor and recorder is necessary. If, on the other hand, the facility being investigated does not utilize

a primary flow device, and a continuous flow record is desired, a portable primary flow device will have to

be installed. Field investigators have open channel equipment available for field use. These devices should

be installed according to the manufacturer’s specifications.

Wastewater flow measurement systems are generally very accurate. Any system that cannot measure

the wastewater flow within +10 percent of the actual flow is considered unacceptable for use in measuring

wastewater flow.

18.2.4 Use of Existing Flow Measurement Systems

The installation of systems to measure wastewater flows can be time consuming, particularly if a

primary device is not available. Therefore, field personnel can use existing facility primary 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 accuracy of existing primary

flow devices and systems.

The field investigator must verify that an existing facility flow measurement system (including

primary flow device) utilized to measure wastewater flows conforms with recognized design and installation

standards, and any deviation from standard conditions shall be 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 measuring device or if the device has been mislocated, the investigator shall attempt to install

a portable primary flow device. 
EISOPQAM 18 - 3 November 2001

If the discharger's flow measurement system is accurate within +10 percent of the actual flow, the

investigator can use the installed system. The accuracy of flow sensors and recorders for open channel flow

devices can be checked by making an instantaneous measurement utilizing the primary flow device and

comparing this against the recorder reading. In addition, EPA flow equipment can be installed to check

facility totalizer readings. The chart recorder should be checked to verify that the time and scale are correct.

If non-standard primary flow devices are being used, data supporting the accuracy and precision of

the methods being employed should be provided by the discharger. Deficiencies should be recorded by the

investigator, and the discharger should be informed that the equipment should be calibrated as soon as

possible.

18.2.5 Specific Techniques

This section outlines and familiarizes the field investigator with the most commonly used methods

for wastewater flow measurements and the primary devices that will be encountered during field studies.

Volumetric and dilution techniques are presented at the beginning of this section since they are applicable

to both open channel and closed conduit flow situations. The remaining methods are grouped under

categories dealing with open channels and closed conduits. The general method of checking individual

primary flow devices is given, where applicable. Several estimation techniques are presented. However, it

should be recognized that flow estimates do not satisfy NPDES permit monitoring requirements unless the

permit specifically states that this is permissible. The following methods are included only to enable the field

investigator to make accurate flow estimates when necessary.

Volumetric 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

of time required to fill 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 they are dumped are all

that is required. An accurate tape to verify vessel dimensions and a stop watch are the only 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 quantity 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, tank, 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.
EISOPQAM 18 - 4 November 2001

Dilution Methods 

Dilution methods for water and wastewater 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. Dilution methods are

described in the EABSOP, Section 14.2.3. (3)

18.2.6 Open Channel Flow Measurements 

Measurement of wastewater flow in 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, or

any closed conduit, such as a pipe, which is not flowing full. The most commonly encountered methods in

measuring open channel wastewater flows are described in this section. Several flow estimation techniques

are also presented.

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 to

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. 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=CLH3/2. Values for the coefficient C are given in

hydraulic handbooks (4,5). Broad crested weirs can only be used to calculate instantaneous flows.

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 in the USDI Water Measurement Manual (1), and provide a uniform influent flow

distribution, and that the weir is placed squarely 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 study

should be noted in the field records or log book.

A set of weir tables is necessary for calculating flows. The USDI Water Measurement Manual (1),

the Stevens Water Resource Data Book (6), and the ISCO Open Channel Flow Measurement Handbook (7)

contain a complete set of tables.

Flumes

Conditions that must be met in a flume are similar to those that occur at a weir or spillway crest since

water passing through the throat 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 pri-
EISOPQAM 18 - 5 November 2001

mary flow device when constructed and installed as outlined in the USDI Water Measurement Manual (1).

A complete discussion of other types of flumes is given in references 8, 9, 10, and 11.

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 framing

square, and a measuring tape. The flume should be closely examined to determine if it is discharging freely.

If there is any question about free discharge, the downstream head (Hb) should be measured and compared

to the head at the proper location (Ha) in the converging section. A staff gage is useful for making head

measurements. Any problems observed during the inspection or study should be noted in the field log book.

A set of flume tables is necessary for calculating flows. The USDI Water Measurement Manual (1),

the Stevens Water Resources Data Book (6), and the ISCO Open Channel Flow Measurement Handbook (7)

contain a complete set 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 that are

not within the usable measurement range.

Open Flow 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 better than + 5 percent of the indicated flow (9). A volumetric flow measurement may be used to check

accuracy of this device if flow volumes are not excessive.

Velocity-Area Method

The basic principal of this method is that the flow in a channel (cubic feet/second) is equal to the

average velocity (feet/second) times the cross sectional area (square feet) of the channel. The velocity of the

water or wastewater is determined with a current meter. The area of the channel is either measured or

calculated using an approximation technique. Refer to Section 18.3 for Surface Water Flow Measurements.

18.2.7 Closed Conduit Flow Measurements

The accuracy of closed conduit flow measuring devices may be difficult to verify. Occasionally, it

may be necessary to verify accuracy by making an independent flow measurement, preferably using a

dilution technique (EABSOP, Section 14.2.3) (3). Below are some of the more commonly used closed

conduit devices. 

Venturi Meter

The Venturi meter employs a conversion 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 (9, 10, 11and

12).

Orifice Meter

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 (9).
EISOPQAM 18 - 6 November 2001

Flow Nozzle

The basic principle of operation is the same as that of the Venturi meter. The flow nozzle has an

entrance section and a throat, but lacks the diverging section of the Venturi meter. Flow nozzle accuracies

can approach those of Venturi meters (9).

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 (9).

Other Closed Conduct Devices

References for other closed conduit flow measurement methods such as acoustic flow meters,

trajectory methods, pump curves, and water meters can be found in the NPDES Compliance Inspection

Manual (2).

18.3 Surface Water Flow Measurements

18.3.1 Introduction

Surface waters are considered to be open channels for flow measurement purposes. Where

installation of a primary flow device is practical, open channel flow measurement shall adhere to Section

18.2.6. Where installation of a primary flow device is not practical, flow measurements shall be made using

stream gaging techniques. 

 Where practical, flow data and/or rating curves shall be obtained from existing permanent stream

gaging stations maintained by the USGS, Army Corps of Engineers, or other federal or state agency. Where

permanent stations do not exist, flow may be measured using stream gaging techniques. In making stream

gaging measurements, Branch personnel shall utilize the procedures outlined in the USGS publication

Discharge Measurements at Gaging Stations (8) (1) select the flow measurement site, (2) perform stream

gaging, and (3) calculate flow. The EABSOP Section 14.2.6 (3) also describes current measurement

techniques. If a station is to be used more than one time during a water quality survey, a rating curve may

be developed for that station. A rating curve is constructed by making a series of independent flow

measurements and simultaneous tape down or staff gage measurements for the same section of a particular

station at different water levels and plotting the resulting data pairs on a semi-log graph. At least two

(preferably three) flow measurement-tape downs shall be made to develop a rating curve.

Available current meters for conducting stream gaging include vertical-axis mounted Price AA and

Price pygmy meters. For wadeable streams, these meters may be deployed using a top-setting wading rod.

For non-wadeable streams, a Price AA meter may be deployed on a weighted line using a bridge rig system.

Depth may be determined using Raytheon or Lowrance fathometers, taken from a standard top setting wading

rod, or by taking the difference of tape down measurements of the river bottom and surface. Width

measurements may be made using a Lee-Au galvanized steel tag line segmented into equal lengths, steel

tapes, or cloth tapes. 
EISOPQAM 18 - 7 November 2001

18.4 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 Gaging Stations (8), the EPA NPDES Compliance Inspection Manual (2) and a set of weir and flume

tables shall be supplied to all field investigators. However, the measurements of wastewater 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.

Wastewater flow shall be expressed in million gallons per day (mgd) or the metric equivalent

(m3

/day). Stream flow shall be expressed in cubic feet per second (second feet) or the metric equivalent

(m3

/sec). Time records associated with flow measurements shall be kept in local time, shall be made in the

2400 hour military time format, and shall be recorded to the nearest five minutes.

All flow measurements conducted shall be documented in field records. All measurements shall be

traceable both to the individual making the measurements and the equipment utilized. All field equipment

shall be operated, calibrated, and maintained according to manufacturer’s specifications. All

equipment shall be visually inspected prior to deployment to ensure proper operation. 

18.5 Equipment

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 instrumentation.

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).

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 memory

current meters. Sounding (determination of depth) is accomplished using recording fathometers or with a

standard top setting wading rod. Width measurements are made using a 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 primary devices

available for installation: V-notch weir plates and rectangular weir plates. The corresponding conversion

of water level to flow rate can be accomplished instantaneously from stage/staff gage readings corresponding

to 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 meters. 
EISOPQAM 18 - 8 November 2001

18.6 REFERENCES

1. Water Measurement Manual, Second Edition, Revised, United States Department of Interior, Bureau

of Reclamation, 1981. Available from the United States Government Printing Office, D.C. 20402.

2. NPDES Compliance Inspection Manual, United States Environmental Protection Agency,

September, 1984.

3. US EPA, Region 4, Ecological Assessment Branch Standard Operating Procedures (EABSOP),

2001.

4. King, H. W., and E. F. Brater, Handbook of Hydraulics, Sixth Edition, McGraw-Hill; New York,

1976.

5. Davis, C. V., and K. E. Sorenson, Handbook of Applied Hydraulics, Third Edition, McGraw-Hill:

New York, 1969.

6. Stevens Water Resource Data Book, Third Edition, Leopold Stevens, Inc.: Beaverton, Oregon, 1978.

7. ISCO Open Channel Flow Measurement Handbook, Second Edition, Second Printing,

Instrumentation Specialists Company: Lincoln, Nebraska, 1985.

8. "Discharge Measurements at Gaging Stations," Hydraulic Measurement and Computation, Book I,

Chapter 11, United States Department of Interior, Geological Survey, 1965.

9. "Sewer Flow Measurement: A State-of-the-Art Assessment," Municipal Environmental Research

Laboratory, Office of Research and Development, U. S. Environmental Protection Agency:

Cincinnati, Ohio, 600-275027.

10. A Guide to Methods and Standards for the Measurement of Water Flow, United States Department

of Commerce, National Bureau of Standards, NBS Special Publication 421, 1975.

11. Wells, E. A. and H. B. Gotaas, "Design of Venturi Flumes in Circular Conduits," American Society

of Civil Engineers, 82, Proc. Paper 928, April 1956.

12. American Society of Testing Materials, 1985 Annual Book of ASTM Standards, Volume 11 - Water,

American Society of Testing Materials: Philadelphia, Pennsylvania, 1985.
EISOPQAM 19 - 1 November 2001

SECTION 19

SOIL GAS SAMPLING

PERFORMANCE OBJECTIVE:

  To present the standard operating procedures and sample collection methodologies for 

 conducting soil gas sampling.

19.1 Introduction

This section discusses the sample collection procedures used for conducting soil gas sampling in

Region 4. These procedures include both manual implantation of passive devices (GORE-SORBER®

Modules) as well as direct push (Geoprobe®) installations for both grab sampling and long term, permanent

installations.

19.1.1 GORE-SORBER® Implants

Soil gas screening surveys may be conducted with GORE-SORBER Modules (patented passive

soil vapor sampling devices). Organic compounds commonly detected using GORE-SORBER® Modules

include fluorinated and chlorinated solvents, straight- and branched chain aliphatics, aromatics, and

polycyclic aromatic hydrocarbons (PAHs). Many of these compounds are associated with a wide range of

petroleum products, including gasoline, mineral spirits, heating oils, creosotes, and coal tars. GORESORBER® Screening Surveys have also been used successfully to screen for nitroaromatic explosives.

Description Of GORE-SORBER® Screening Modules

A typical GORE-SORBER® Screening Module consists of several separate GORE-SORBER®

passive sorbent collection devices (sorbers). A typical sorber is 15 to 25 millimeters (mm) long, with a 3

mm inside diameter (ID), and contains 40 milligrams (mg) of a suitable granular adsorbent material

depending on the specific compounds to be detected. Typically, polymeric and carbonaceous resins are used

for their affinity for a broad range of VOCs and SVOCs. The sorbers are sheathed in the bottom of a one

(1) foot length of vapor-permeable insertion and retrieval cord which is fashioned with a loop. This

construction is termed a GORE-SORBER® module. Both the retrieval cord and sorbent container are

constructed solely of inert, hydrophobic, microporous GORE-TEX® expanded polytetrafluoroethylene

(ePTFE, similar to Teflon® brand PTFE). The loop is used as a means of tying the module to a string for

installation and retrieval.

Module Installation

1. Drive/drill narrow pilot hole at desired location. Ideally, this hole should be no more than

1 inch in diameter. Typical depth is two to three feet below ground surface.

2. Wearing clean latex gloves, remove the module from it’s numbered container and re-seal

the jar, verifying that the number on the container corresponds to the number on the module

tag.
EISOPQAM 19 - 2 November 2001

3. Measure and cut a section of cord of sufficient length to reach from the bottom of the

sample hole to the cork to be used to seal the hole.

4. Tie one end of the cord to the loop in the module, and tie the other end of the cord to a

screw-eye in the cork used for sealing the hole.

 

5. Place insertion rod into the pre-cut pocket at the base of the module and lower it into the

hole. If you encounter resistance remove the module and enlarge the hole and re-insert the

module.

6. Once deployed to the desired depth, press the insertion rod against the side of the hole and

twist slightly to release the module. Remove the rod and push any excess cord into the pilot

hole and plug it with the cork.

7. Indicate the module number, date and time of installation and any pertinent comments on

the installation/retrieval log and in the investigation field book. Write the module serial

number on the site map adjacent to the appropriate map location.

