TECHNOLOGICALLY ENHANCED

NATURALLY OCCURRING

RADIOACTIVE MATERIALS (TENORM)

STUDY REPORT

Rev. 0

January 2015

Prepared for:

Pennsylvania Department of Environmental Protection

Rachel Carson State Office Building

400 Market Street 

Harrisburg, PA 17101

Prepared by:

Perma-Fix Environmental Services, Inc.

325 Beaver Street, Suite 3

Beaver, PA 15009
TECHNOLOGICALLY ENHANCED

NATURALLY OCCURRING

RADIOACTIVE MATERIALS (TENORM)

STUDY REPORT

Rev. 0

January 2015

Prepared for:

Pennsylvania Department of Environmental Protection

Rachel Carson State Office Building

400 Market Street 

Harrisburg, PA 17101

Prepared by:

Perma-Fix Environmental Services, Inc.

325 Beaver Street, Suite 3

Beaver, PA 15009
PA DEP TENORM Study Report – Table of Contents Rev. 0

January 2015 iii

TABLE OF CONTENTS

LIST OF APPENDICES................................................................................................................ vi

LIST OF FIGURES ...................................................................................................................... vii

LIST OF TABLES....................................................................................................................... viii

ABBREVIATIONS, ACRONYMS, AND SYMBOLS ................................................................ xi

GLOSSARY ................................................................................................................................ xiv

0.0 SYNOPSIS...................................................................................................................... .0-1

1.0 INTRODUCTION ........................................................................................................... 1-1

1.1 Purpose and Objectives of the Study ................................................................... 1-1

1.2 Background.......................................................................................................... 1-1

1.3 Pennsylvania Oil and Gas Operations (Conventional and Unconventional)....... 1-3

1.4 Subject Media ...................................................................................................... 1-5

1.4.1 Media Sampled ........................................................................................ 1-5

1.5 Facility Selection ................................................................................................. 1-8

1.5.1 Well Site Selection................................................................................... 1-8

1.5.2 Wastewater Treatment Plant Selection .................................................... 1-8

1.5.3 Landfill Facility Selection Criteria .......................................................... 1-8

1.5.4 Gas Distribution and End Use Operations Selection Criteria.................. 1-8

1.5.5 Road Sites Selection Criteria ................................................................... 1-9

1.5.6 Well Component Reconditioning Selection Criteria ............................... 1-9

1.5.7 Centralized Impoundments...................................................................... 1-9

2.0 STUDY IMPLEMENTATION ....................................................................................... 2-1

2.1 Sampling and Survey Methods............................................................................ 2-1

2.1.1 Field Surveys ........................................................................................... 2-1

2.1.2 Field Sampling Activities ........................................................................ 2-3

2.2 Laboratory Methods............................................................................................. 2-5

2.2.1 Solid Matrix ............................................................................................. 2-5

2.2.2 Liquid Matrix........................................................................................... 2-6

2.2.3 Gas Matrix ............................................................................................... 2-8

2.2.4 Filter Matrix – Smears............................................................................. 2-8

2.3 Survey and Sample Analyses Data Management ................................................ 2-8

2.3.1 Limitations on Gamma Spectroscopy Results......................................... 2-9

2.3.2 Radium-226 Quantification by Gamma Spectroscopy ............................ 2-9

2.3.3 Criteria for Comparison to Analytical Analyses Results....................... 2-10

2.3.4 Normal Background Radioactivity Values............................................ 2-10

2.3.5 Data Presentation ................................................................................... 2-10

3.0 WELL SITES................................................................................................................... 3-1

3.1 Radiological Survey Results................................................................................ 3-1

3.1.1 Removable Alpha/Beta Surface Radioactivity Measurement Results..... 3-1

3.1.2 Total Alpha/Beta Surface Radioactivity Measurement Results............... 3-2

3.1.3 Gross Gamma Radiation Scan Results .................................................... 3-2

3.1.4 Gamma Radiation Exposure Rate Results............................................... 3-2
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3.2 Solid Sample Results........................................................................................... 3-3

3.2.1 Vertical Phase Drill Cuttings................................................................... 3-3

3.2.2 Horizontal Phase Drill Cuttings............................................................... 3-4

3.2.3 Drilling Mud ............................................................................................ 3-6

3.2.4 Hydraulic Fracturing Proppant Sand ....................................................... 3-6

3.2.5 Flowback Solids....................................................................................... 3-7

3.3 Liquid Sample Results......................................................................................... 3-7

3.3.1 Drilling Liquid (Mud).............................................................................. 3-7

3.3.2 Hydraulic Fracturing Fluid ...................................................................... 3-7

3.3.3 Flowback Fluid ........................................................................................ 3-7

3.3.4 Produced Water........................................................................................ 3-8

3.4 Radon Sample Results ......................................................................................... 3-8

3.4.1 Ambient Air Samples During Flowback.................................................. 3-8

3.4.2 Production Gas Radon ............................................................................. 3-8

3.5 Well Site Worker Exposure Assessment ............................................................. 3-8

3.5.1 External Gamma Exposure .................................................................... 3-10

3.5.2 Internal Alpha/Beta Exposure................................................................ 3-10

3.5.3 Internal Radon Exposure........................................................................ 3-10

3.6 Well Site Data Assessments............................................................................... 3-10

3.6.1 Comparison of Different Geological Formations Based on X-Ray 

Fluorescence Data.................................................................................. 3-10

3.6.2 Filtered Versus Unfiltered Sample Data Evaluation.............................. 3-11

3.6.3 Conventional Versus Unconventional Produced Water Data 

Evaluation .............................................................................................. 3-11

3.7 Potential Off-site Environmental Impact........................................................... 3-11

4.0 WASTEWATER TREATMENT PLANTS .................................................................... 4-1

4.1 Publicly Owned Treatment Works....................................................................... 4-1

4.1.1 Radiological Survey Results.................................................................... 4-1

4.1.2 Solid Sample Results............................................................................... 4-2

4.1.3 Liquid Sample Results............................................................................. 4-3

4.1.4 Indoor Radon Sampling Results .............................................................. 4-3

4.1.5 POTW Data Comparisons........................................................................ 4-3

4.1.6 POTW Worker Exposure Assessment..................................................... 4-4

4.1.7 POTW Radiological Environmental Impacts .......................................... 4-5

4.2 Centralized Wastewater Treatment Plants........................................................... 4-5

4.2.1 Survey Results ......................................................................................... 4-5

4.2.2 Solid Sample Results............................................................................... 4-6

4.2.3 Liquid Samples ........................................................................................ 4-7

4.2.4 Indoor Radon Sampling Results .............................................................. 4-7

4.2.5 Filtered Versus Unfiltered Sample Data Evaluation................................ 4-8

4.2.6 CWT Exposure Assessment..................................................................... 4-8

4.2.7 CWT Radiological Environmental Impacts............................................. 4-9

4.3 Zero Liquid Discharge Plants .............................................................................. 4-9

4.3.1 Survey Results ......................................................................................... 4-9

4.3.2 Solid Sample Results............................................................................. 4-10

4.3.3 Liquid Samples ...................................................................................... 4-10

4.3.4 Indoor Radon Sampling Results ............................................................ 4-11
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January 2015 v

4.3.5 Filtered Versus Unfiltered Sample Data Evaluation.............................. 4-11

4.3.6 ZLD Worker Exposure Assessment....................................................... 4-11

4.3.7 Alpha Spectroscopy Analysis of Filter Cake ......................................... 4-14

5.0 LANDFILLS.................................................................................................................... 5-1