Module Retrieval

1. Following the module exposure period (usually 10-14 days) identify and check each module

location in the field using the site map.

2. Remove the cork with a penknife or cork screw. Grasp the cord and pull the module from

the ground; verify the module ID number. Cut off and discard the cork and cord. Place

the entire module in its labeled container and tightly secure the lid.

3. Replace the sample container in the box. Where possible, please attempt to keep modules

in numbered sequence to expedite sample check-in and processing.

4. Complete the module retrieval date/time on the installation/retrieval log.

5. Do not use Styrofoam “peanuts” as packing material. Bubble packing is acceptable. When

packing for shipment, take extra precautions to keep boxes dry.

6. Return the samples with insertion rod and paperwork (preferrably by overnight courier) to:

Screening Modules Laboratory

W.L. Gore & Associates, Inc.

100 Chesapeake Blvd.

Elkton, MD 21921

Phone: (410) 392-7600

Attn: NOTIFY LAB IMMEDIATELY UPON DELIVERY!!

IMPORTANT: Samples should not be shipped for weekend or holiday delivery at GORE.
EISOPQAM 19 - 3 November 2001

19.1.2 Geoprobe® Grab Sampling using the PRT System

Single event or grab sampling may be conducted using the Post-Run Tubing System (PRT). This

system allows EIB personnel to collect soil gas samples quickly and with a high degree of assurance that the

samples are representative of the targeted depth, i.e., using this method, there is no leakage at probe rod joints

that will compromise the integrity of the sample.

The downhole components of the PRT system include:

• Sample delivery tubing

• Probe rods

• PRT Adapter

• Expendable point holder

• Expendable point

O-ring seals are used on the PRT Adapter and the expendable point holder to provide a leak-proof

system that assures sample integrity.

PRT System Installation Procedures

The following procedures are used to collect soil gas samples using the Geoprobe® PRT system.

The PRT system can be used with either the 1.0-inch or 1.25-inch diameter probe rod. All parts or

accessories used in the PRT system must be selected with the appropriate diameter probe rod in mind to

ensure compatibility of all components.

1) Place O-ring on PRT expendable point holder and attach to initial section of probe rod.

2) Place O-ring on expendable point and press into expendable point holder. 

3) Add drive cap to probe rod and push PRT system into ground. Add additional probe rods, as needed,

to push system to the desired sampling depth.

4) At the desired sampling depth, attach pull cap to probe rod and pull the rod back to disengage the

expendable point and expose the soil interval for sampling. Remove the pull cap when this step is

completed.

5) Secure the PRT adapter to a length of tubing sufficient to reach from the sampling interval to the

surface, with several feet of excess tubing extending beyond the top of the probe rod to facilitate

sampling. The adapter is secured tightly to the tubing using electrical tape. This will not

compromise the integrity of the sample to be collected, as the sample is pulled directly through the

adapter and is never exposed to the tape.

6) Run the tubing and adapter into the probe rod and, using steady downward pressure, turn the tubing

counter-clockwise to dock the adapter into the top of the expendable point holder. Tug gently on

the tubing to ensure that the adapter docked firmly into the expendable point holder. Failure to dock

could indicate that soil intruded during the push or that the expendable point was lost during the

push. 
EISOPQAM 19 - 4 November 2001

7) At this point, the PRT system has been installed and is ready for sampling. If the sample can not be

collected immediately, the end of the tubing should be capped. 

PRT System Sampling Methodology

Soil gas samples may be collected from the installed PRT system using several methods. These are

listed below:

• Cannister Sampling - After purging the PRT system tubing to introduce representative soil gas into

the system, an evacuated SUMMA® cannister is attached using a Swagelok® or other suitable

secure connection. After connection, the valve on the SUMMA® cannister is opened, pulling soil

gas from the exposed soil interval into the cannister. 

• Continuous Sampling - Continuous sampling may be conducted using appropriate analytical

instrumentation. 

Special Considerations for Sampling

The tubing used to complete the PRT system should be Teflon®. As most soil gas sampling will be

conducted to investigate the presence or extent of organic compounds, Teflon® tubing is required to ensure

the integrity of the sample.

19.1.3 Geoprobe® Permanent Soil Gas Implants

Long-term soil gas sampling may be conducted using permanent soil gas sampling implants installed

with the Geoprobe®. Stainless steel implants may be installed at any depth achievable by the Geoprobe®

and may be installed in 1.0-inch and 1.25-inch diameter probe rod in custom lengths, using 6-inch (152 mm)

or 21-inch (533 mm) screens, which can be connected in any combination. The screens are double-woven

stainless steel mesh with 0.0057-inch (0.15 mm) pore openings. A 14-inch long screen is available for use

only with the 1.25-inch diameter probe rod.

The following procedures are used by EIB to install a permanent soil gas sampling implant using the

Geoprobe®. These are general procedures which are used with either 1.0-inch or 1.25-inch diameter probe

rod. Attention should be given to rod diameter when ordering points and point holders.

Installation of Permanent Soil Gas Sampling Implants

1) Attach O-ring to implant point anchor.

2) Press implant point anchor into point holder and attach to first section of probe rod.

3) Push implant point anchor to the desired depth for implant installation.

4) When the desired depth has been reached, attach the implant to the sample delivery tubing. This is

accomplished by loosening or removing the Swagelok® fitting and pressing the tubing into the

implant. When the end of the tubing is sufficiently engaged in the end of the implant, the

Swagelok® fitting is tightened to secure the tubing in the implant. It is critical that the tubing be

securely attached to the implant so that it does not pull off during subsequent steps of the

installation.
EISOPQAM 19 - 5 November 2001

5) Feed the tubing into the probe rod until the implant reaches the implant point anchor. At this point,

cut the tubing to allow enough tubing to remain for sampling, usually three to four feet.

6) Rotate the tubing and implant counter-clockwise, threading the implant into the anchor. If there was

any soil intrusion during the push, the implant may not dock. If the implant does not dock, it is

possible to salvage the installation by removing the implant and sealing the small hole on the bottom

of the implant with foil or with a small sheet metal screw then returning the implant to the hole.

7) After the implant has been docked, use a pull cap and pull the probe rod approximately one foot,

exposing the implant. Observe the tubing to make sure that anchor remained in place and is not

being pulled with the rod.

8) If the implant remained in place, slowly pour a measured amount of 60-100 mesh glass beads down

the inside of the probe rod. The glass beads are used as a filter pack around the implant. Ideally,

the implant should be covered with beads with approximately six inches of beads above the top of

the implant. The volume of beads should be calculated based on the length of implant used. While

pouring the beads, it is advisable to gently shake the tubing to prevent the beads from bridging inside

the probe rod.

9) After placing the beads, the implant is sealed using a flowable mixture of the glass beads and finepowdered bentonite. To accomplish this, two to three feet of rod is pulled and the mixture is slowly

poured into the rod above the bead-packed implant. As with the bead placement, similar care should

be taken to avoid bridging of this mixture.

10) If it is appropriate to grout the installation, grouting may be accomplished either through pressure

grouting through the probe rod as the rods are pulled after placement of the seal or, if the hole

remains open, the grout may be mixed and poured down the open hole after retrieval of the rods.

11) For permanent or long-term installations, efforts should be taken to protect the tubing at the surface

using some type of surface completion and protective casing.

Permanent Soil Gas Sampling Methodology

Soil gas samples may be collected from the installed permanent soil gas implant using several

methods. These are listed below:

• Cannister Sampling - After purging implant tubing to introduce representative soil gas into the

system, an evacuated SUMMA® cannister is attached using a Swagelok® or other suitable secure

connection. After connection, the valve on the SUMMA® cannister is opened, pulling soil gas from

the implant into the cannister.

• Continuous Sampling - Continuous sampling may be conducted using appropriate analytical

instrumentation. 

Special Considerations for Sampling

The tubing used for the permanent soil gas implant should be Teflon®. As most soil gas sampling

will be conducted to investigate the presence or extent of organic compounds, Teflon® tubing is required

to ensure the integrity of the sample.
EISOPQAM 19 - 6 November 2001

19.2 References 

1. Description of Service for Soil Gas Applications, W.L. Gore & Associates, Inc., Elkton, MD.

2. GORE-SORBER® Screening Survey Module Storage, Installation, and Retrieval Information, W.L.

Gore & Associates, Inc., Elkton, MD. 

3. Geoprobe Systems Tools and Equipment Catalog, Kejr Engineering, Inc., Salinas, Kansas, 1997.

4. The Yellow Field Book, Kejr Engineering, Inc., Salinas, Kansas, 2000.
EISOPQAM A-1 November 2001

APPENDIX A

RECOMMENDED VOLUMES, CONTAINER TYPES, PRESERVATION and HOLDING TIMES

The following tables summarize the amount of sample required, typical containers, preservative (if any)

and holding times for many analyses, by media. 

Soil and Sediment - Organic Compounds

Analysis Amt.1 Container

Type2

Preservative3 Holding

Time4

Dioxin/Dibenzofurans 8 oz. G ice 30

Extractable Organic Compounds/pesticides/

PCBs

8 oz. G ice 14

Extractable Organic Compounds - TCLP 8 oz. G ice 14

Organic Halide 8 oz. G ice 28

VOC  200 ug\kg (water suspension) 120 ml. G/S ice 48 Hours

VOC  200 ug\kg 15 g. E ice 48 Hours

VOC  200 ug\kg (water suspension) 120 ml. G/S NaHSO4 (pH<2), ice 14

VOC 200 ug\kg 120 ml. G/S CH3OH, ice 14

VOC 200 ug\kg 15 g. E ice 48 Hours

VOC 200 ug\kg 2 oz. G/S ice 48 Hours

VOC - TCLP Analysis 2 oz. G ice 14
EISOPQAM A-2 November 2001

Soil and Sediment - Inorganic Compounds

Analysis Amt.1 Container

Type2

Preservative3 Holding

Time4

Chloride 8 oz. G NA NS

Chromium - hexavalent 8 oz. G ice 30

Cyanide 8 oz. G ice NS

COD 8 oz. G ice NS

Fluoride 8 oz. G NA NS

Grain size 8 oz. G NA NS

Mercury 8 oz. G ice 28

Mercury - TCLP 8 oz. G NA 28

Metals 8 oz. G ice 180

Metals - TCLP 8 oz. G NA 180

Metals - EP 8 oz. G NA 180

Nitrate 8 oz. G ice NS

Nitrite 8 oz. G ice NS

Nutrients (ammonia, TKN, NO2, NO3, N,

total phosphate)

8 oz. G ice NS

pH 8 oz. G NA NS

Sulfates 8 oz. G NA NS

Sulfides 8 oz. G ice NS

TOC 8 oz. G ice NS
EISOPQAM A-3 November 2001

Water and Waste Water - Biological

Analysis Amt.1 Container

Type2

Preservative3 Holding

Time4

Bacteriological 150 ml. P, G, W ice 6 Hours

Toxicity, acute 1 gal. C ice 36 Hours

Toxicity, chronic 1 gal. C ice 36 Hours

Water and Waste Water - Organic Compounds

Analysis Amt.1 Container

Type2

Preservative3 Holding

Time4

Alcohol - Percent 1gal. G/A ice NS

Dioxin/Dibenzofurans 2 L. L/A ice (0- 4 C.) 365

Dioxin/Dibenzofurans - residual chlorine 2 L. L/A ice (0- 4 C.) 80 mg.

sodium thiosulfate /L.

365

Methane/Ethane/Ethene 120 ml. G/S HCl (pH<2), ice 14

Extractable Organic Compounds/ pesticides/

PCBs

1 gal. G/A ice 7

Extractable Organic Compounds/

pesticides/PCBs - residual chlorine present

1 gal. G/A 3 ml. of 10% sodium

thiosulfate per gallon

7

Extractable Organic Compounds - TCLP 1 gal. G/A ice 14

Organic Halide 1 L. G/A H2SO4 (pH<2), ice 28

Phenols 1 L. G/A H2SO4 (pH<2), ice 28

Volatile Organic Compounds 120 ml. G/S ice 7

Volatile Organic Compounds 120 ml. G/S HCl (pH<2), ice 14

Volatile Organic Compounds 120 ml. G/S NaHSO4 (pH<2), ice 14

Volatile Organic Compounds - residual

chlorine present

120 ml. G/S HCl (pH<2), ice5 14

Volatile Organic compounds - TCLP 120 ml. G/S ice 14
EISOPQAM A-4 November 2001

Water and Waste Water - Inorganic Compounds

Analysis Amt.1 Container

Type2

Preservative3 Holding

Time4

Ammonia 1 L. P H2SO4 (pH<2), ice 28

Alkalinity 1 L. P ice 14

BOD5 2 L. P ice 2

Bromide 1 L. P ice 28

Chlorine - Residual 500 ml. P NA ASAP

Chloride 1 L. P NA 28

Chromium - hexavalent 1 L. P ice 24 Hours

COD 1 L. P H2SO4 (pH<2), ice 28

Color 1 gal. G/A ice 2

Conductivity 500 ml. P ice 28

Cyanide 1 L. P NaOH (pH>12) 14

Cyanide - Residual chlorine 1 L. P see footnote 6 14

DOC 1 L. P H2SO4 (pH<2), ice 28

Fluoride 1 L. P NA 28

Hardness 1 L. P HNO3 (pH<2) 180

Iron (Fe 2+) 1 L. P NA ASAP

Mercury 1 L. P HNO3 (pH<2) 28

Mercury - TCLP 1 L. P NA 28

Metals 1 L. P HNO3 (pH<2) 180

Metals - TCLP 1 L. P NA 180

Metals - EP 1 L. P NA 180

Nitrate 2 L. P ice 2

Nitrite 1 L. P ice 2

Nutrients (Ammonia, TKN, NO2, NO3, -N,

total phosphorus)

2 L. P H2SO4 (pH<2), ice 28
EISOPQAM A-5 November 2001

Water and Waste Water - Inorganic Compounds (continued)

Analysis Amt.1 Container

Type2

Preservative3 Holding

Time4

Oil and Grease 1 L. P H2SO4 (pH<2), ice 28

Oxygen - dissolved 40 ml. G NA ASAP

pH 500 ml. P NA ASAP

Phenols 1 L. P H2SO4 (pH<2), ice 28

Phosphate - ortho 1 L. P ice 2

Phosphate - dissolved 1 L. P H2SO4 (pH<2), ice 28

Solids Series 2 L. P ice 7

Solids - Settleable 2 L. P ice 2

Sulfates 1 L. P ice 28

Sulfides 1 L. P 2 ml zinc acetate,

NaOH (pH>9), ice

7

Temperature 500 ml. P none ASAP

TOC 1 L. P H2SO4 (pH<2), ice NS

Turbidity 500 ml. P ice 2
EISOPQAM A-6 November 2001

Waste - Organic Compounds

Analysis Amt.1 Container

Type2

Preservative3 Holding

Time4

Alcohol - Percent 8 oz. G NA NS

Dioxin/Dibenzofurans 8 oz. G ice 75

Extractable Organic Compounds/pesticides/

PCBs

8 oz. G NA 14

Extractable Organic Compounds - TCLP 8 oz. G NA 14

VOC  200 ug\kg 2 oz. G ice 48 hours

VOC  200 ug\kg 15 g. E ice 48 hours

VOC 200 ug\kg 8 oz. G NA 48 hours

Volatile Organic compounds - TCLP 8 oz. G NA 28

Waste - Inorganic Compounds

Analysis Amt.1 Container

Type2

Preservative3 Holding

Time4

Ash Content 8 oz. G NA NS

BTU Content 8 oz. G NA NS

Chromium - hexavalent 8 oz. G NA NS

Cyanide 8 oz. G NA NS

Dermal Corrosion 8 oz. G NA NS

Flashpoint 8 oz. G NA NS

Mercury 8 oz. G NA 180

Mercury - TCLP 8 oz. G NA NS

Metals 8 oz. G NA 28

Metals - TCLP 8 oz. G NA NS

Metals - EP 8 oz. G NA 28

pH 8 oz. G NA NS

Sulfides 8 oz. G NA NS
EISOPQAM A-7 November 2001

Footnotes:

1. Amount - The amounts listed must be considered approximate requirements that are appropriate for most

media. If a particular media to be sampled is very light, more sample may be required to obtain

the necessary mass for the analysis.

2. Container Type:

G = Glass

P = Polyethylene

E = EncoreTM

C = Cubitainer

S = Septum Seal

A = Amber

W = Whirl-PakTM

3. ice: Sufficient ice must be placed in the shipping/transport container to ensure that ice is still

present when the samples are received at the laboratory

NaHSO4: The proper amount of NaHSO4 (Sodium Bisulfate) is added to the sample container at

the laboratory prior to sampling.

CH3OH: The proper amount of CH3OH (Methanol) is added to the sample container at the

laboratory prior to sampling.

HCl: HCl (Hydrochloric Acid) used as a preservative must be present at concentrations of

0.04% or less by weight (pH about 1.96 or greater), as specified in 40 CFR 136.3, Table

II, footnote 3. The proper amount of HCl is added to the sample container at the

laboratory prior to sampling.

H2SO4: H2SO4 (Sulfuric Acid) used as a preservative must be present at concentrations of 0.35%

or less by weight (pH about 1.15 or greater), as specified in 40 CFR 136.3, Table II,

footnote 3. Approximately 5 ml. of the laboratory prepared preservative is added to the

sample.

NaOH: NaOH (Sodium Hydroxide) used as a preservative must be present at concentrations of

0.080% or less by weight (pH about 12.30 or less), as specified in 40 CFR 136.3, Table

II, footnote 3. Four tablets are added to the sample after collection.

HNO3: HNO3 (Nitric Acid) used as a preservative must be present at concentrations of 0.15% or

less by weight (pH about 1.62 or greater), as specified in 40 CFR 136.3, Table II,

footnote 3. Approximately 5 ml. of the laboratory prepared preservative is added to the

sample.

NA: Not Applicable. No sample preservation is required

4. Holding Time - Holding time is stated in days unless marked otherwise. A holding time of ASAP

indicates the sample is to be analyzed within 15 minutes. A holding time of NS indicates

that no holding time is specified in the analytical method.
EISOPQAM A-8 November 2001

5. Collect sample in 8 oz. glass container containing ascorbic acid solution prepared by the laboratory.

Gently mix sample and transfer to sample containers prepared by the laboratory with the proper amount

of HCl. 

6. Use ascorbic acid only if the sample contains residual chlorine. To test for residual chlorine, place a

drop of sample on potassium iodide-starch test paper. If the test paper turns blue, residual chlorine is

present. Add a few crystals of ascorbic acid and re-test until the test paper no longer turns blue. Add an

additional 0.6 gram of ascorbic acid for each liter of sample.
EISOPQAM B - 1 November 2001

APPENDIX B

STANDARD FIELD CLEANING PROCEDURES

 PERFORMANCE OBJECTIVE:

 To remove contaminants of concern from sampling, drilling and other field equipment to

concentrations that do not impact study objectives using a standard cleaning procedure.

B.1 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. 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 in 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.

 Analyte free water (deionized 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 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. Analyte free water obtained by other methods is acceptable, as long as it meets the above

analytical criteria.
EISOPQAM B - 2 November 2001

 Organic/analyte free water is defined as tap water that has been treated with activated carbon and

deionizing units. A portable system to produce organic/analyte free water under field conditions

is available. At a minimum, the finished water 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 as determined by the Region

4 laboratory for a given set of analyses. Organic/analyte free water obtained by 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 during

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 in clean plastic, metal, or glass containers until used. It should be poured

directly from the container during use.

 Solvent must be stored in the unopened original containers until used. They may be applied using

the low pressure nitrogen system fitted with a Teflon® nozzle, or using Teflon® squeeze bottles.

 Tap water may be kept in clean tanks, hand pressure sprayers, squeeze bottles, or applied directly

from a hose.

 Analyte 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/analyte free water must be stored in clean glass, Teflon®, or stainless steel containers

prior to use. It may be applied using Teflon® squeeze bottles, or with the portable system.

Note: Hand pump sprayers generally are not acceptable storage or application containers for the

above materials (with the exception of tap water). This also applies to stainless steel

sprayers. All hand sprayers have internal oil coated gaskets and black rubber seals that may

contaminate the solutions.

B.1.3 Disposal of Solvent Cleaning Solutions

Procedures for the safe handling and disposition of investigation derived waste (IDW), including

used wash water, rinse water, and spent solvents are in 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

from the study. At a minimum, this should consist of washing with soap and rinsing with tap water. More

stringent procedures may be required at the discretion of the field investigators.
EISOPQAM B - 3 November 2001

B.1.5 Safety Procedures for Field Cleaning Operations

Some of the materials used to implement the cleaning procedures outlined in this appendix can be

harmful if used improperly. Caution should be exercised by all field investigators and all applicable safety

procedures should be followed. At 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 recontamination. If the equipment is not to be immediately re-used it should be covered with

plastic sheeting or wrapped in aluminum foil to prevent re-contamination. The area where the equipment

is kept prior to 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 entire study can be conducted

without the need for field cleaning. However, this is not possible for some specialized items such as portable

power augers (Little Beaver®), well drilling rigs, soil coring rigs, and other large pieces of field equipment.

In addition, particularly during large scale studies, it is not practical or possible to transport all of the

precleaned field equipment required into the field. In these instances, sufficient pre-cleaned equipment

should be transported to the field to perform at least one days work. The following procedures are to be

utilized when equipment must be cleaned in the field.

B.2.1 Specifications for Decontamination Pads

Decontamination pads constructed for field cleaning of sampling and drilling equipment should meet

the following minimum specifications:

 The pad should be constructed in an area known or believed to be free of surface contamination.

 The pad should not leak excessively.

 If possible, the pad should be constructed on a level, paved surface and should facilitate the

removal of wastewater. This may be accomplished by either constructing the pad with one corner

lower than the rest, or by creating a sump or pit in one corner or along one side. Any sump or pit

should also be lined. 

 Sawhorses or racks constructed to hold equipment while being cleaned should be high enough

above ground to prevent equipment from being splashed.

 Water should be removed from the decontamination pad frequently.
EISOPQAM B - 4 November 2001

 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.

At the completion of site activities, the decontamination pad should be deactivated. The pit or sump

should be backfilled with the appropriate material designated by the site project leader, but only after all

waste/rinse water has been pumped into containers for disposal. No solvent rinsates will be placed in the

pit. Solvent rinsates 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 Kemmerers, 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 unavailable the samplers should be flushed at the

next sampling location with the substance (water) to be sampled, 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 previously 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 to be used for all sampling equipment used to collect routine samples

undergoing trace organic or inorganic constituent analyses:

1. Clean with tap water and soap using a brush if necessary to remove particulate matter and surface

films. Equipment may 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 saw horses at

least two feet above the floor of the decontamination pad. PVC or plastic items should not be

steam cleaned.

2. Rinse thoroughly with tap water.

3. Rinse thoroughly with analyte free water.

4. Rinse thoroughly with solvent. Do not solvent rinse PVC or plastic items.

5. Rinse thoroughly with organic/analyte free water. If organic/analyte free water is not available,

equipment should be allowed to completely dry. Do not apply a final rinse with analyte water.

Organic/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.
EISOPQAM B - 5 November 2001

B.2.4 Well Sounders or Tapes

1. Wash with soap and tap water.

2. Rinse with tap water.

3. Rinse with analyte free water.

B.2.5 Goulds® Pump Cleaning Procedure

CAUTION - During cleaning always disconnect the pump from the generator.

The Goulds© 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.

B.2.6 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.

1. 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-attach the ball check valve to the Redi-Flo2® pump head.
EISOPQAM B - 6 November 2001

B.2.7 Automatic Sampler Tubing

The Silastic® and Tygon® tubing previously used in the automatic samplers may be field cleaned

as follows:

1. Flush tubing with tap water and soap.

2. Rinse tubing thoroughly with tap water.

3. Rinse tubing with analyte free water.

B.3 Downhole Drilling Equipment

These procedures are to be used for drilling activities involving the collection of soil samples for

trace organic and inorganic constituent analyses, and for the construction of monitoring wells to be used for

the collection of groundwater samples for trace organic and inorganic constituent analyses.

B.3.1 Introduction

Cleaning and decontamination of all equipment should occur at a designated area (decontamination

pad) on the site. The decontamination pad should meet the specifications of Section B.2.1.

Tap water (potable) brought on the site for drilling and cleaning purposes should be contained in a

pre-cleaned tank.

A steam cleaner and/or high pressure hot water washer capable of generating a pressure of at least

2500 PSI and producing hot water and/or steam (200F plus), with a soap compartment, 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

not serve as a source of contaminants. In addition, associated drilling and decontamination equipment, well

construction materials, and equipment handling procedures should meet these minimum specified criteria:

 All downhole augering, drilling, and sampling equipment should be sandblasted before use if

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 hot water), or wire brushing. Sandblasting should be

performed prior to arrival on site, or well away from the decontamination pad and areas to be

sampled.

 Any portion of the drill rig, backhoe, etc., that is over the borehole (kelly 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 may have come from other hazardous waste sites before being brought

on site.

 Printing and/or writing on well casing, tremie tubing, etc., should be removed before use. Emery

cloth or sand paper can be used to remove the printing and/or writing. Most well material

suppliers can supply materials without the printing and/or writing if specified when ordered.
EISOPQAM B - 7 November 2001

 The drill rig 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 tubes should be inspected. Items that cannot be cleaned

are not acceptable and should be discarded.

B.3.3 Drill Rig Field Cleaning Procedure

Any portion of the drill rig, backhoe, etc., that is over the borehole (kelly bar or mast, backhoe

buckets, drilling platform, hoist or chain pulldowns, spindles, cathead, etc.) should be steam cleaned (soap

and high pressure hot water) between boreholes.

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 to 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 particulate 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. 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

New one-pint or one-quart mason jars may be used to collect samples for analyses of organic

compounds 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 compound analyses.

The rubber sealing ring should not be in contact with the jar and aluminum foil should be used, if

possible, between the jar and the sealing ring. If possible, the jar and aluminum foil should be rinsed with

pesticide-grade isopropanol and allowed to air dry before use. Several empty bottles and lids should be

submitted to the laboratory as blanks for quality control purposes.
EISOPQAM C - 1 November 2001

APPENDIX C

FIELD EQUIPMENT CENTER STANDARD CLEANING PROCEDURES

 PERFORMANCE OBJECTIVE:

 To remove contaminants of concern from sampling, drilling and other field equipment to

concentrations that do not impact study objectives using a standard cleaning procedure.

C.1 Introduction

Cleaning procedures outlined in 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 are 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. Deviations from these

procedures should be documented in the approved study plan, field records, and investigative reports.

C.1.1 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 Liquinox®.

 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 (10%) shall be made from reagent-grade nitric acid and deionized water.

 Analyte free water (deionized water) is tap water that has been treated by passing it through a

standard deionizing 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.