5.1 Leachate ............................................................................................................... 5-1

5.2 Nine Selected Landfills........................................................................................ 5-1

5.2.1 Influent and Effluent Leachate................................................................. 5-1

5.2.2 Leachate Filter Cake ................................................................................ 5-2

5.2.3 Effluent Discharge Sediment-Impacted Soil ........................................... 5-2

5.2.4 Ambient Air ............................................................................................. 5-2

5.2.5 Surveys..................................................................................................... 5-2

5.3 Radon Ingrowth Within Filter Cake From WWTP to Landfills.......................... 5-3

5.4 Landfill Worker Exposure Assessment ............................................................... 5-5

5.4.1 Landfill External Radiation Exposure ..................................................... 5-5

6.0 GAS DISTRIBUTION AND END USE ......................................................................... 6-1

6.1 Natural Gas in Underground Storage................................................................... 6-1

6.2 Natural Gas-Fired Power Plants........................................................................... 6-1

6.3 Compressor Stations ............................................................................................ 6-2

6.4 Natural Gas Processing Plant............................................................................... 6-2

6.5 Potential Exposure from Gas Scale Inside Pipes and Equipment........................ 6-3

6.6 Radon Dosimetry ................................................................................................. 6-4

7.0 OIL AND GAS BRINE-TREATED ROADS ................................................................. 7-1

7.1 Gamma Radioactivity Survey Results................................................................. 7-1

7.1.1 Gross Gamma Radiation Scan Results .................................................... 7-1

7.1.2 Gamma Radiation Exposure Rate Results Summary............................... 7-2

7.2 Soil Sample Results............................................................................................. 7-2

7.2.1 Road Surface Soils Biased Sample Results............................................. 7-2

7.2.2 Road Surface Soils – Reference Background Roads Soils...................... 7-3

7.3 Public Exposure to Oil and Gas Brine-Treated Roads......................................... 7-4

8.0 QUALITY ASSURANCE AND QUALITY CONTROL............................................... 8-1

8.1 Data Quality Levels (DQLs)................................................................................ 8-1

8.2 Quality Control Parameters.................................................................................. 8-1

8.3 Field Screening .................................................................................................... 8-1

8.4 Sample Identification ........................................................................................... 8-2

8.5 Sample Custody ................................................................................................... 8-2

8.6 Analytical Procedures.......................................................................................... 8-2

8.7 Instrument Calibrations........................................................................................ 8-2

8.8 Data Evaluation and Validation........................................................................... 8-2

8.8.1 Validation of Field Data........................................................................... 8-3

8.8.2 Validation of Laboratory Data ................................................................. 8-3

8.9 Data Reporting – Analytical Laboratory.............................................................. 8-3

8.9.1 DQL III Reporting ................................................................................... 8-4
PA DEP TENORM Study Report – Table of Contents Rev. 0

January 2015 vi

8.10 Quality Control Procedures.................................................................................. 8-4

8.10.1 Field QC Checks...................................................................................... 8-4

8.10.2 Internal Laboratory QC Checks............................................................... 8-5

8.11 Laboratory Performance Audits........................................................................... 8-5

8.12 Laboratory System Audits ................................................................................... 8-6

8.13 Assessment Procedures for Data Acceptability ................................................... 8-6

8.13.1 Precision................................................................................................... 8-6

8.13.2 Accuracy .................................................................................................. 8-6

8.13.3 Completeness........................................................................................... 8-6

8.13.4 Quality Control Charts............................................................................. 8-7

8.14 Preventative Maintenance.................................................................................... 8-7

8.14.1 Field Equipment....................................................................................... 8-7

8.14.2 Laboratory Instruments............................................................................ 8-7

8.15 QA Reports to Management ................................................................................ 8-8

8.16 Third-Party Quality Control................................................................................. 8-8

9.0 OBSERVATIONS AND RECOMMENDATIONS........................................................ 9-1

9.1 Observations ........................................................................................................ 9-1

9.1.1 Well Sites (Section 3.0) ........................................................................... 9-1

9.1.2 Wastewater Treatment Plants (Section 4.0)............................................. 9-3

9.1.3 Landfills (Section 5.0) ............................................................................. 9-8

9.1.4 Gas Distribution and End Use (Section 6.0)............................................ 9-9

9.1.5 Oil and Gas Brine-Treated Roads (Section 7.0) .................................... 9-11

9.2 Recommendations for Future Actions............................................................... 9-12

9.2.1 Well Sites............................................................................................... 9-12

9.2.2 Wastewater Treatment Plants ................................................................ 9-13

9.2.3 Landfills................................................................................................. 9-13

9.2.4 Gas Distribution and End Use................................................................ 9-13

9.2.5 Oil and Gas Brine-Treated Roads.......................................................... 9-13

10.0 REFERENCES .............................................................................................................. 10-1

LIST OF APPENDICES

Appendix A: Additional Geological Information

Appendix B: Field Instrumentation QC Documentation

Appendix C: Gamma Spectroscopy Analytical Results

Appendix D: Total and Removable Alpha/Beta Surface Radioactivity Results

Appendix E: Gross Gamma Radiation Survey Figures

Appendix F: XRF Analytical Analyses Results

Appendix G: T-test Output Files

Appendix H: Radon Monitor/Sample Analytical Analyses Reports

Appendix I: Filtered Versus Unfiltered Liquid Sample Comparison

Appendix J: MicroShield® Output Files

Appendix K: Laboratory Data Reports

Appendix L: Peer Review Comment and Resolution Document
PA DEP TENORM Study Report – List of Figures Rev. 0

January 2015 vii

LIST OF FIGURES

1-1. Marcellus Shale Formation in Pennsylvania.................................................................... 1-2

1-2. Marcellus Shale Formation “Wet” and “Dry” Areas....................................................... 1-2

1-3. Uranium-238 Decay Chain .............................................................................................. 1-4

1-4. Thorium-232 Decay Chain .............................................................................................. 1-4

1-5. Natural Gas Operations.................................................................................................... 1-7

3-1. Comparison of Ra-226 Gamma Spectroscopy Results to U-238 XRF Results in 

Vertical Drill Cuttings...................................................................................................... 3-4

3-2. Comparison of Ra-228 Gamma Spectroscopy Results to Th-232 XRF Results in 

Vertical Drill Cuttings...................................................................................................... 3-4

3-3. Comparison of Analytical Analyses Results for Horizontal and Vertical Drill Cutting 

Samples............................................................................................................................ 3-5

3-4. Comparison of Ra-226 Gamma Spectroscopy Results to U-238 XRF Results in 

Horizontal Drill Cuttings ................................................................................................. 3-5

3-5. Comparison of Ra-228 Gamma Spectroscopy Results to Th-232 XRF Results in 

Horizontal Drill Cuttings ................................................................................................. 3-6

3-6. Natural Gas Radon Sampling Location ........................................................................... 3-9

3-7. Conventional vs Unconventional Produced Water Radium Concentrations................. 3-11

4-1. CWT Influent and Effluent Liquid Ra-226 Minimum, Maximum, and Average............ 4-7

4-2. ZLD Influent and Effluent Liquid Ra-226 Minimum, Maximum, and Average........... 4-11

4-3. MicroShield®External Exposure Scenarios Input/Output............................................. 4-13

5-1. Ra-226 Progeny Ingrowth (Days Post Removal) versus Exposure Rate from 

13.34 pCi/g Ra-226.......................................................................................................... 5-4

5-2. Ra-226 Progeny Ingrowth versus Days (Days Post Removal)........................................ 5-5
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January 2015 viii

LIST OF TABLES

2-1. Theoretical Overestimation of Ra-226 Activity in Solid Samples with Natural 

Uranium Analyzed by Gamma Spectroscopy ........................................................... 2-11

2-2. Criteria for Comparison............................................................................................. 2-12

2-3. Natural Background Radioactivity Values for U.S. Soil........................................... 2-14

3-1. Removable Alpha and Beta Surface Radioactivity Measurement Results 

Summary ................................................................................................................... 3-13

3-2. Total Alpha and Beta Surface Radioactivity Measurement Results Summary......... 3-16

3-3. Gross Gamma Scan Results Summary...................................................................... 3-19

3-4. Results Summary of NaI Count Rate Data Converted to Exposure Rates................ 3-20

3-5. Vertical Solids, Drill Cuttings – Gamma Spectroscopy Results............................... 3-21

3-6. XRF Uranium and Thorium for Vertical Cuttings.................................................... 3-22

3-7. Horizontal Solids, Drill Cuttings – Uranium Series Gamma Spectroscopy 

Results....................................................................................................................... 3-24

3-8. XRF Uranium and Thorium for Horizontal Cuttings................................................ 3-25

3-9. Drilling Solids, Mud – Gamma Spectroscopy Results.............................................. 3-26

3-10. Proppant Sand – Gamma Spectroscopy Results........................................................ 3-26

3-11. Flowback Solids, Sand – Gamma Spectroscopy Results.......................................... 3-27

3-12. Drilling Fluids – Gamma Spectroscopy and Miscellaneous Results ........................ 3-27

3-13. Fracturing Fluids – Gamma Spectroscopy and Miscellaneous Results .................... 3-28

3-14. Flowback Fluids – Gamma Spectroscopy and Miscellaneous Results ..................... 3-28

3-15. Unfiltered Produced Waters – Gamma Spectroscopy and Miscellaneous Results ... 3-29

3-16. Filtered Produced Waters – Gamma Spectroscopy and Miscellaneous Results ....... 3-29

3-17. Ambient Radon at Well Sites During Flowback ....................................................... 3-30

3-18. Natural Gas Samples from Production Sites............................................................. 3-31

3-19. Thorium and Uranium XRF Data for Drill Cuttings By Formation.......................... 3-32

4-1. POTW-I Removable Alpha and Beta Surface Radioactivity Measurement Results 

Summary ................................................................................................................... 4-15

4-2. POTW-I Total Alpha and Beta Surface Radioactivity Measurement Results 

Summary ................................................................................................................... 4-17

4-3. POTW-I Gross Gamma Radiation Scan Results Summary ...................................... 4-19

4-4. POTW-I Results Summary of NaI Count Rate Data Converted to Exposure 

Rates.......................................................................................................................... 4-19

4-5. POTW-I Filter Cake Results Summary – Gamma Spectroscopy Results................. 4-20

4-6. POTW-N Filter Cake Results Summary – Gamma Spectroscopy Results............... 4-21

4-7. POTW-I Sediment Sample Results Summary – Gamma Spectroscopy Results....... 4-21

4-8. POTW-I Filtered Effluent Results Summary – Gamma Spectroscopy and 

Miscellaneous Results............................................................................................... 4-22

4-9. POTW-I Unfiltered Effluent Results Summary – Gamma Spectroscopy and 

Miscellaneous Results............................................................................................... 4-23

4-10. POTW-N Filtered Effluent Results Summary – Gamma Spectroscopy and 

Miscellaneous Results............................................................................................... 4-24

4-11. POTW-N Unfiltered Effluent Results Summary – Gamma Spectroscopy and 

Miscellaneous Results............................................................................................... 4-24

4-12. POTW-I Filtered Influent Results Summary – Gamma Spectroscopy and 

Miscellaneous Results............................................................................................... 4-25
PA DEP TENORM Study Report – List of Tables Rev. 0

January 2015 ix

4-13. POTW-I Unfiltered Influent Results Summary – Gamma Spectroscopy and 

Miscellaneous Results............................................................................................... 4-26

4-14. POTW-N Filtered Influent Results Summary – Gamma Spectroscopy and 

Miscellaneous Results............................................................................................... 4-27

4-15. POTW-N Unfiltered Influent Results Summary – Gamma Spectroscopy and 

Miscellaneous Results............................................................................................... 4-27

4-16. POTW-I Ambient Radon........................................................................................... 4-28

4-17. POTW-I vs POTW-N Average Concentrations Comparison for Filtered ................ 4-28

4-18. POTW-I vs POTW-N Average Concentrations Comparison for Unfiltered ............ 4-28

4-19. Average Radium, Gross Alpha, and Gross Beta Concentrations for Filtered

Influent and Effluent POTW Samples....................................................................... 4-29

4-20. Average Radium, Gross Alpha, and Gross Beta Concentrations for Unfiltered 

Influent and Effluent POTW Samples....................................................................... 4-29

4-21. POTW-I Sediment and Effluent Results for Ra-226 and Ra-228 ............................. 4-30

4-22. POTW Sediment and Effluent Ratios for Ra-226/Ra-228 ........................................ 4-31

4-23. Summary of Removable Alpha and Beta Surface Contamination Results at CWT 

Plants......................................................................................................................... 4-32

4-24. Summary of Total Alpha and Beta Surface Contamination Results at CWT 

Plants......................................................................................................................... 4-34

4-25. Summary of NaI Count Rate Data at CWTs............................................................. 4-36

4-26. Results Summary of NaI Count Rate Data Converted to Exposure Rates................ 4-37

4-27. CWT Solids, Filter Cake – Gamma Spectroscopy Results....................................... 4-38

4-28. CWT Solids, Sediment – Gamma Spectroscopy Results.......................................... 4-39

4-29. CWT Solids, Biased Soil – Gamma Spectroscopy Results....................................... 4-39

4-30. CWT Filtered Effluent – Gamma Spectroscopy and Miscellaneous Results............ 4-40

4-31. CWT Unfiltered Effluent – Gamma Spectroscopy and Miscellaneous Results........ 4-41

4-32. CWT Filtered Influent – Gamma Spectroscopy and Miscellaneous Results............ 4-42

4-33. CWT Unfiltered Influent – Gamma Spectroscopy and Miscellaneous Results........ 4-43

4-34. CWT Radon Sample Results..................................................................................... 4-44

4-35. Summary of Removable Alpha and Beta Surface Contamination Results at 

ZLDs.......................................................................................................................... 4-45

4-36. Summary of Total Alpha and Beta Surface Contamination Results at ZLDs........... 4-47

4-37. Summary of NaI Count Rate Data at ZLDs.............................................................. 4-49

4-38. Results Summary of NaI Count Rate Data Converted to Exposure Rates................ 4-50

4-39. ZLD Solids, Filter Cake – Gamma Spectroscopy Results ........................................ 4-51

4-40. ZLD Solids, Biased Soil – Uranium Series Gamma Spectroscopy Results.............. 4-51

4-41. ZLD Filtered Effluent – Gamma Spectroscopy and Miscellaneous Results............. 4-52

4-42. ZLD Unfiltered Effluent – Gamma Spectroscopy and Miscellaneous Results......... 4-53

4-43. ZLD Filtered Influent – Gamma Spectroscopy and Miscellaneous Results............. 4-54

4-44. ZLD Unfiltered Influent – Gamma Spectroscopy and Miscellaneous Results ......... 4-55

4-45. ZLD Radon in Ambient Air Results.......................................................................... 4-56

4-46. ZLD and CWT Filter Cake Sample Alpha Spectroscopy Results............................. 4-56