 Organic/analyte free water is defined as tap water that has been treated with activated carbon and

deionizing units. At 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. Organic/analyte free water obtained by other methods is

acceptable, as long as it meets the above analytical criteria.
EISOPQAM C - 2 November 2001

 Other solvents may be substituted for a particular investigation if needed. Pesticide-grade

acetone or methanol are acceptable. However, it should be noted that if pesticide-grade acetone

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 materials:

 Soap should be kept in clean containers until use. It should be poured directly from the

container.

 Disinfectant soap should be kept in clean containers until use. It 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.

 Analyte free water should be stored in cleaned containers that can be closed when not being used.

It may be applied from squeeze bottles.

 Organic/analyte free water should be stored in cleaned glass, Teflon®, or stainless steel

containers prior to use. It may be applied using Teflon® squeeze bottles, or directly from the

system.

 Nitric acid should be kept in the glass container it is received in, and placed in squeeze bottles

prior to application.

C.1.3 Disposal of Spent Cleaning Solutions

Procedures for safe handling and disposition of spent cleaning solutions, including washwater, rinse

water, spent acid solutions, and spent solvents are as follows:

Washwater

Since equipment is decontaminated before its return to the FEC, the washwater may be disposed in

the sanitary drain in the washroom. When large equipment (vehicles, augers, etc.) is washed outside, it may

wash onto the ground without recovery of the washwater.
EISOPQAM C - 3 November 2001

Rinsewater

Since equipment is decontaminated before its return to the FEC, the rinsewater may be disposed in

the sanitary drain in the washroom. When large equipment (vehicles, augers, etc.) is rinsed outside, it may

go onto 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 sanitary

drain 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 drain 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 recovery"

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 (e.g., tar removal, etc.)

should be designated for disposal. The two groups should be labeled "For Recovery" or "For Disposal" and

stored separately at the FEC. 

C.1.4 Safety Procedures for Cleaning Operations

Some materials used to implement the cleaning procedures outlined in this Appendix are harmful

if used improperly. Caution should be exercised and all applicable safety procedures shall be followed. At

a minimum, the following precautions shall be taken in the washroom during these cleaning operations:

 Safety glasses with splash shields or goggles, a neoprene apron, and neoprene gloves will be

worn during all cleaning operations. When cleaning heavy items such as hollow-stem augers or

other drill rig equipment, safety boots will be worn.

 All solvent rinsing operations will be conducted under a fume hood or in the open (never in a

closed room).

 No eating, smoking, drinking, chewing, or any hand to mouth contact shall be permitted during

cleaning operations.

C.1.5 Handling and Labeling of Cleaned Equipment

After cleaning, equipment should be handled only by personnel wearing clean latex gloves to prevent

re-contamination.

After the cleaned equipment is wrapped in aluminum foil and sealed in plastic, the date that the

equipment was cleaned should be written on the plastic. If the equipment was not cleaned according to the

procedures outlined in this appendix, this should also be noted on the plastic.
EISOPQAM C - 4 November 2001

C.1.6 Initial Processing of Returned Equipment

Field or sampling equipment that needs to be repaired will be identified with a "repair" tag. Any

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 coolers, plastic wrapped equipment, containers, and tubing not used in the field may be placed

back into 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 Teflon® and Glass

1. Wash equipment thoroughly with soap and hot tap water using a brush or scrub pad to remove

any particulate matter or surface film.

2. Rinse equipment thoroughly with hot tap water.

3. Rinse equipment with 10 percent nitric acid solution. Small and awkward equipment such as

vacuum bottle inserts and well bailer ends may be soaked in the nitric acid solution instead of

being rinsed with it. Fresh nitric acid solution should be prepared for each cleaning session.

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. 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.
EISOPQAM C - 5 November 2001

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 particulate 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. This activity may be conducted in the event of a special, civil or criminal

investigation.

C.3 Automatic Wastewater Sampling Equipment

C.3.1 ISCO© 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 pre-cleaned, Silastic pump tubing (see Appendix C.4.1) will be installed.

C.3.2 ISCO© 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.

3. Replace in sampler.
EISOPQAM C - 6 November 2001

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 Composite Sample Containers

1. Wash containers thoroughly with hot tap water and laboratory detergent, using a bottle brush to

remove particulate 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 thoroughly with tap water.

5. Rinse containers thoroughly with analyte free water.

6. Rinse twice with solvent and allow to air dry for at least 24 hours.

7. Cap with aluminum foil or Teflon® film.

When these containers are used to collect samples that contain oil, grease, or other hard to remove

materials, it may be necessary 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 Composite Sample Containers (2700 - 5 gal., 3700 - 4 gal.)

1. Wash containers thoroughly with hot tap water and laboratory detergent, using a bottle brush to

remove particulate 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 thoroughly with tap water.

5. Rinse containers thoroughly with analyte free water.

6. Cap with aluminum foil or Teflon® film.

Any plastic composite sample containers that have a visible film, scale, or other discoloration

remaining after this cleaning procedure will be discarded.
EISOPQAM C - 7 November 2001

C.3.6 ISCO© 1680, 2700, and 3700 Glass Sequential Bottles for GC/MS Analyses

1. Rinse with 10 percent nitric acid.

2. Rinse thoroughly with tap 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.3.7 Bottle Siphons for Composite Containers

Tubing should be rinsed with solvent and dried in 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 in plastic and labeled. The siphon should be flushed with sample thoroughly before use.

C.3.8 Reusable Teflon® Composite Mixer Rods

1. Wash equipment thoroughly with soap and hot tap water using a brush or scrub pad to remove

any particulate matter or surface film.

2. Rinse equipment thoroughly with hot tap water.

3. Rinse equipment with at least a 10 percent nitric acid solution.

4. Rinse equipment thoroughly with tap water.

5. Rinse equipment thoroughly 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

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 Step 1. 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.4 Cleaning Procedures for Tubing

C.4.1 Silastic® Pump Tubing

The Silastic® pump tubing in the automatic samplers and peristaltic pumps should be replaced after

each study. After installation, the exposed ends should be capped with clean, unused aluminum foil.
EISOPQAM C - 8 November 2001

C.4.2 Teflon® Sample Tubing

Use only new Teflon® tubing which has been pre-cleaned as follows for the collection of samples

for trace organic compound or ICP analyses:

1. Teflon® tubing shall be precut in 10, 15 or 25-foot lengths before cleaning.

2. Rinse outside of tubing with solvent.

3. Flush interior of tubing with solvent.

4. After flushing with solvent, pressurize the tubing to a safe level (one end only) to flush out

solvent. 

5. Dry overnight in the drying oven.

6. Coil. Cap ends with aluminum foil. Wrap tubing in one layer of aluminum foil. Roll edges of

foil into a "tab" to allow for easy removal. Seal the foil wrapped tubing in plastic and label.

C.4.3 Stainless Steel Tubing

1. Wash with soap and hot tap water using a long, narrow, bottle brush.

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. Cap ends with aluminum foil. Wrap tubing in one layer of aluminum foil. Roll edges of foil into

a "tab" to allow for easy removal. 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 necessary to rinse the equipment several times with pesticide-grade acetone,

hexane, or petroleum ether to remove the materials before proceeding with Step 1. If the equipment cannot

be cleaned utilizing these procedures, it should be discarded.

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 tube/pack) to prevent

contamination during storage.
EISOPQAM C - 9 November 2001

C.5 Cleaning Procedures for 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 to air dry overnight.

C.5.2 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.5.3 Redi-Flo2® Pump

CAUTION - Make sure that the controller is not plugged in.

CAUTION - Do not wet the controller.

Controller Box Cleaning:

1. Wipe the controller box with a damp cloth. Immediately remove any excess water.

2. Let the controller box dry completely.

Pump Cleaning:

CAUTION - 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. Place pump in clean water and have it discharge into a bucket or or another area to clean the

inside of the pump, using a soap and water mixture first. Then run tap water or DI water through

the pump and flush out the soap. 
EISOPQAM C - 10 November 2001

4. Completely air dry.

5. Place equipment in 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 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.5.4 Little Beaver®

The engine and power head should be cleaned with a power washer, steam jenny, or hand washed

with a brush using soap to remove oil, grease, and hydraulic fluid from the exterior of the unit. Do not use

degreasers. Rinse thoroughly with tap 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 to cleaning.

2. Clean with tap water and soap, using a brush if necessary, to remove particulate 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 at 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 project leader or the Quality Assurance Officer, this equipment may be

cleaned as specified in Section C.2.2 prior to use.

C.5.5 Drill Rig, Grout Mixer, 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 then rinsed with

tap water. The steam jenny 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.
EISOPQAM C - 11 November 2001

 The grout mixer should be washed with soap and tap water. The steam jenny may be used.

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 particulate 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. Drilling equipment that has been steam 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 water.

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.2.2 prior to use.

C.5.6 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.

C.5.7 Field Analytical Equipment

Field instruments for in-situ water analysis should be wiped with a clean, damp cloth. The probes

on these instruments (pH, conductivity, DO, etc.), should be rinsed with analyte-free water and air dried.

Any desiccant in these instruments should be checked and replaced, if necessary, each time the

equipment is cleaned.

C.5.8 Ice Chests and Shipping Containers

Ice chests and reusable containers shall be washed with soap (interior and exterior) and rinsed with

tap water and air dried before storage. If in the opinion of the field investigators the container is severely

contaminated with concentrated waste or other toxic material, it shall be cleaned as thoroughly as possible,

rendered unusable, and properly disposed.

C.5.9 Pressure Field Filtration Apparatus

1. Wash equipment thoroughly with soap and hot tap water using a brush to remove any particulate

matter or surface film.

2. Rinse equipment thoroughly with hot tap water.

3. Rinse equipment with 10 percent nitric acid solution.
EISOPQAM C - 12 November 2001

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 to prevent contamination during storage.

7. 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 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 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.5.10 Organic/Analyte Free Water Storage Containers

NOTE: These containers will be used only for transporting organic/analyte free water.

1. Wash containers thoroughly (interior and exterior) with hot tap water and laboratory detergent,

using a bottle brush to remove particulate 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 thoroughly with tap water.

5. Rinse containers thoroughly with analyte free water.

6. Rinse containers thoroughly with solvent and allow to air dry for at least 24 hours.

7. Cap with aluminum foil or Teflon® film.

8. Store in plastic bags.

When transporting organic/analyte free water to the field, use only containers cleaned as specified

above. Thoroughly rinse the interior of the container with organic/analyte free water prior to filling. Cap

with one layer of Teflon® film, one layer of aluminum foil, and label the container as "organic/analyte free

water" and include the date it was prepared. Do not store the organic/analyte free water at the FEC for more

than three days.
EISOPQAM C - 13 November 2001

C.5.11 Portable Solvent Rinse System

1. Replace Teflon® tubing if necessary. Wash nozzle and tubing fittings with hot, soapy water.

2. Rinse with analyte-free water.

3. Wrap nozzle and tubing ends with aluminum foil.

C.5.12 Splash Suits

CAUTION: Splash suits should be inspected for wear or damage. If, after consultation with the

Branch Safety Officer, the suit cannot be repaired, it should be discarded.

1. Wash and brush suit 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.5.13 SCBA Face-masks

CAUTION: Face-masks should be inspected for wear or damage. If, after consultation with the Safety

Officer, the face-mask cannot be repaired, it should be discarded.

1. Wash face-mask thoroughly inside and out with hot tap water and disinfectant soap. Use only

soft brushes. Do not use scouring pads of any type.

2. Rinse face-mask thoroughly inside and out with tap water.

3. Hang face-mask up until completely dry.

4. Place face-mask in plastic bag and return to SCBA case.

APRs are completely dismantled prior to cleaning. Then Steps 1 - 3 for SCBA face-masks are used.

When Completely dry, the APR is reassembled and placed in a plastic bag. 

C.5.14 Garden Hose

1. Brush exterior with soap and tap water

2. Rinse with tap water.

3. Flush interior with tap water until clear (minimum of one gallon).

4. Let completely air dry.

5. Coil and place in clean plastic bag.
EISOPQAM C - 14 November 2001

C.5.15 Portable Tanks for Tap Water

1. Scrub interior and exterior with soap and tap water.

2. Rinse with tap water.

3. Let completely air dry.

4. Close.

C.5.16 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 properly

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)

may be reused. All disposable sample containers will be stored in their original packing containers. When

packages of uncapped sample containers are opened, they will be placed in new plastic garbage bags and

sealed to prevent contamination during storage.

Specific pre-cleaning instructions for disposable sample containers are given in the following

sections.

C.6.2 Plastic Containers used for "Classical" Parameters

Plastic containers used for oxygen demand, nutrients, classical inorganics, and sulfides have no precleaning requirement. However, only new containers may be used.
EISOPQAM C - 15 November 2001

C.6.3 Glass Bottles for Semi-Volatile GC/MS Analytes

These procedures are to be used only if the supply of pre-cleaned, certified sample bottles is

disrupted. The Quality Assurance Officer will instruct personnel in the proper implementation of these

procedures.

If desired, pesticide-grade methylene chloride may be substituted for pesticide-grade isopropanol.

In addition, 1:1 nitric acid may be substituted for the 10% nitric acid solution.

When these sample containers are cleaned and prepared, they should be cleaned in standard sized

lots of 100 to facilitate the quality 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 times with tap water.

3. Rinse with 10% nitric acid solution.

4. Rinse three times with analyte free water.

5. Rinse bottles, jars, and liners (not caps) with solvent.

6. Oven dry bottles, jars, and liners at 125C. Allow to cool.

7. Place liners in caps and close containers.

8. Store in contaminant-free area.

C.6.4 Glass Bottles for Volatile GC/MS and TOX Analyses

These procedures are to be used only if the supply of pre-cleaned, certified sample bottles is

disrupted. The Quality 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 quality control procedures outlined in Section 5.14.