5-1. Landfill Leachate – Gamma Spectroscopy and Miscellaneous Results...................... 5-7

5-2. Selected Landfill Leachate – Gamma Spectroscopy and Miscellaneous Results....... 5-8

5-3. Landfill Leachate Original and Aqueous Sample Analysis Results............................ 5-9

5-4. Selected Landfill Effluent Leachate  Gamma Spectroscopy and Miscellaneous 

Results....................................................................................................................... 5-10
PA DEP TENORM Study Report – List of Tables Rev. 0

January 2015 x

5-5. Selected Landfill Influent Leachate – Gamma Spectroscopy and Miscellaneous 

Results....................................................................................................................... 5-10

5-6. Selected Landfill Solids, Filter Cake  Gamma Spectroscopy Results .................... 5-11

5-7. Selected Landfill Solids, Sediment  Gamma Spectroscopy Results....................... 5-11

5-8. Selected Landfill Radon Concentrations................................................................... 5-12

5-9. Selected Landfill Removable Alpha and Beta Surface Radioactivity Results 

Summary ................................................................................................................... 5-13

5-10. Selected Landfill Total Alpha and Beta Surface Radioactivity Results Summary ... 5-14

5-11. Selected Landfill Gross Gamma Radiation Scan Results Summary......................... 5-15

5-12. Results Summary of NaI Count Rate Data Converted to Exposure Rates................ 5-15

5-13. Gamma Spectroscopy Results (pCi/g) of Sealed Wastewater Treatment Sludge 

Sample Over 24 Days................................................................................................ 5-16

6-1. Natural Gas Underground Storage Radon Concentrations, Injection ......................... 6-6

6-2. Natural Gas Underground Storage Radon Concentrations, Withdrawal..................... 6-6

6-3. Natural Gas-Fired Power Plant Samples Analyzed for Radon Content...................... 6-6

6-4. Natural Gas-Fired Power Plants Ambient Fence Line Radon Monitors (PP 02)........ 6-7

6-5. Compressor Station Radon Samples ........................................................................... 6-7

6-6. Compressor Station Ambient Fence Line Radon Monitors (CS 01)........................... 6-7

6-7. Natural Gas Processing Plant Radon Samples............................................................ 6-7

6-8. Compressor Station and Natural Gas Processing Plant Filter Case Removable 

Radioactivity Results................................................................................................... 6-8

6-9. Compressor and Natural Gas Processing Plant Filter Media, Gamma 

Spectroscopy ............................................................................................................... 6-8

6-10. Natural Gas Processing Plant Filter Media, Gross Alpha/Gross Beta ........................ 6-8

6-11. Radon Dosimetry Values for a Typical Home ............................................................ 6-9

7-1. Gamma Scan Survey Summary................................................................................... 7-5

7-2. Summary of NaI Gamma Count Rate Data Converted to Exposure Rate................... 7-7

7-3. Road-Biased Soil – Uranium Series Gamma Spectroscopy Results......................... 7-10

7-4. Road-Biased Soil – Thorium Series Gamma Spectroscopy Results......................... 7-11

7-5. Road-Biased Soil – Actinium Series and Miscellaneous Gamma Spectroscopy 

Results....................................................................................................................... 7-12

7-6. Reference Background Road – Uranium Series Gamma Spectroscopy Results....... 7-13

7-7. Reference Background Road – Thorium Series Gamma Spectroscopy Results....... 7-14

7-8. Reference Background Road – Actinium Series and Miscellaneous Gamma 

Spectroscopy Results................................................................................................. 7-15

7-9. Dose Assessment Results for Oil and Gas Brine-Treated Roads.............................. 7-15

8-1. Summary of Analytical Procedures........................................................................... 8-10

8-2. Bi-214 Split Solid Sample Comparison Results........................................................ 8-11

8-3. Pb-212 Split Solid Sample Comparison Results....................................................... 8-12

8-4. Pb-214 Split Soil Sample Comparison Results......................................................... 8-12

8-5. Ra-226 Split Soil Sample Comparison Results......................................................... 8-13

8-6. Bi-214 Split Liquid Sample Comparison Results ..................................................... 8-13

8-7. Pb-214 Split Liquid Sample Comparison Results..................................................... 8-14

8-8. Ra-226 Split Liquid Sample Comparison Results..................................................... 8-14

8-9. Ra-228 Split Liquid Sample Comparison Results..................................................... 8-15
PA DEP TENORM Study Report – Abbreviations, Acronyms, and Symbols Rev. 0

January 2015 xi

ABBREVIATIONS, ACRONYMS, AND SYMBOLS

Ac Actinium

ALARA As Low As Reasonably Achievable

 Alpha

ANSI American National Standards Institute

API American Petroleum Institute

ATD Alpha Track Detector

Ba Barium

Bcf billion cubic feet

 Beta

Bi Bismuth

BRP Bureau of Radiation Protection

CERCLA Comprehensive Environmental Response, Compensation, and Liability Act

CFR Code of Federal Regulations

CLP Contract Laboratory Program

cm centimeter

cpm counts per minute

CWT Centralized Wastewater Treatment

DAC Derived Air Concentration

DCNR Department of Conservation and Natural Resources

DEP Department of Environmental Protection

DEP Laboratory DEP Bureau of Laboratories

DER Duplicate Error Ratio

DOE U.S. Department of Energy

DOT U.S. Department of Transportation

dpm disintegrations per minute

DQL Data Quality Level

EIC Electret Ion Chamber

EPA U.S. Environmental Protection Agency

Fe Iron

FSP Field Sampling Plan

ft foot/feet

ft2square foot

ft3cubic foot

g gram

GIS Geographic Information System

GM Geiger-Muller

GIS Geographic Information Systems

GPS Global Positioning System

HASL Health and Safety Laboratory

HCl Hydrochloric Acid

HDPE High Density Polyethylene

HNO3 Nitric Acid

HPS Health Physics Society

hr hour

K Potassium

keV kilo-electron volt
PA DEP TENORM Study Report – Abbreviations, Acronyms, and Symbols Rev. 0

January 2015 xii

L liter

LLD Lower Level of Detection

μR/hr microroentgens per hour

μrem/hr microroentgen equivalent man per hour

mcf thousand cubic feet

MDC Minimum Detectable Concentration

mph miles per hour

mrem millirem

MS Matrix Spike

MSD Matrix Spike Duplicate

NaI Sodium Iodide

NELAP National Environmental Laboratory Accreditation Program

NIST National Institute of Standards and Technology

NJDEP New Jersey Department of Environmental Protection

NORM Naturally Occurring Radioactive Material

NPDES National Pollutant Discharge Elimination System

NRC U.S. Nuclear Regulatory Commission

O&G Oil and Gas

OSHA Occupational Safety and Health Administration

%R Percent Recovery

± plus or minus

Pa Protactinium

PA Pennsylvania

Pa. C.S. Consolidated Statutes

PASDA Pennsylvania Spatial Data Access

Pb Lead

pCi/g picocuries per gram

Perma-Fix Perma-Fix Environmental Services, Inc.

pH Potential Hydrogen

Po Polonium

POTW Publicly Owned Treatment Works

PPE Personal Protective Equipment

ppm parts per million

PSIA pounds per square inch absolute

QA Quality Assurance

QAM Quality Assurance Manual

QAPP Quality Assurance Project Plan

QC Quality Control

Ra Radium

RESRAD Residual Radiation

RG Regulatory Guide

Rn Radon

RPD Relative Percent Difference

SOP Standard Operating Procedure

Sv Sievert

TDS Total Dissolved Solids

TENORM Technologically Enhanced Naturally Occurring Radioactive Materials

Th Thorium
PA DEP TENORM Study Report – Abbreviations, Acronyms, and Symbols Rev. 0

January 2015 xiii

Tl Thallium

U Uranium

UNSCEAR United Nations Scientific Committee on the Effects of Atomic Radiation

U.S. United States

USACE U.S. Army Corps of Engineers

U.S.C. United States Code

USGS U.S. Geological Survey

WL Working Level

WWTP Wastewater Treatment Plant

XRF X-ray Fluorescence

yr year

ZLD Zero Liquid Discharge
PA DEP TENORM Study Report – Glossary Rev. 0

January 2015 xiv

GLOSSARY*

Alpha – A positively charged particle consisting of two protons and two neutrons, emitted in 

radioactive decay or nuclear fission. They are generally produced in the process of alpha decay 

but may also be produced in other ways. They are designated by the Greek letter α.

Basic Sediment – Oil and gas production storage impurities/sediment from produced oil at 

storage tank battery. 

Beta – High-energy, high-speed electrons or positrons emitted by certain types of radioactive 

nuclei. The beta particles emitted are a form of ionizing radiation also known as beta rays. The 

production of beta particles is termed beta decay. They are designated by the Greek letter β.

Brine – Water that is produced with oil and gas when a well is in production, typically water 

containing more dissolved inorganic salt than seawater.

Condensate – A low density, high American Petroleum Institute (API) gravity, mixture of 

hydrocarbons that is present in a gaseous state at formation temperatures and pressures but 

condenses out of the raw gas to a liquid form at standard temperature of 60 degrees Fahrenheit 

and pressure 14.7 pounds per square inch (PSIA). 

Conventional Formation – A formation that is not an unconventional formation. 

Conventional Well – A bore hole drilled or being drilled for the purpose of or to be used for 

construction of a well regulated under 58 Pa. C. S. § § 3201—3274 (relating to development) 

that is not an unconventional well, irrespective of technology or design. The term includes, but 

is not limited to:

 Wells drilled to produce oil.

 Wells drilled to produce natural gas from formations other than shale formations.

 Wells drilled to produce natural gas from shale formations located above the base of the Elk 

Group or its stratigraphic equivalent.

 Wells drilled to produce natural gas from shale formations located below the base of the Elk 

Group where natural gas can be produced at economic flow rates or in economic volumes 

without the use of vertical or nonvertical well bores stimulated by hydraulic fracture 

treatments or multilateral well bores or other techniques to expose more of the formation to 

the well bore.

 Irrespective of formation, wells drilled for collateral purposes, such as monitoring, geologic 

logging, secondary and tertiary recovery, or disposal injection.

Drill Cuttings – Rock cuttings and related mineral residues generated during the drilling of an 

oil or gas well. 

Drilling Fluid Waste – Oil and gas drilling mud and other drilling fluids (other than fracturing 

fluid and spent lubricant). 

Drilling Mud – A chemical, water-based, or oil-based mixture pumped into an oil well during 

drilling in order to seal off porous rock layers, equalize the pressure, cool the bit, and flush out 
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the cuttings. The mud is circulated down the drill pipe, out through the drill bit, across the rock 

face being drilled, then back to the surface carrying debris from the bottom of the well.

Flowback – The return flow of water and formation fluids recovered from the well bore of an oil 

or gas well following the release of pressures induced as part of the hydraulic fracture 

stimulation of a target geologic formation until the well is placed into production.

Flowback Fluid – Flowback fluid is a water based solution that flows back to the surface during 

and after the completion of hydraulic fracturing. It consists of the fluid used to fracture the target 

formation. The fluid contains clays, chemical additives, dissolved metal ions, and total dissolved 

solids (TDS).

Flowback Fracturing Sand – Oil and gas drilling flowback fracturing sand. 

Fracturing Fluid Waste – Oil and gas fracturing/stimulation fluid waste and/or flowback. 

Gamma – Electromagnetic radiation of an extremely high frequency and high energy. Gamma 

rays are ionizing radiation, and are thus biologically hazardous. They are classically produced 

by the decay of atomic nuclei as they transition from a high energy state to a lower state known 

as gamma decay, but may also be produced by other processes. Natural sources of gamma rays 

include gamma decay from naturally occurring radioisotopes, and secondary radiation from 

atmospheric interactions with cosmic ray particles. They are designated by the Greek letter .

Gas – A fluid, combustible or noncombustible, which is produced in a natural state from the 

earth and maintains a gaseous or rarified state at standard temperature of 60 degrees Fahrenheit 

and pressure of 14.7 PSIA. This product type must be reported in Mcf (1,000 cubic feet) at a 

standard temperature of 60 degrees Fahrenheit and pressure of 14.7 PSIA. 

Horizontal Drill Cuttings – Drill cuttings from the horizontal portion of an oil or gas well.

Hydraulic Fracturing Fluid – Hydraulically pressurized liquid used to fracture rock in the 

hydraulic fracturing process. Hydraulic fracturing fluids are used to initiate and/or expand 

fractures, as well as to transport proppant into fractures. The U.S. O&G industry has used fluids 

for fracturing geologic formations since the early 1940s.

Leachate – A solution resulting from water that has percolated through solid, e.g., waste in 

landfill, and potentially leached out some of the soluble constituents.

Marinelli – A lightweight polypropylene sample container with snap-on lid used for gamma 

spectroscopy analysis.

Natural Gas – A fossil fuel consisting of a mixture of hydrocarbon gases, primarily methane, 

and possibly including ethane, propane, butane, pentane, carbon dioxide, oxygen, nitrogen, and 

hydrogen sulfide and other gas species. The term includes natural gas from oil fields known as 

associated gas or casing head gas, natural gas fields known as nonassociated gas, coal beds, shale 

beds, and other formations. The term does not include coal bed methane.
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NORM – Naturally occurring radioactive material. It is a nuclide that is radioactive in its 

natural physical state, not man-made, but does not include source or special nuclear material.

Oil – Hydrocarbons in liquid form at formation temperatures and pressures that remain in liquid 

form at standard temperature of 60 degrees Fahrenheit and pressure 14.7 PSIA. 

Produced Water – Water that is produced with oil and gas when the well is in production.

Proppant Sand – Solid treated sand suspended in water or other fluid designed to keep an 

induced hydraulic fracture open during or following a fracturing treatment.

Radiological Environmental Impact – Impact to the environment from the release and 

subsequent spreading of radionuclides and from the direct emission of radiation from facilities.

Removable Contamination – The fraction of total surface alpha/beta radioactive contamination 

easily removed by pressing a 47-mm diameter filter paper to the surface with moderate pressure,

i.e., smear sampling. Usually expressed in units of dpm/100 cm

2

of surface area sampled.

Secular Equilibrium – A type of radioactive equilibrium in which the half-life of the precursor 

(parent) radionuclide is so much longer than that of the product (progeny) radionuclide(s) that 

the radioactivity of the progeny become equal to the parent over time equal to approximately 

10 half-life’s of the progeny.

Servicing Fluid – Oil and gas production well maintenance and work-over fluids and/or 

oil/water-based mud and foam. 

Smear Sample – A sample of removable alpha and beta surface radioactivity collected by 

pressing a 47-mm diameter filter paper to 100 cm2of surface area sampled to obtain an assumed 

fraction of removable material. The filter paper is counted for alpha and beta radioactivity 

without any preparation.