1. Wash vials, bottles and jars, Teflon“ liners and septa, and caps in hot tap water and laboratory

detergent.

2. Rinse all items with analyte free water.

3. Oven dry at 125C 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.
EISOPQAM C - 16 November 2001

C.6.5 Plastic Bottles for ICP Analytes

These procedures are to be used only if the supply of pre-cleaned, certified sample bottles is

disrupted. The Quality 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 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.
EISOPQAM D - 1 November 2001

APPENDIX D

SAMPLE SHIPPING PROCEDURES

D.1 Introduction

Samples collected during field investigations or in response to a hazardous materials incident must

be classified prior to 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 wastewater effluent, biological specimens, or any samples not expected to

be contaminated with high levels of hazardous materials.

Samples collected from process wastewater 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 (IATA), 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, IATA, 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 may 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 partially known, the

sample may not be offered for air transport.

In addition, the shipment of pre-preserved sample containers or bottles of preservatives (e.g.,

NaOH pellets, HCL, etc.) which are designated as dangerous goods by IATA 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 designee.

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, subject "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
EISOPQAM D - 2 November 2001

In addition, the shipment of the following preserved samples is not regulated, provided the amount

of preservative used does not exceed the amounts found in 40 CFR 136.3 (4) (see Appendix A). It is the

shippers' (individual signing the airway bill) responsibility to ensure that proper amounts of preservative are

used:

 Drinking water

 Ambient water

 Treated effluent

 Biological specimens

 Sediment

 Wastewater treatment plant sludge

 Water 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 Laboratory 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 may 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) to 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 tight (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 sturdy cooler in good repair. Secure and tape the drain plug with fiber or duct tape.

Line the cooler with a large heavy duty plastic bag.

6. Place two to four inches of vermiculite in 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" (or ice that has been "double bagged" in heavy duty polyethylene bags and

properly sealed) on top of and/or between the samples. Fill all remaining space between the

bottles or cans with vermiculite.
EISOPQAM D - 3 November 2001

8. Securely fasten the top of the large garbage bag with tape (preferably plastic electrical tape).

9. Place the Chain-of-Custody Record and the CLP Traffic Report Form (if applicable) into

a plastic bag, and tape the bag to the inner side of the cooler lid.

10. Close the cooler and securely tape (preferably with fiber tape) the top of the cooler shut.

Chain-of-custody seals should be affixed to the top and sides of the cooler within the

securing tape so that the cooler cannot be opened without breaking the seal.

11. Shipping containers must be marked "THIS END UP", and arrow labels which indicate the

proper upward position of the container should be affixed to the container. A label

containing the name and address of the shipper should be placed on the outside of the

container. Labels used in the shipment of hazardous materials (e.g., Cargo Only Air Craft,

Flammable Solids, etc.) are not permitted to be on the outside of containers used to transport

environmental samples.
EISOPQAM D - 4 November 2001

D.4 References

1. Dangerous Goods Regulations, International Air Transport Authority (IATA). Current Edition.

which changes annually. 

2. EPA Order 1000.18, February 16, 1979.

3. "Final Regulation Package for Compliance with DOT Regulations in the Shipment of

Environmental Laboratory Samples," Memo from David Weitzman, Work Group Chairman,

Office of Occupational Health and Safety (PM-273), US-EPA, April 13, 1981.

4. 40 CFR 136.3. July 1, 2001. See Table 11, Footnote 3.
EISOPQAM E - 1 November 2001

APPENDIX E

PUMP OPERATING PROCEDURES

E.1 Peristaltic Pump

E.1.1 Introduction

When relatively small volumes of water are required for purging and sampling, and the water level

is within the limit 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

l. Place a coil of standard-cleaned (Appendix B) Teflon® tubing, equal to the well depth plus an

additional five to ten feet, 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 purge.

Observe pump direction 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.
EISOPQAM E - 2 November 2001

8. For wells which are not evacuated to dryness, particularly those with recovery rates equal to

or very nearly equal to the purge rate, there may not be a complete exchange and removal of

stagnant water in that portion of the water column above the tubing intake. For this reason, it

is important that the tubing intake be placed in the very uppermost portion of the 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 is not acceptable for collecting samples for organic

compounds analyses and cannot easily be field cleaned between sampling locations prior to collecting

samples for other parameters. For these reasons, it is necessary to use a vacuum container, placed between

the pump and the well for sample collection with a peristaltic pump. However, if the flexible pump tubing

is decontaminated according to Appendix C of this 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 tubing 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.

1. Disconnect the purge tubing from the pump. Make sure the tubing is securely attached to the

protective casing or other secure object.

2. Insert the tubing into one of the ferrule nut fittings of a Teflon® vacuum container transfer cap

assembly.

3. Place a suitable length of Teflon® tubing between the remaining transfer cap assembly ferrule

nut fitting and the vacuum side of the flexible tubing in the peristaltic pump head. Securely

hand tighten both fittings.

4. Turn the pump on. Water should begin to collect in the transfer container (typically a 4-liter

or 1-gallon sample container) 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 extractable

organic compounds, metals, and cyanide can be collected using this system. Because the onegallon (4-liter) containers used by the Branch are rinsed with nitric acid during cleaning, they

cannot be used for collecting samples to be analyzed for nitrogen sensitive parameters.

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 the water

column in the sample delivery tubing during the transfer phase, when large volumes of sample

are required, is acceptable. These devices, however, must be constructed so that they may be

completely disassembled and cleaned according to the procedures in Appendix C.2.1

7. When sampling is completed, all Teflon® tubing should be discarded.
EISOPQAM E - 3 November 2001

E.2 Large Diameter Electric Submersible Pumps

E.2.1 Introduction

Pumps included within this category are any of the typical, large diameter (3-inch to 4-inch) electric

submersibles, such as Goulds®, Grunfos®, or Jacuzzi®. These pumps are necessary when large amounts

of water must be removed from wells such as deep, 4-inch monitoring wells and drilled or bored potable

wells.

These pumps are generally powered by 120-volt generators and require a minimum of two persons

for 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.

E.2.2 Safety

1. Place the generator on dry 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.

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 tripod 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 downgradient 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 the back of any passenger vehicle or with any sampling equipment or

containers.

E.2.3 Pre-loadout Checkout Procedure

1. 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.
EISOPQAM E - 4 November 2001

E.2.4 Operation

1. 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 by 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 cart.

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 below the top of the water column.

3. Start generator, then connect power cord from pump.

4. After starting pump, closely observe operation to determine if drawdown is occurring in well.

If the water level is not pulled down significantly, keep pump at initial level and continue to

purge. If the water level drops, lower the pump to keep up with the drawdown. Do not allow

the pump to run dry, as this will damage it.

E.2.5 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 in trailer with generator.
EISOPQAM E - 5 November 2001

E.2.6 Trouble Shooting

No Power to Pump

1. Loose connections at

pump.

1. Check wiring at pump. 

Repair as needed. 

(Generator Off!!)

2. Cord unplugged at

generator.

2. Plug pump back in.

Generator Running,

No Pump Output

1. Pump out of water. 1. Lower pump into

water.

2. Hose collapsed or

kinked.

2. Unkink hose.

3. Generator output

failing.

3. Put load on generator

and check output or

check voltage output

meter.

Sluggish Discharge

1. Sediment or other

material clogging

screen.

1. Remove material from

screen.

2. Kinked hose. 2. Unkink hose.

E.3 QED® Bladder and Purge Pumps

E.3.1 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,

usually 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.

E.3.2 Operation - Bladder Pump

1. Connect air supply hose to "pump supply" connection on controller and to brass air connection

on hose reel cart.

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 well

as possible, in the down wind direction.
EISOPQAM E - 6 November 2001

4. Adjust the timing of the discharge and refill cycles until maximum flow is achieved.

5. Lower pump, as necessary, if water level is reduced in well.

E.3.3 Operation - Purge Pump

1. Connect air supply 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 top of pump.

3. Lower pump, air hose and garden hose into water column until top of pump is several feet

below top of water column.

4. Follow Steps 3 through 5 above.

E.3.4 Trouble Shooting

Compressor running,

no pressure on discharge cycle

1. Air supply fittings

loose.

1. Check all fittings and

tighten.

2. Bladder is perforated. 2. Replace bladder.

3. Exhaust adapter

installed in wrong

direction.

3. Remove adapter and

replace in correct

orientation.

Compressor running,

pressure low,

no water discharged

1. Obstruction in ball

check assembly

allowing water to be

pushed out of pump at

check.

4. Remove obstruction.

2. Air supply fittings

loose.

5. Check all fittings.

E.4 Small Diameter Electric Submersible Pumps

E.4.1 Introduction

Included within this category is the Grundfos Redi-Flo2 small diameter electric submersible pump.

With a diameter of approximately 1.75 inches, it is designed to be used in 2-inch diameter and larger wells.

(Note: If used in any well larger than 4-inch diameter, this pump must be equipped with a cooling shroud to

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 operating range).

The Redi-Flo2 is a variable speed pump capable of providing pump rates from less than 100 ml/minute to

in excess of 8 gallons per minute.
EISOPQAM E - 7 November 2001

The pump, depending on the controller being used, operates with either 115v or 220v power. The

pump rate is controlled by adjusting the frequency of the current going to the pump motor. It is a lightweight pump and can be easily handled by one person when lowering, but two people are generally needed

when removing the pump, one to pull and another to reel in the hose and power lead.

E.4.2 Safety

1. Place the generator on dry 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.

2. Inspect the electrical extension cord, as well as the lead to the pump, 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. Wear rubber boots to insulate against shock hazards.

5. If purge water is not collected, direct the discharge away from the well and generator,

preferably downgradient of the area.

6. Make sure that the generator is set to the proper voltage.

7. Do not add gasoline or oil to 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 equipment or

containers.

E.4.3 Pre-loadout Checkout Procedures

1. Check the oil and gasoline in the generator, making sure that there is enough gasoline to test

the generator prior to 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 organic/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.4.4 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.
EISOPQAM E - 8 November 2001

3. Start the generator, then connect the power cord from the pump. Make sure the proper voltage

has been selected. 

4. After starting the pump, closely observe operation to determine if drawdown is occurring in

the well. If the water level is not pulled down, raise the pump in the water column one to two

feet from the top of the water 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, it will create delays in sampling.

E.4.6 Maintenance and Precautions

1. Empty the hose of contaminated water before leaving the sampling location. Do not bring the

hose back to the FEC if it 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 it is operating. This is a common place for debris or other material

to accumulate and interfere with the proper operation of the device.

E.4.7 Trouble Shooting

Generator Running,

No Pump Output

1. Loose connection at

pump.

1. Check wiring at pump. 

Repair as needed.

(Generator off!!)

2. Cord unplugged at

generator.

2. Plug pump back in.

3. Over voltage on

controller display.

3. Adjust generator

output/idle speed;

allow generator more

warm-up time.

4. Pump out of water. 4. Lower pump into

water.

5. Hose collapsed or

kinked.

5. Unkink hose.

6. Pump will not run or

shuts down with

thermal overload signal.

6. Open cooling water

reservoir and check

cooling water. Add

additional

organic/analyte-free

water to cooling water

reservoir.
EISOPQAM F - 1 November 2001

APPENDIX F

REGIONAL TECHNICAL SUPPORT FOR CRIMINAL INVESTIGATIONS

 SESD/CID

The Science and Ecosystem Support Division (SESD) provides technical support to the Atlanta Area

and Jacksonville Area Offices, Office of Criminal Enforcement, Forensic and Training, Criminal

Investigation Division (CID), for those investigations requiring the collection of samples, laboratory

analyses, or other technical support. These procedures address the means by which technical support is

requested by the CID Offices and provided by SESD. Detailed technical procedures will be referenced to

the various Standard Operating Procedures and Quality Assurance Manuals utilized by SESD.

The primary objectives of SESD support for the CID criminal investigations are to provide accurate,

complete, admissible, and defensible reports and data for case development and subsequent legal

proceedings. To accomplish these objectives, SESD and the CID Offices have jointly agreed to follow these

procedures.

F.1 Technical Assistance Required by the Atlanta Area Office

The CID Offices under the Direction of a Special Agent-in-Charge (SAC) conducts criminal

investigations in Region 4 and 14 pursuant to federal environmental laws and regulations. The technical

assistance requirements for criminal cases vary from investigation to investigation. To assist the SAC in

identifying the type and scope of technical assistance required, a Technical Coordinator position has been

established in the Atlanta Area Office. The Technical Coordinator’s primary function is to provide technical

advice to the SAC and Case Agents. It is the responsibility of the Technical Coordinator to assure that

requests for technical support are directed to the appropriate Regional Program and SESD offices. After a

decision by the SAC to request technical support for a criminal investigation, the Technical Coordinator will

discuss the case with the SESD Director or their designated representative. The SESD Director in

consultation and with the concurrence of the Deputy Regional Administrator (DRA) will decide whether or

not technical support will be provided by SESD.

Following a decision that technical support will be provided by SESD, the SAC will prepare a

written request addressed through the DRA to the SESD Director. Copies of the request will be routed to

the appropriate Regional program offices.

Prior to conducting of the investigation, the Technical Coordinator will discuss the case with SESD

personnel, and will inform the Case Agent of any technical requirements that may influence project planning.

Conversely, it is the responsibility of the Technical Coordinator to inform SESD personnel of all known

technical aspects of a case including the presence of any known situations which may pose health and/or

safety risks or otherwise interfere with their operations. 

Subsequent to the field investigation, the Technical Coordinator in consultation with the Case Agent

will discuss with SESD personnel the progress of scheduled analyses and the potential need for additional

or more detailed analyses. Information regarding the need to alter work schedules so as to meet changing

grand jury or federal court dates will be transmitted immediately from the Technical Coordinator to SESD.