Spent Lubricant – Oil and gas drilling and/or plug drilling lubricants that have exceeded their 

useful life.

Student t-test – A test for determining whether or not an observed sample mean differs 

significantly from a hypothetical normal population mean.

TENORM – Technologically enhanced naturally occurring radioactive materials. It is naturally 

occurring radioactive material not specifically subject to regulation under the laws of the 

Commonwealth of Pennsylvania or Atomic Energy Act of 1954 (42 U.S.C. §2011 et seq.), but 

whose radionuclide concentrations or potential for human exposure have been increased above 

levels encountered in the undisturbed natural environment by human activities.

Total Contamination – The surface alpha/beta radioactive contamination comprised of fixed 

and removable components. Total contamination is measured by placing an appropriate 

alpha/beta detector on the surface to be surveyed so that both the fixed and removable fractions 

are counted together. Usually expressed in units of dpm/100 cm

2

of surface area surveyed.
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Unconventional Formation – A geological shale formation existing below the base of the Elk 

Sandstone or its geologic equivalent stratigraphic interval where natural gas generally cannot be 

produced at economic flow rates or in economic volumes except by vertical or horizontal well 

bores stimulated by hydraulic fracture treatments or by using multilateral wellbores or other 

techniques to expose more of the formation to the well bore.

Unconventional Well – A bore hole drilled or being drilled for the purpose of or to be used for 

the production of natural gas from an unconventional formation.

Vertical Drill Cuttings – Drill cuttings from the vertical portion of an oil or gas well.

Well Site – The area occupied by the equipment or facilities necessary for or incidental to the 

drilling, production, or plugging of a well.

*These definitions are for the purposes of this report only and are not necessarily regulatory definitions.
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0.0 SYNOPSIS

In 2013, the Pennsylvania Department of Environmental Protection (DEP) initiated a study to 

collect data relating to technologically enhanced naturally occurring radioactive material 

(TENORM) associated with oil and gas (O&G) operations in Pennsylvania. This study included 

the assessment of potential worker and public radiation exposure, TENORM disposal, and other 

possible environmental impacts. The study encompassed radiological surveys at well sites, 

wastewater treatment plants, landfills, gas distribution and end use, and O&G brine-treated 

roads. The media sampled included solids, liquids, natural gas, ambient air, and surface 

radioactivity.

The observations and recommendations for future actions based on this peer-reviewed study are:

1. There is little potential for additional radon exposure to the public due to the use of natural 

gas extracted from geologic formations located in Pennsylvania.

2. There is little or limited potential for radiation exposure to workers and the public from the 

development, completion, production, transmission, processing, storage, and end use of 

natural gas. There are, however, potential radiological environmental impacts from O&G

fluids if spilled. Radium should be added to the Pennsylvania spill protocol to ensure 

cleanups are adequately characterized. There are also site-specific circumstances and 

situations where the use of personal protective equipment by workers or other controls 

should be evaluated.

3. There is little potential for radiation exposure to workers and the public at facilities that treat 

O&G wastes. However, there are potential radiological environmental impacts that should 

be studied at all facilities in Pennsylvania that treat O&G wastes to determine if any areas 

require remediation. If elevated radiological impacts are found, the development of 

radiological discharge limitations and spill policies should be considered.

4. There is little potential for radiation exposure to workers and the public from landfills 

receiving waste from the O&G industry. However, filter cake from facilities treating O&G 

wastes are a potential radiological environmental impact if spilled, and there is also a 

potential long-term disposal issue. TENORM disposal protocols should be reviewed to 

ensure the safety of long-term disposal of waste containing TENORM.

5. While limited potential was found for radiation exposure to recreationists using roads treated 

with brine from conventional natural gas wells, further study of radiological environmental 

impacts from the use of brine from the O&G industry for dust suppression and road 

stabilization should be conducted.
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1.0 INTRODUCTION

1.1 Purpose and Objectives of the Study

During the expansion of the Marcellus Shale Gas industry the Pennsylvania Department of 

Environmental Protection (DEP) staff observed a steady increase in the volume of waste 

containing technologically enhanced naturally occurring radioactive material (TENORM), 

generated by the oil and gas (O&G) industry, being disposed in Pennsylvania landfills.

TENORM is naturally occurring radioactive material whose radionuclide concentrations or 

potential for human exposure have been increased above levels encountered in the undisturbed 

natural environment by human activities.

In 2013, DEP initiated a study to collect information and data needed to effectively manage

TENORM from O&G operations for environmental and health protection. This study included 

the assessment of potential worker and public radiation exposure, evaluation of potential impacts

from TENORM waste disposal, and the investigation of possible radiological environmental 

effects. The survey and sample data will be used to address potential radiological concerns from 

O&G operations, disposal of waste, and product use.

This study report includes recommendations for future actions to be taken to address issues of 

concern identified by the study, including additional investigations and surveys.

1.2 Background

The Marcellus Shale formation underlies much of Pennsylvania, with the exception of 

southeastern Pennsylvania. The organic-rich portion reaches its maximum thickness in the 

northeastern part of the state. The northwestern borders of Franklin, Cumberland, Lebanon, 

Berks, Lehigh, and Northampton counties provide the southeastern margin of the Marcellus 

Shale formation. Between this border and the approximate corridor with US 220/I 99, the 

Marcellus Shale formation crops out in the folded Ridge and Valley physiographic province 

where it may be a concern for indoor Radon (Rn). The type of gas found in most areas of the 

Marcellus Shale throughout Pennsylvania is geologically mature and consists of mostly methane 

that requires little processing prior to use. This gas is commonly called “dry gas.” Marcellus 

Shale gas found along the westernmost border of Pennsylvania is less geologically mature; 

therefore, in addition to methane, the gas contains additional hydrocarbons such as ethane, 

propane, and butane. This gas is commonly called “wet gas” and can be used to produce plastics 

and other high-value petroleum-based products. Figure 1-1 depicts the extent of the Marcellus 

Shale formation within Pennsylvania. Figure 1-2 shows the approximate dividing line between 

the wet and dry gas zones in the state.

The Pennsylvania Department of Conservation and Natural Resources (DCNR) has documented 

that Marcellus Shale can contain from 10 to 100 parts per million (ppm) uranium (U). Typical 

crustal U concentrations in the United States (U.S.) average 3 ppm.

See Appendix A for additional geologic information on other natural gas-producing formations 

and on heavy metal content.
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Figure 1-1. Marcellus Shale Formation in Pennsylvania

Figure 1-2. Marcellus Shale Formation “Wet” and “Dry” Areas

Source: PSU Marcellus Center for Outreach and Research (MCOR), www.marcellus.psu.edu
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Marcellus Shale and other geologic formations rich in O&G resources may contain naturally 

occurring radioactive material (NORM), specifically U, U-238 parent and thorium (Th), Th-232 

parent, and their decay progeny, as well as Potassium-40 (K-40). These series occur naturally 

and are the most prevalent of the three natural decay series, the third being the actinium (Ac), 

U-235 parent. The decay series of U and Th are illustrated in Figures 1-3 and 1-4, respectively.

Surface soil typically contains approximately 1 to 2 picocuries per gram (pCi/g) of both the U

and Th series radionuclides with all of the series members at approximately equal activity, i.e.,

secular equilibrium. The radioactive materials, including TENORM, are brought to the land 

surface by O&G activities.

Each of the natural decay series includes a Rn gas member. Radon and its progeny are the 

primary issue of concern associated with natural gas distribution and its end uses.

1.3 Pennsylvania Oil and Gas Operations (Conventional and Unconventional)

Natural gas wells are classified as either conventional or unconventional. Related statutory and 

regulatory definitions include the following:

Pennsylvania’s 2012 Oil and Gas Act (58 Pa. C. S. § 2301)

“Unconventional formation." A geological shale formation existing below the base of the Elk 

Sandstone or its geologic equivalent stratigraphic interval where natural gas generally cannot be 

produced at economic flow rates or in economic volumes except by vertical or horizontal well 

bores stimulated by hydraulic fracture treatments or by using multilateral wellbores or other 

techniques to expose more of the formation to the well bore.

"Unconventional gas well." A bore hole drilled or being drilled for the purpose of or to be used 

for the production of natural gas from an unconventional formation.

25 Pa. Code § 78.1

“Conventional formation.” A formation that is not an unconventional formation. 

“Conventional well.”

(i) A bore hole drilled or being drilled for the purpose of or to be used for construction of 

a well regulated under 58 Pa. C. S. §§ 3201—3274 (relating to development) that is 

not an unconventional well, irrespective of technology or design.

(ii) The term includes, but is not limited to:

(A) Wells drilled to produce oil.

(B) Wells drilled to produce natural gas from formations other than shale formations.

(C) Wells drilled to produce natural gas from shale formations located above the 

base of the Elk Group or its stratigraphic equivalent.
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Figure 1-3. Uranium-238 Decay Chain

Note: y = years, d= days, h = hours, and m = minutes

Figure 1-4. Thorium-232 Decay Chain

Note: y = years, d= days, h = hours, and m = minutes
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(D) Wells drilled to produce natural gas from shale formations located below the 

base of the Elk Group where natural gas can be produced at economic flow rates 

or in economic volumes without the use of vertical or nonvertical well bores 

stimulated by hydraulic fracture treatments or multilateral well bores or other 

techniques to expose more of the formation to the well bore.

(E) Irrespective of formation, wells drilled for collateral purposes, such as 

monitoring, geologic logging, secondary and tertiary recovery, or disposal 

injection.

1.4 Subject Media

The types of media evaluated as part of this study result from the product media that either 

contain TENORM or may be impacted by TENORM due to O&G operations. The product 

streams evaluated are natural gas and natural gas liquids, i.e., condensates. Other media 

evaluated includes solid and liquid wastes, soils, ambient air, and gaseous emission products 

associated with O&G operations.

1.4.1 Media Sampled

1.4.1.1 Solids

Natural gas exploration, extraction and production result in various types of solids that may 

contain TENORM or may be impacted by TENORM. These materials include drill cuttings, 

filter sock residuals, impoundment sludge, tank bottom sludge, pipe scale, wastewater treatment 

plant (WWTP) sludge, and soils. Drill cuttings are wastes brought to the surface during the 

drilling process. Filter sock residuals and WWTP sludge are generated during the processing of 

wastewaters generated by O&G activities. Impoundment and tank bottom sludge accumulates as 

a result of solid material settling out of well site wastewater.

Other solids potentially impacted by radioactive isotopes include soils at WWTP discharge 

outfalls, soils in the proximity of dirt roads where brines from conventional O&G operations are 

used for dust suppression, and pipe scale on natural gas transmission infrastructure.

1.4.1.2 Liquids

There are various types of liquids generated during the development and operating life of a gas 

well including drilling muds, used hydraulic fracturing fluid, brine, and other wastewaters.

Liquid wastes are processed at WWTPs for reuse on well sites or to meet National Pollutant 

Discharge Elimination System (NPDES) criteria prior to discharge to waters of the 

Commonwealth.

The study classified WWTPs into three categories:

1) Publicly Owned Treatment Works (POTWs) are the most common type of WWTPs. These 

facilities are designed to process sewage and wastewater from residences and businesses and 

may take industrial wastewater under specific circumstances. After the wastewater is 
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processed and meets specified chemical criteria, the processed water may be discharged to 

streams under an NPDES permit.

2) Centralized Waste Treatment (CWT) facilities are designed to process commercial and 

industrial liquid wastes prior to discharge to receiving streams under an NPDES permit. 

Additionally, there are some industrial facilities that process wastewater prior to discharge to 

POTWs for final processing and discharge (pre-treatment).

3) Zero Liquid Discharge (ZLD) facilities are the most modern and utilize distillation and 

chemical technologies to remove solids from the wastewater. The processed wastewater is 

returned for reuse at natural gas well sites for hydraulic fracturing of new wells. All 

centralized ZLD facilities that recycle water to be used for hydraulic fracturing must be 

permitted by DEP.

Landfill leachate is liquid waste generated by the movement of precipitation through the 

disposed waste and by the compaction and decomposition of the waste itself. As liquid moves 

through the waste, contaminants are leached from the disposed material. Landfills are designed 

to ensure leachate does not enter the groundwater and is collected for treatment. Upon meeting 

NPDES water quality standards, the treated leachate may be discharged to surface waters. Some 

landfills operate onsite treatment systems while others are connected to local POTWs, which 

treat landfill leachate prior to discharge. Because landfills accept natural gas industry wastes 

such as drill cuttings and treatment sludge that may contain TENORM, there is a potential for 

leachate from those facilities to also contain TENORM.

1.4.1.3 Natural Gas

Many facilities, structures, and systems are utilized during the exploration, extraction, and 

production of natural gas before the product is distributed to the residential, industrial, and 

commercial end users.

Natural gas samples were collected and evaluated for Rn at compressor stations, natural gas 

processing plants, and underground storage facilities. Ambient air samples were also collected 

and evaluated for Rn at well sites, WWTPs, gathering compressor stations, natural gas-fired 

power plants, and landfills.

Natural gas passes through gathering lines, compressor stations, transmission lines, natural gas 

processing plants, underground storage facilities, and a network of pipes and valves (see 

Figure 1-5).

Gathering Compressor Stations:

Gathering compressor stations compress the natural gas from the well sites to transport the 

product to the transmission line network. These facilities include large internal combustion 

engines and may also include dewatering equipment such as glycol dehydrators and liquid 

storage tanks. Geographically, they are typically located at a nexus of piping from well sites.
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Figure 1-5. Natural Gas Operations

Source: US EPA, http://www.epa.gov/methane/gasstar/basic-information/index.html

Natural Gas Processing:

Natural gas and condensate are also used as feedstock for the synthesis of other products.

Natural gas enters a processing facility and undergoes a dehydration process, is refrigerated to 

remove condensable liquids, then goes through a series of other processes including deethanizing/de-propinizing and fractionation. These facilities can be quite large with very

extensive piping networks. They also have several intermediate and final product storage tanks 

and vessels. The operations at these facilities necessitate opening of the product conveyance 

network for periodic cleaning and maintenance.

Transmission Line Compressor Stations:

These facilities are larger than their gathering station counterparts. Power to the compressors is 

supplied by natural gas turbine engines, similar to those found on jet aircraft. These facilities 

normally do not have dehydrating equipment or liquid storage tanks. Dehydration and 

condensate removal take place further upstream at the well sites and gathering compressor 

stations. The origin of the natural gas passing through these facilities can be difficult to 

ascertain. Transmission line compressor stations may be handling natural gas from 

Pennsylvania, other parts of the U.S., or international sources.

Underground Storage Facilities:

Some deep sandstone formations, such as the Oriskany Sandstone formation, are used for storing 

natural gas. These underground reservoirs are used to address fluctuations in demand for natural 

gas.
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End Users:

The primary radionuclide of concern in natural gas is Rn-222. Radon is a noble gas and is not 

destroyed by combustion, nor is it removed by an air emission source control device.