When work schedules must be delayed, the technical reasons for the delay will be communicated from the

Technical Coordinator to the Case Agent.

Upon completion of analyses and report preparation by SESD, and prior to presentation of the results

to a grand jury or federal court, the Technical Coordinator will arrange for an audit and inventory of evidence

and files in SESD’s possession.
EISOPQAM F - 2 November 2001

F.2 Project Requests

All requests for SESD support for criminal investigations shall originate with the Atlanta Area or

Jacksonville Area Offices. Any information obtained by SESD staff regarding potential criminal activities

shall immediately be referred to the appropriate CID Office. Direct requests to SESD from any other federal,

state, or local agency shall be referred to the corresponding CID SAC for appropriate action.

Prior to an official request from the CID Office to SESD, an informal contact shall be made with the

SESD Senior Enforcement Specialist for the appropriate SESD Branch or Section Chief concerning the

availability of resources and expertise necessary for providing the requested technical support. If SESD is

able to provide the support, the SAC shall prepare an official request to the SESD Director, through the DRA

(with copies to the SESD Senior Enforcement Specialist and the appropriate SESD Branch or Section

Chief). For criminal investigations when SESD’s priorities prohibit and immediate response, the DRA will

determine an appropriate course of action. If the DRA determines that providing the requested technical

support will be in the best interest of the Region, the support will be provided and adjustments will be made

to other SESD commitments. SESD’s technical support may begin immediately after receiving concurrence

from the DRA. The SAC has the responsibility of notifying appropriate regional organizational units, e.g.,

Office Directors, Division Directors, etc., of potential or on-going investigations receiving assistance from

SESD or the technical divisions at NEIC.

All emergency requests shall be handled expeditiously. In such instances, SESD may provide the

requested assistance immediately upon obtaining verbal approval from the DRA. Either the SAC or the

SESD Director may initiate contact with the DRA for emergency requests. However, all such requests shall

be followed by a written request from the SAC, through the DRA to the SESD Director.

F.3 Project Coordination

Once the decision has been made to provide technical support, the SESD Director or their designee

shall assign the project to the appropriate Branch/Section for assignment of a Project Leader. The Project

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 shall discuss the technical and workload requirements with his/her immediate

supervisor. A core team shall then be selected which will eventually conduct the study, coordinate analytical

support, and/or provide other technical support. When required, additional staff will be assigned from other

Sections or Branches with the approval of the appropriate Branch Chief or SESD Director. Once the 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 Agent.

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 appropriate SESD, Analytical Support Branch

personnel. The study plan and site-safety plan shall be assembled under the direction of the Project Leader

and submitted to the appropriate management, and Case Agent for review and concurrence. The time-frame

for receiving comments will depend upon the urgency of the investigation, but shall not exceed 10 working

days. During emergencies, an investigation may be conducted without the preparation of a detailed study

plan. However, during these situations, a memorandum shall be prepared by the Project Leader briefly

describing the technical work to be accomplished and stating that the investigation will strictly conform to

appropriate SESD Standard Operating Procedures and Quality Assurance Manuals, and Safety Manuals.
EISOPQAM F - 3 November 2001

A final study plan will be prepared once all appropriate comments are received by the Project Leader.

In general, these study plans should contain the following elements. However, upon advice of the Case

Agent, the content and format of any study plan may be substantially changed to meet the needs of the

particular investigation.

 Introduction -- a brief statement of the problem to be investigated;

 Background – a short but concise history of the case history; 

 Objectives -- a statement as to what the investigation is to accomplish and what specific

laws and regulations may have been violated;

 Scope -- a definition of the limits of the study;

 Time Schedule -- a statement outlining when the study will be conducted, analytical results

will be available, the draft 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 SESD’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 Quality Assurance Manuals shall be thoroughly justified and must

produce evidence which can withstand objections by the defense;

 Analytical Requirements -- an estimate of the number of samples to be collected, required

analyses and which laboratory(s) will analyze the samples;

 Logistics -- an estimate of manpower requirements and a general description of specific

functions of project personnel, special equipment and vehicles to be used, use of mobile

laboratories, how samples are to be transported to the laboratory, etc.; and

 Safety Plan -- a safety contingency plan will be included.

F.5 Field Investigation

The field investigation will be conducted under the direct supervision of the Project Leader and the

general supervision of the Case Agent responsible for conducting the investigation. SESD will endeavor to

meet all objectives set forth in the study plan and any on-scene changes or additional activities requested by

the Case Agent. The SESD Project Leader or the SESD Safety Officer shall have sole 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.

Any deviations from the study plan or the appropriate Standard Operating Procedures and Quality Assurance

Manuals must be approved and documented by the Project Leader. Any deviations must produce evidence

which can withstand objections by the defense.

During the field study, the Project Leader or designee is responsible for insuring that all chain-ofcustody and quality control procedures for sampling, flow measurements, field analyses, record-keeping, etc.,

are followed. All field personnel participating in criminal investigations must understand and follow the

chain-of-custody and quality control procedures relative to their assignments. Following completion of the

field activities, the Project Leader or designee shall account for all field documentation, e.g. field logbooks,

sample tags and chain-of-custody records, and verify that they are complete. Sample tags will remain on the

sample containers in the custody of the laboratory until relinquishment to the court or final disposition of the

case.
EISOPQAM F - 4 November 2001

F.6 Laboratory Support

A senior analyst shall assist in determining the analytical needs of the investigation and provide

overall coordination of sample analyses and data reporting. 

Upon delivery of samples to the Science Ecosystem Technology Center custody room, the samples

shall be transferred, via chain-of-custody procedures, from the Project Leader or designee to the laboratory

Sample Custodian or designee. The Sample Custodian shall document the condition of the samples and

verify the uniformity of information on the sample tags and chain-of-custody records prior to placing the

samples in the sample custody room.

All sample handling, sample preparation, and analyses shall be in strict conformance with the

Analytical Support Branch Operations and Quality Control Manual (ASBOQCM).

The senior analyst shall notify the Project Leader as results become available. Final analytical data

shall be reported directly to the Project Leader after all QA/QC procedures have been completed. Any

analytical problems or deviations concerning holding times, analytical procedures, etc., shall be reported to

the Project Leader. When requested by the Case Agent, this information shall be documented in a

memorandum stamped “CONFIDENTIAL”, and transmitted to the Project Leader who shall immediately

notify the Case Agent. A copy of the memorandum shall also be immediately sent to the Technical

Coordinator and the Case Agent as requested.

F.7 Final Report

The Project Leader is responsible for preparing a final investigative report. A draft report shall be

prepared for internal review by all core team members and the Case Agent. The draft report may also be

reviewed by other appropriate staff, e.g., supervisors and technical experts. All draft reports shall be

destroyed upon completion of the final report.

A final investigative report will be prepared by the Project Leader. This report shall be limited to

factual information and observations concerning SESD activities, e.g., sampling, analyses, etc., 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. When this

is done, the memorandum will be stamped “CONFIDENTIAL” on each page and delivered to the Case

Agent. The final report(s) shall be delivered to the Case Agent who shall be responsible for ultimate

distribution.

F.8 Document Control

The core team members are responsible for the initial collection and maintenance of all SESD

documents, records, and evidence obtained during the field investigation. The documents, records and

evidence shall be delivered to the Project Leader at the competition of the field investigation. The Project

Leader shall immediately construct an inventory of all such materials obtained. If requested, the Project

Leader will deliver all such materials to the Case Agent.

All original analytical data and supporting documentation, e.g., chromatograms, mass spectra,

QA/QC records, calculations, etc., shall be maintained by the Analytical Support Branch according to their

Laboratory Operations and Quality Assurance Manual. If requested, copies of all records shall be provided

to the Case Agent. Dissemination of such records shall only occur under federal court order, as directed by

DOJ, or as directed by the prosecuting attorney. The Laboratory Coordinator 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.
EISOPQAM F - 5 November 2001

All documents, records, evidence, etc., retained by the SESD will be maintained in a locked filing

cabinet or a secure area under the direct control of the appropriate Branch Chief, Section Chief, or the

custodian of SESD’s central records center.

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 insufficient space in

the sample custody room, the Case Agent shall expeditiously inform the laboratory when samples can be

disposed. Sample disposal procedures shall be as described in the Analytical Support Branch Laboratory

Operations and Quality Assurance Manual.
EISOPQAM G - 1 November 2001

APPENDIX G

BATTERY CHARGING AND STORAGE OPERATIONS

PERFORMANCE OBJECTIVES:

 To insure that field batteries are properly charged and maintained.

 To insure that field battery charging is conducted in a safe and efficient manner.

 To provide a means for keeping an inventory of the status and number of field

batteries on hand.

G.1 Receiving Batteries from the Field

Upon return from the field, batteries may or may not require maintenance and charging. The

following procedure will be used to process incoming batteries.

CAUTION

DANGER OF EXPLODING BATTERIES

Batteries generate explosive gasses. Keep sparks, flames, burning cigarettes, cigars, or other ignition

sources away at all times. Always shield eyes when working near batteries. Charge batteries only in well

ventilated areas. Wear protective covering when working around batteries.

DANGER OF ACID BURNS

Always wear a face shield, protective coat, and rubber gloves when handling batteries. In case of

skin contact with acid, immediately wash affected area for 15 minutes, using safety shower, eye wash, or sink

as required. Seek medical attention as soon as possible. Notify the designated Safety Officer or management

in the event of injury. 

Procedure

Only designated persons are allowed entry into the battery charging building.

1. Check batteries for proper electrolyte level; if necessary, use battery filler to add tap water

until levels in each cell are mid-way between the two level marks on the case. Insure that

cell filler cap vents are clear. Replace filler caps immediately after filling.

2. Check battery terminals for cleanliness, and clean with wire brush if necessary.

3. Check batteries with load tester. Batteries which register in the green arc can be placed back

in a battery box and stored in the "Charged Battery Area". Batteries which register below

the green arc are to be removed from the battery box and stored in the "Discharged Battery

Area". Empty battery boxes are to be stored beside the sink in the battery building using

care not to block access to the safety shower.
EISOPQAM G - 2 November 2001

G.2 Charging Batteries

Battery charging equipment is to be operated only by trained personnel who are familiar with these

procedures. If at any time personnel are not absolutely sure of what to do, work should stop immediately and

assistance should be sought. NOTE: Charger will not operate on less than four batteries.

CAUTION

DANGER OF EXPLODING BATTERIES

Batteries generate explosive gasses. Keep sparks, flames, burning cigarettes, cigars, or other ignition

sources away at all times. Always shield eyes when working near batteries. Charge batteries only in well

ventilated areas. Wear protective covering when working around batteries.

DANGER OF ELECTRICAL SHOCK

Never touch output leads while charger switch is on. Charger's maximum output is 280 volts at 9.5

amps.

DANGER OF ACID BURNS

Always wear face shield, protective coat, and rubber gloves when handling batteries. In case of skin

contact with acid, immediately wash affected area for 15 minutes, using safety shower, eye wash, or sink as

required. Seek medical attention as soon as possible. Notify the designated Safety Officer or management

in the event of any injury. 

Procedure

1. Insure that the 240 volt power supply box is locked in the "OFF" position.

2. Insure that the Charger Power Switch is in the "OFF" position.

3. Insure that the Charger Control Knob is set at "0".

4. Inspect all terminal clips for broken insulation and proper connection. 

5. Clean all terminal clips with a wire brush.

6. Place the batteries in the charger bench so that the battery numbers are visible from the front

and that the battery terminals are to the right when facing the bench. In this configuration,

the positive terminals of all batteries will be to the front of the charging bench.

7. Connect the terminal clips securely to the battery terminals. Dirty terminal clips, dirty

battery terminals, or loose connections will result in dangerous arcing when the charger is

turned on. 

8. Insure that the charger's positive lead is attached to the positive terminal of the battery on

the right hand facing end of the bench and that the charger's negative lead is attached to the

negative terminal of the battery on the left hand facing end of the bench.

9. Remove all battery cell filler caps and store them in the box on the battery bench. Insure

that the battery electrolyte level is between fill lines. If low, add tap water with the battery

filler. If high, use battery filler to remove the excess electrolyte and dispose of it in the

carboy labeled "Battery Acid".
EISOPQAM G - 3 November 2001

10. Unlock the 240 volt power supply box and place lock on top of the box. Do not place lock

back in the lock-out holes for storage as this will prevent a rapid turn off of the system in

an emergency.

11. Place the 240 volt power supply box switch in the "ON" position.

12. Set the charger's timer as follows:

For 4-7 batteries, set timer to 6 hours.

For 8-11 batteries, set timer to 9 hours.

For 12-18 batteries, set timer to 12 hours.

Never operate the charger with the timer in "Hold" position.

13. Recheck the charger's control knob to insure it is on "0", and then place the charger's power

switch to "ON".

14. SLOWLY increase the charger's control knob until a reading of between 7 and 8 amps is

obtained on the amp meter. 

WARNING

Never exceed a reading of more than 8 amps output from the charger.

Always advance the control knob slowly. In the event of a bad contact, arching of the

charge current will occur and can result in an excessive flow of current to the batteries.

15. Observe the batteries for a few minutes to insure that none are boiling over.

G.3 Post-Charging

After batteries have charged for the amount of time set on the charger, the following procedure will

be used to shut-down the charger and to remove and store charged batteries.

CAUTION

DANGER OF EXPLODING BATTERIES

Batteries generate explosive gasses. Keep sparks, flames, burning cigarettes, cigars, or other ignition

sources away at all times. Always shield eyes when working near batteries. Charge batteries only in well

ventilated areas. Wear protective covering when working around batteries.

DANGER OF ELECTRICAL SHOCK

Never touch output leads while charger switch is on. Charger's maximum output is 280 volts at 9.5

amps.

DANGER OF ACID BURNS

Always wear face shield, protective coat, and rubber gloves when handling batteries. In case of skin

contact with acid, immediately wash affected area for 15 minutes, using safety shower, eye wash, or sink as

required. Seek medical attention as soon as possible. Notify the designated Safety Officer or management

in the event of any injury. 
EISOPQAM G - 4 November 2001

Procedure

1. Turn charger's control knob to "0".

2. Place charger's power switch in the "OFF" position.

3. Place the 240 volt power supply box switch in the "OFF" position and lock out the switch.

4. Replace all battery cell filler caps.

5. Disconnect all terminal clips.

6. Check all batteries with the load tester. Any batteries not indicating in the green arc, or

slightly above will be red-tagged and stored in the "Discharged Battery Area". Those

batteries indicating a sufficient charge on the load tester are to be placed in a battery box and

stored in the "Charged Battery Area".

7. Record the status of all batteries removed from the bench in the "Battery Log Book".

G.4 Maintenance

During the first week of each month, the following maintenance procedures will be performed at the

battery building. The individual performing the maintenance will complete a maintenance report and submit

it to the designated Safety Officer.

Procedure

1. Sweep floor

2. Empty trash can

3. Check battery acid carboy. If more than half full, note on the maintenance report.

4. Check contents of the acid spill kit. If contents have been depleted, note on the maintenance

report.

5. Check contents of the first aid kit. If contents have been depleted, note on the maintenance

report.

6. Check operation of safety shower and eye wash.

7. Check all batteries in the "Charged Battery Area" with the load tester. Any batteries testing

below the green arc of the load tester should be removed from their battery box, red-tagged

with the notation "Failed Monthly Check" and date of check, and placed in the "Discharged

Battery Area".
EISOPQAM G - 5 November 2001

FIGURE G.1

BATTERY LOG

BATTERY

NUMBER

DATE

CHARGED

CHARGE 

YES/NO

INIT BATTERY

NUMBER

DATE

CHARGED

CHARGE 

YES/NO

INIT
EISOPQAM G - 6 November 2001

FIGURE G.2

BATTERY BUILDING

MAINTENANCE REPORT

DATE:________________

COMMENTS

1. Floor Clean (Y/N) _____ _____________________________________________________

2. Trash Can Empty (Y/N) _____ _____________________________________________________

3. Carboy Under Half 

Full (Y/N) _____ _____________________________________________________

4. Acid Spill Kit

OK (Y/N) _____ ____________________________________________________

5. First Aid Kit

OK (Y/N) _____ _____________________________________________________

6. Safety Shower/Eye Wash

OK (Y/N) _____ _____________________________________________________

7. Charged Battery Status

Enter # In Stock _____ ____________________________________________________

SIGNED:__________________________________________________________________________________________

NOTE: SEND COMPLETED REPORT TO BRANCH SAFETY OFFICER
EISOPQAM H - 1 November 2001

APPENDIX H

TECHNICAL SYSTEMS AUDIT FORM QUESTIONNAIRE

Agency

Address

Telephone Number

Reporting Period (beginning-ending dates)

Organization Director

Air Program Supervisor

Data Management Supervisor

Quality Assurance Officer

Questionnaire Completed

(date) (by)

On-Site Visit

Date: Audit Team Members:

Affiliation of Audit Team
EISOPQAM H - 2 November 2001

A. NETWORK MANAGEMENT

1. General

 Complete the table below for each of the pollutants monitored as part of your air monitoring network

SO2 NO2 CO O3 PM-10 PM-2.5 Pb

NAMS

SLAMS

SPM

PAMS

Total

 Describe any changes which will be made within the agency’s monitoring program the next calendar year

Question Yes No Comment

What is the most current official SLAMS Network

Description?

 I. Is it available for public inspection ?

 II. Does it include the following for each site ?

 Monitor ID Code (AIRS Site ID#)

 Sampling and Analysis Method

 Operative Schedule

 Monitoring Objective and Scale of Representativeness

 Any Proposed Changes

 Modification since last audit date of last audit

Number of Monitors

Pollutant Added Deleted Relocated

SO2

NO2

CO

O3

PM-10

PM-2.5

Pb
EISOPQAM H - 3 November 2001

2. Network Design and Siting

 Indicate by Site ID # any non-conformance with the requirements of 40 CFR 58, Appendices D and E

Monitor Site ID Reason for Non-Conformance

SO2

O3

CO

NO2

PM-10

PM-2.5

Pb

Question Yes No Comment

 Have NAMS hard copy information reports been prepared and 

submitted for all monitoring sites within the network?

 Does each site have the required information including:

AIRS Site ID Number?

Photographs/slides to the four cardinal compass points?

Startup and shutdown dates?

Documentation of instrumentation?

Reasons for periods of missing data?

 Who has custody of the current network documents ? Name:

Title:

 Does the current level of monitoring effort, site placement,

 instrumentation, etc., meet requirements imposed by

 current grant conditions?

 How often is the network design and siting reviewed? Frequency:

Date of last review:

 Provide a summary of the monitoring activities conducted as the SLAMS/NAMS network by the agency

I. Monitoring is seasonal for (indicate pollutant and month of high and low concentrations).

Pollutant High Concentrations Low Concentrations
EISOPQAM H - 4 November 2001

II Monitoring is year-round for (indicate pollutant)

Pollutant Collocated (Y/N)

Question Yes No Comment

 Does the number of collocated monitoring sites meet the 

requirements of 40 CFR 58 Appendix A?

 Does the agency monitor and/or analyze for non-criteria air and

/or toxic air pollutants? 

If yes complete forms below

Pollutant Monitoring Method/Instrument SOP Available (Y/N)

3. Organization, Staffing and Training

 Number of individuals available to each of the following program areas

Program Area Number Comment on need for additional personnel

Network Design and

Siting

Resources and Facilities

Data and Data

Management

QA/QC

Question Yes No Comment

 Does the agency have an established training program?

I Where is it documented

 Does it make use of seminars, courses, EPA sponsored 

college level courses?
EISOPQAM H - 5 November 2001

4. Facilities

Identify the principal facilities where the work is performed which is related to the SLAMS/NAMS network. Do not include monitoring sites but

do include any work which is performed by contract or other arrangements

Facility Location Main SLAMS/NAMS Function

 Indicate any areas of facilities that should be upgraded. Identify by location

 Are there any significant changes which are likely to be implemented to agency facilities before the next systems audit? Comment on your

agency’s needs for additional physical space (laboratory, office, storage, etc.)

Facility Function Proposed Change - Date
EISOPQAM H - 6 November 2001

B: FIELD OPERATIONS

1. Routine Operations

Question Yes No Comment

 On average, how many sites does a single site operator have 

responsibility for?

 How many of the sites of your SLAMS/NAMS network are 

equipped with manifolds(s)

I Briefly describe most common manifold type

II Are manifolds cleaned periodically ? How often?

IV Are manifold(s) equipped with a blower ?

V Is there sufficient air flow through the manifold at all

times?

Approximate air flow:

VI Is there a conditioning period for the manifold after 

 cleaning?

Length of time:

I)What material is used for instrument lines?

2) How often are lines changed?

l) Please comment briefly and prioritize your currently identified instrument needs

2. Quality Control

Please indicate frequency of multi point calibrations

Pollutant Frequency

SO2

NO2

CO

O3

PM10

Pb

PM2.5

Please list the authoritative standards used for each type of flow measurement, indicate the frequency of calibration standards to maintain field

material/device credibility

Flow Device Primary Standard Frequency of Calibration
EISOPQAM H - 7 November 2001

 Please complete the table below for your agency’s site standards.

Parameter Primary Standard Secondary Standard Recertification Frequency

CO

NO2

SO2

O3

Question Yes No Comment

 Are level 1 zero and span (z/s) calibrations (or calibration

checks made for all continuous monitoring equipment and flow

checks made for PM 10 and PM2.5 samplers?

 Does the agency have acceptance criteria for zero/span checks?

 I. Are these criteria known to the field operations

personnel?

 II. Are they documented in standard operating procedures? If not indicate document and section where they can be

found.

III. Do the documents discussed in (II) above indicate when

 zero/span adjustments should and should not be made? 

 In keeping with 40 CFR 58 regulations, are any necessary zero

and span adjustments made after precision checks?

 If no, why not?

 Are precision check control charts maintained?

 Are precision checks routinely performed within concentration

ranges and with a frequency which meets or exceeds the

requirements of 40 CFR 58, Appendix A?

Please comment on any discrepancies

3. Preventive Maintenance

 Has the field operator been given any special training in performing preventive maintenance? Briefly comment on background and/or courses.

 Is this training routinely reinforced? Yes No 

 If no, why not?

 Comment briefly on the adequacy and availability of the supply of spare parts, tools and manuals available to the field operator to perform any 

necessary maintenance activities. Do you feel that this is adequate to prevent any significant data loss?

 Is the agency currently experiencing any recurring problem with equipment or manufacturer(s)? If so, please identify the equipment and/or

manufacturer, and comment on steps taken to remedy the problem.
EISOPQAM H - 8 November 2001

4. Record Keeping

Question Yes No Comment

Is a record maintained at each site to document site visits,

preventive maintenance and resolution of site operational

problems and corrective actions taken?

Other uses?

Is the record maintained currently and reviewed periodically? Frequency of Review

 Once entries are made and all the record completed, is it sent

 to the laboratory for archiving? 

 If no, is it stored at other location(s) (specify)

 What other records are used?

Zero/span record?

Maintenance log?

Log of precision checks?

 Control charts?

 A record of audits?

Are calibration records or at least calibration constants available

to field operators?

5. Data Acquisition and Handling

 With the exception of PM 10, are instrument outputs (that is data) recorded to (a) stripcharts, (b) magnetic tape acquisition system, (c) digitized

and telemetered directly to agency headquarters? Please complete the table below for each of the reporting organizations, or agencies within the

overall R.O.

 Data Acquisition Media

Reporting Organization Pollutants (a, b, c or combination) 

Question Yes No Comment

 Is there a stripchart backup for all continuous analyzers?

 On High-volume samplers without flow controllers? Log sheet , Dixon chart , Other (specify)

What kind of recovery capabilities for data acquisition equipment are available to the field operator after power outages, storms, etc? Briefly

describe below.
EISOPQAM H - 9 November 2001

C. LABORATORY OPERATIONS (WHERE APPLICABLE)

1. Routine Operations

 What analytical methods are employed in support of your air monitoring network?

 

Analysis Methods

 PM-10

 Pb

 

 PM 2.5

 Others (list by pollutant)

 

Question Yes No Comment

 Do any laboratory procedures deviate from the 

reference, equivalent, or approved methods? 

 If yes, are the deviations for lead analysis ,

PM-10 filter conditioning or other 

(specify below)?

 Have the procedures and/or any changes been approved 

 by EPA? 

Date of Approval

 Is the documentation of Laboratory SOP complete?

Is sufficient instrumentation available to conduct your laboratory analyses? Yes No If no, please indicate instrumentation

needs 

 Instrument Needed Analysis New or Replacement Year of Acquisition
EISOPQAM H - 10 November 2001

2. Quality Control

 Please complete the table for your agency’s laboratory standards.

Parameter Primary Standard Secondary Standard Recertification Schedule

Weights

Temperature

Moisture

Barometric Pressure

Flow

Lead

Sulfate

Nitrate

 Comment on the traceability of chemicals used in the preparation of calibration standards.

Question Yes No Comment

Does the laboratory purchase standard solutions such as those

for use with lead or other AA analysis?

Are all calibration procedures documented? Where? 

 (title) (revision)

 Are at least one duplicate, one blank, and one standard or

 spike included with a given analytical batch?

Identify analyses for which this is routine operation

 Briefly describe the laboratory’s use of data derived from blank analyses.

Question Yes No Comment

Do criteria exist which determine acceptable/non-acceptable

blank data?
EISOPQAM H - 11 November 2001

How frequently and at what concentration ranges does the lab perform duplicate analysis? What constitutes acceptable agreement?

How does the lab use data from spiked samples? Please indicate what may be considered acceptable percentage recovery by analysis? Please

complete the table below

Pollutant % Recovery Acceptance Criteria

Question Yes No Comment

Do criteria exist for “real time quality control based on the

results obtained for the mid-range standards? 

 Are appropriate acceptance criteria documented for each type

of analysis conducted?

Are they known to the analysts working with

 respective instruments? 

3. Preventive Maintenance

Question Yes No Comment

 Is a maintenance record maintained for each major laboratory

 instrument?

Comment

4. Record Keeping

Question Yes No Comment

Does a chain-of-custody procedure exist for laboratory

samples?

If yes, indicate date, title and revision number where it can

be found.

 Are records kept for all analytical laboratory instruments?

 Do these records indicate:

analytical batches processed?

quality control data?

calibration data?

results of blanks, spikes and duplicates?
Question Yes No Comment

EISOPQAM H - 12 November 2001

initials of analyst?

Is there a record which indicates the checks made on: weights

 humidity indicators?

balances?

thermometer(s)?

 Are records maintained to track the preparation of filters for the

field?

Are they current? 

Do they indicate proper use of conditioning?

Weighing?

 Are records kept which track filters returning from the field for

analysis?

 How are data records from the laboratory archived?

 Where?

 How long are records kept? Years

5. Data Acquisition and Handling

Question Yes No Comment

Are QC data readily available to the analyst during a given

analytical run?

What is the laboratory’s capability with regard to data recovery? In case of problems, can they recapture data or are they dependent on computer

operations? Discuss briefly.

Has a users manual been prepared for the automated data

acquisition instrumentation?

Comment

 Is it in the analyst’s or user’s possession?

Is it current?
EISOPQAM H - 13 November 2001

6. Specific Pollutants: PM-10, PM 2.5 and Lead

Question Yes No Comment

PM10 and PM 2.5

Are filters supplied by EPA used at SLAMS sites?

Are filters visually inspected via strong light from a view box

for pinholes and other imperfections? 

If no, comment on way imperfections are determined?

Are unexposed filters equilibrated in controlled conditioning

environment which meets or exceeds the requirements of 40

CFR 50?

If no, why not?

Is the conditioning environment monitored? Indicate frequency

Are the monitors properly calibrated? Indicate frequency

Is the balance checked with Class “S” weights each day it is

used? 

If no, indicate frequency of such checks

Is the balance check information placed in QC logbook? If no, where is it recorded?

Is the filter weighed to the nearest milligram? If not, what mass increment

Are filter serial numbers and tare weights permanently

recorded?

If no, indicate where

Are filters packaged for protection while transporting to and

from the monitoring sites?

How often are filter samples collected? (Indicate average lapse time (hrs.) between end of sampling and laboratory receipt.)

Are exposed filters reconditioned for at least 24 hrs in the same

conditioning environment as for unexposed filters?

 If no, why not?

Are exposed filters removed from folders, etc., before

conditioning? 

Is the exposed filter weighed to the nearest milligram? 

Are exposed filters archived? Where?

 Indicate retention period

Are blank filters re-weighed? (PM2.5) If no, explain why not.

If yes, how frequently?

Are analyses performed on filters? Indicate analyses other than Pb and mass which are

routinely performed.

Are sample weights and collection data recorded?

LEAD

Is analysis for lead being conducted using atomic absorption

spectrometry with air acetylene flame?

If not, has the Agency received an equivalency designation

of their procedure?

Is either the hot acid or ultrasonic extraction procedure being

followed precisely?

Which?

Is Class A borosilicate glassware used throughout the analysis? 
Question Yes No Comment

EISOPQAM H - 14 November 2001

Is all glassware scrupulously cleaned with detergent, soaked

and rinsed three times with distilled-deionized water?

If not, briefly describe or attach procedure.

If extracted samples are stored, are linear polyethylene bottles

used? 

Are all batches of glass fiber filters tested for background lead

content?

At a rate of 20 to 30 random filters per batch of 500 or 

greater? 

Indicate rate

Are ACS reagent grade HNO3 and HCI used in the analysis? If not, indicate grade used

Is a calibration curve available having concentrations that cover

the linear absorption range of the atomic absorption

instrumentation? 

Is the stability of the calibration curve checked by alternately

remeasuring every 10th sample a concentration  1g Pb/ml; 

10 g Pb/ml?

If not, indicate frequency.

Are measured air volumes corrected to reference conditions as

given in CFR regulations (Qstd of 760 mm Hg and 25C) prior

to calculating the Pb concentration?

If not, indicate conditions routinely employed for both

internal and external reporting.

In either the hot or ultrasonic extraction procedure, is there

always a 30-min H2O soaking period to allow HNO3 trapped in

the filter to diffuse into the rinse water?

Is a quality control program in effect that includes periodic

quantification of (1) lead in 3/4" x 8" glass fiber filter strips

containing 100-300 g Pb/strip, and/or (2) a similar strip with 

 600-1000g strip, and (3) blank filter strips with zero Pb

content to determine if the method, as being used, has any bias? 

Comment on lead QC program or attach applicable SOP

Are blank Pb values subtracted from Pb samples assayed? If not, explain why
EISOPQAM H - 15 November 2001

D: DATA AND DATA MANAGEMENT

1. Data Handling

Question Yes No Comment

Is there a procedure, description, or a chart which shows a

complete data sequence from point of acquisition to point of

submission of data to EPA?

Are data handling and data reduction procedures documented?

For data from continuous analyzers?

For data from non-continuous methods? 

Is there documentation accompanying the data regarding any media changes, transcriptions, and/or flags which have been placed into the data

before data are released to agency internal data processing? Describe.

Have special data handling procedures been adopted for air

pollution episodes?

If yes, provide brief description

2. Software Documentation

Question Yes No Comment

Does the agency have available a copy of the AIRS Manual? 

Does the agency have the PARS user’s guide available?

Does the Data Management Section have complete software

documentation? 

If yes, indicate the implementation date and latest revision

dates for such documentation.

Are the computer system contents, including ambient air

monitoring data backed up regularly?

Briefly describe, indicating at least the media, frequency,

and backup-media storage location

What is the recovery capability (how much time and data would be lost) in the event of a significant computer problem?

3. Data Validation and Correction

Question Yes No Comment

Have validation criteria, applicable to all pollutant data

processed by the reporting organization been established and

documented? 

Does documentation exist on the identification and applicability

of flags (i.e., identification of suspect values) within the data as

recorded with the data in the computer files?
Question Yes No Comment

EISOPQAM H - 16 November 2001

Do documented data validation criteria address limits on and

for the following:

I. Operational parameters, such as flow rate

measurements or flow rate changes

 II. Calibration raw data, calibration validation and

calibration equipment tests.

 III. All special checks unique to a measurement system

IV. Tests for outliers in routine data as part of screening 

 process

V. Manual checks such as hand calculation of 

concentrations and their comparison with computer-calculated

data

Are changes to data submitted to NADB documented in a

 permanent file?

If no, why not?

Are changes performed according to a documented Standard

Operating Procedure or your Agency Quality Assurance Project

Plan?

 If not according to the QA Project Plan, please attach a

copy of your current Standard Operating Procedure

Who has signature authority for approving corrections?

 (Name) (Program Function)

Is the group supplying data provided an opportunity to review

data and correct erroneous entries?

If yes, how?

Are corrected data resubmitted to the issuing group for

cross-checking prior to release? 

4. Data Processing

Question Yes No Comment

Does the agency generate data summary reports?

 Are the data used for in-house distribution and use? 

Publication ? Other (specify)

Question Yes No Comment

Have special procedures been instituted for pollution index

reporting? 

.

Who at the agency has the responsibility for submitting data to AIRS?

Name Title

Are those persons different from the individuals who submit

data to PARS?
Question Yes No Comment

EISOPQAM H - 17 November 2001

 If yes, provide name and title of individual responsible for PARS data submittal.

 Name Title

How often are data submitted to: -

 AIRS ?

 PARS?

Does the agency routinely request a hard copy printout on

submitted data:

 from AIRS?

 from PARS?

Are records kept for at least 3 years by the agency in an orderly,

accessible form? 

 If yes, does this include raw data , calculation , QC

data , and reports ? If no, please comment.

Do field data include the following documentation:

 Site ID? 

Pollutant type?

Date received at the center? 

Collection data (flow, time date)?

Date of Laboratory Analysis /if applicable)

Operator/Analyst?

Are data reduction audits performed on a routine basis? If yes, at what frequency?

 

Are they done by an independent group?

Are precision and accuracy data checked each time they are

recorded, calculated or transcribed to ensure that incorrect

values are not submitted to EPA?

Is a final data processing check performed prior to submission

of any data?

 If no, explain

5. Internal Reporting

Question Yes No Comment

Does the agency prepare Precision and Accuracy summaries

other than Form 1?

 Do either the audit or precision reports indicated include a

discussion of corrective actions initiated based on audit or

precision results?
EISOPQAM H - 18 November 2001

Who has the responsibility for the calculation and preparation of data summaries? To whom are such P and A summaries delivered?

Name Title Type of Report Recipient

Identify the individual within the agency who receives the results of the agency’s participation in the NPAP and the internal distribution of the

results once received.

Principal Contact for NPAP is (name, title) 

6. External Reporting

What number of the SLAMS sites (by pollutant) reported less than 75% of the data (adjusted for seasonal monitoring and site start-ups and

terminations)?

Number of Sites <75% Data Recovery FY 

Pollutant 1st Quarter 2nd Quarter 3rd Quarter 4th Quarter 

Ozone

 Nitrogen Dioxide

Sulfur Dioxide

 Carbon Monoxide

PM-10

 Lead

Question Yes No Comment

Does the agency’s annual report (as required in 40 CFR 58.26)

include the following?

 Data summary required in Appendix F

 Annual precision and accuracy information described in 

Section 5.2 of Appendix A.

 Location, date, pollution source and duration of all episodes 

 reaching the significant harm levels.

 Certification by a senior officer in the State or his designee.

Please provide the dates at which the annual reports have been submitted for the last 2 years.
EISOPQAM H - 19 November 2001

E. QUALITY ASSURANCE/QUALITY CONTROL

1. Status of Quality Assurance Program

Question Yes No Comment

Does the agency have an EPA-approved quality assurance

program plan?

If yes, have changes to the plan been approved by the EPA?

Please provide: Date of Original Approval Date of Last Revision Date of Latest Approval

Do you have any revisions to your QA Program Plan still

 pending?

Is the QA Plan fully implemented?

Are copies of QA Plan or pertinent sections available to agency

personnel?

If no, why not?

Which individuals routinely receive updates to QA Plan?

2. Audits and Audit System Traceability

Question Yes No Comment

Does the agency maintain a separate audit/calibration support

facility laboratory?

Has the agency documented and implemented specific audit

procedures?

Have audit procedures been prepared in keeping with the

requirements of Appendix A to 40 CFR 58?

Do the procedures meet the specific requirements for

independent standards and the suggestions regarding

 personnel and equipment? 

Are SRM or CRM materials used to routinely certify audit

materials?

Does the agency routinely use NBS-SRM or CPM materials? For audits only? For calibrations only? For both? 

 For neither, secondary standards are employed 

Does the agency audit the Meteorological sites?

Please list below areas routinely covered by this review, the date of the last review, and changes made as a direct result of the review.

Pollutants Audit Method Audit Standard

 CO

 O3

NO2

 S02

PM-10

PM 2.5
EISOPQAM H - 20 November 2001

Question Yes No Comment

Are SRM or CRM materials used to establish traceability of

calibration and zero/span check materials provided to field

operations personnel? 

Specifically for gaseous standards, how is the traceability of

audit system standard materials established?

Are they: purchased certified by the vendor?

Certified by the QA support laboratory which is part of this

agency?

Are all agency traceability and standardization methods used

documented?

Do the traceability and standardization methods conform with

the guidance of VOL. Il of the Handbook for Air Pollution

Measurement Systems?

For permeation devices?

For cylinder gases?

Does the agency have identifiable auditing equipment

(specifically intended for sole use) for audits?

If yes, how is the equipment identified?

How often is auditing equipment certified for accuracy against

standards and equipment of higher authority?

3. National Performance Audit Program (NPAP) And Additional Audits

Identify the individual with primary responsibility for the required participation in the National Performance Audit Program.

For gaseous materials? (name, title)

For laboratory materials? (name, title)

Question Yes No Comment

Does the agency currently have in place any contracts or similar

agreements either with another agency or outside contractor to

perform any of the audits required by 40 CFR 58?

If yes, has the agency included QA requirements with this 

agreement?

 Is the agency adequately familiar with their QA program?

Date last systems audit was conducted Date: By Whom:

Question Yes No Comment

Does the agency participate in the National Performance Audit

Program (NPAP) as required under 40 CFR 58 Appendix A? 

If no, why not? Summarize below.
EISOPQAM H - 21 November 2001

Please complete the table below

 Parameter Audited Date of Last NPAP

SO2

CO

Pb

PM-10

O3

 NO2

4. Documentation and Data Processing Review

Question Yes No Comment

Does the agency periodically review its record-keeping

activities?

Question Yes No Comment

Are data audits (specific re-reductions of strip charts or similar

activities routinely performed for criteria pollutants data

reported by the agency?

If no, please explain.

Are procedures for such data audits documented? 

Are they consistent with the recommendations of Sections

16.4.2.3 of Vol. II of the QA Handbook for Air Pollution

Measurement Systems?

If no, why not?

What is the frequency and level (as a percentage of data processed of these audits?

Pollutant Audit Frequency Period of Data Audited % of Data Rechecked

Identify the criteria for acceptable/non-acceptable result from a data processing audit for each pollutant, as appropriate

Pollutant Acceptance Criteria Data Concentration Level
EISOPQAM H - 22 November 2001

Question Yes No Comment

Are procedures documented and implemented for corrective

actions based on results of data audits which fall outside the

established limits?

If yes, where are such corrective action procedures

documented?

5. Corrective Action System

Question Yes No Comment

Does the agency have a comprehensive Corrective Action

program in place and operational? 

Have the procedures been documented?

 As a part of the agency QA Plan?

As a separate Standard Operating Procedure?

How is responsibility for implementing corrective actions on the basis of audits, calibration problems, zero/span checks, etc assigned? Briefly

discuss.

How does the agency follow up on implemented corrective actions?

6. Audit Result Acceptance Criteria

Question Yes No Comment

Has the agency established and has it documented criteria to

define agency-acceptable audit results?

Question Yes No Comment

Were these audit criteria based on, or derived from, the

guidance found in Vol./. Il of the QA Handbook for Air

Pollution Measurement System, Section 2.0.12? 

If no, please explain.

If yes, please explain any changes or assumptions made in

the derivation.

What corrective action may be taken if criteria are exceeded?

As a goal, the 95 percent probability limits for precision (all pollutants) should be less than +/- 15 percent. At 95 percent probability limits, the

accuracy for PM10 should be less than +/- 15% and all other pollutants should be less than +/- 20 percent. Using a short narrative and a summary

table, compare the reporting organizations performance against these goals over the last year. Explain any deviations.