Consequently, Rn present in the fuel gas will remain after combustion. However, the process of 

combustion dilutes the concentration of Rn in the exhaust gas stream by a ratio of 10:1 of 

ambient air to natural gas when perfect combustion is achieved.

1.5 Facility Selection

Category-specific criteria were used to select specific facilities for inclusion in the study. The 

criteria differed based on the type of facility. The following lists the various selections.

1.5.1 Well Site Selection

1) A Marcellus Shale formation well site from the dry gas areas predominantly in the northern 

and central parts of the state.

2) A Marcellus Shale formation well site from the wet gas area found predominantly in the 

southwestern part of the state.

3) A Utica formation well site and other non-Marcellus Shale formations, e.g., Geneseo, Burket,

and Rhinestreet that became available.

4) A conventional O&G well site.

1.5.2 Wastewater Treatment Plant Selection

1) The three types of WWTPs, including POTW facilities, CWT facilities, ZLD facilities.

2) WWTPs that accept wastewater from conventional and unconventional types of well sites.

3) WWTPs that accept waste material from unconventional well sites in the wet gas-producing

area rather than the dry gas-producing area.

4) WWTPs where elevated radioactivity readings have been measured from the intake 

wastewater, produced sludge, effluent discharge, or discharge point stream/river sediments,

etc.

5) WWTPs that DEP regional offices have indicated are of particular interest.

1.5.3 Landfill Facility Selection Criteria

1) All Pennsylvania landfills.

2) Nine landfills that accepted the largest amount of TENORM-containing waste during the past 

year.

3) Large-volume TENORM-containing waste disposal sites where onsite worker exposure 

measurements could be obtained and representative samples of solids could be collected.

1.5.4 Gas Distribution and End Use Operations Selection Criteria

1) Facilities that compress, carry, and distribute natural gas from the wet gas-producing area of 

the state.

2) Facilities that compress, carry, and distribute natural gas from the dry gas-producing area of 

the state.
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3) Facilities that distribute or process natural gas produced in Pennsylvania rather than those 

that distribute or process natural gas from out of state.

4) Major natural gas users, e.g., electrical generator, processing, and storage facilities.

1.5.5 Road Sites Selection Criteria

1) Multiple locations in the southwestern, northwestern, and north-central regions of the state.

2) Roads where liquids from wells in the wet and dry gas-producing areas were applied for dust 

suppression and road stabilization.

3) Roads where liquids from wells in the wet and dry gas-producing areas were not applied for 

dust suppression and road stabilization.

1.5.6 Well Component Reconditioning Selection Criteria

Well casing/pipe reconditioning or de-scaling facilities in the state.

1.5.7 Centralized Impoundments

1) A facility in the wet gas-producing area.

2) A facility in the dry gas-producing area.
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2.0 STUDY IMPLEMENTATION

2.1 Sampling and Survey Methods

The primary data for this study were gathered using radiological screening surveys and through 

the sampling and analysis of solid and liquid wastes, soils, ambient air, and gaseous emission 

products associated with O&G operations.

2.1.1 Field Surveys

2.1.1.1 Scope

Radiological surveys were performed to identify the possible presence and abundance of NORM 

and TENORM in locations that include the following:

 Well Sites (Section 3.0)

 Offices and living quarters

 Storage and maintenance areas

 Drill rigs and associated equipment

 Temporary wastewater storage tanks

 Wastewater impoundments

 Production equipment

 Drill cutting pits (closed)

 Wastewater Treatment Plants (Section 4.0)

 Wastewater off-load areas

 Influent wastewater storage areas (untreated)

 Effluent wastewater storage areas (treated)

 Processing tanks and equipment

 Offices, break rooms, laboratories

 Discharge points where applicable

 Landfills (nine study landfills – details provided in Section 5.0)

 Offices and other occupied spaces

 Storage and maintenance areas

 Natural gas processing facilities

 Leachate processing facilities

 Earthmoving equipment

 Gas Distribution and End Use (Section 6.0)

 Compressor stations

 Natural gas-fired power plants

 Natural gas processing facilities

 Oil and Gas Brine-Treated Roads (Section 7.0)

2.1.1.2 Instrumentation and Documentation

Radiological instrumentation used for field surveys included portable scalers/ratemeters with 

various scintillators for detection of alpha (, beta ( and/or gamma radiation; portable gamma 
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dose rate meters; portable gamma exposure rate meters; general purpose Geiger-Muller (GM)

detectors; and field counters for low-level  and  radiation detection.

All instruments used were calibrated and their operation verified prior to use on each day they 

were used. The instruments were maintained and operated in accordance with Perma-Fix

Environmental Services, Inc. (Perma-Fix) operating procedures by qualified health physics 

technicians. Records of calibration, daily quality control (QC) checks for the days used, survey 

results, logbooks, and various other records generated during field screening survey activities are 

included in Appendix B.

2.1.1.3 Activities

General descriptions of the various field surveys performed as part of this study are provided 

below.

2.1.1.3.1 Radiological Surveys of Facilities and Reference Background Areas

Gamma radiation exposure rates and gross gamma radioactivity surveys were performed at each 

facility included in the study. The gamma radiation exposure rates were measured using a

Bicron Micro-Rem Meter recorded in micro-Roentgen equivalent man per hour (μrem/hr) or a 

Ludlum Model 19 Micro-R Meter recorded in units of micro-Roentgen per hour (μR/hr). The 

gross gamma radioactivity surveys were recorded in counts per minute (cpm) using a Ludlum 

Model 44-10 Sodium Iodide (NaI) detector. To properly evaluate survey data, surveys were also 

performed in areas outside the influence of the facility to establish natural background.

2.1.1.3.2 Radiological Surveys of Liquid Samples and Tanks

Liquid samples were collected at each of the three types of WWTPs and included influent, 

effluent, and in-stream discharge points where POTWs, and in limited cases CWTs, are 

permitted to discharge directly to a receiving stream.

During liquid sampling, gamma radiation exposure surveys were performed. In addition, gamma 

radiation exposure rates were performed on contact with tanks when possible. Otherwise, 

measurements were collected in the general proximity of the point of sample collection or tank.

To properly evaluate survey data, surveys were also performed in areas outside the influence of 

the facility to establish natural background.

2.1.1.3.3 Radiological Surveys of Equipment and Structures

Equipment such as drill rigs, well development equipment, etc., was subject to field screening 

surveys including:

 Gamma radiation exposure rate surveys using a Bicron MicroRem Meter or Ludlum Model 

19.

 Gross gamma radioactivity surveys using a Ludlum Model 44-10 NaI detector.

 Total  and  surface radioactivity using a direct frisk Ludlum Model 43-89 detector and/or a 

Ludlum Model 44-93 and cpm results converted to units of disintegrations per minute per 

100 square centimeters (dpm/100 cm

2

) of surface area surveyed.
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 Removable  and  surface radioactivity by sample collection with smears. Smears were 

counted on a Ludlum 2929 with a Model 43-10-1 portable scaler/ratemeter and detector.

Count results were converted to units of dpm/100 cm2of surface area smeared. 

To properly evaluate survey data, surveys were also performed in areas outside the influence of 

the facility to establish natural background.

2.1.1.3.4 Radiological Surveys of Samples

All samples collected were surveyed prior to transportation to the laboratory. The surveys were 

performed on contact with the sample container and included:

 Gamma radiation exposure rate surveys using a Bicron MicroRem Meter or Ludlum Model 

19.

 Gross gamma radioactivity surveys using a Ludlum Model 44-10 NaI detector.

 Total  and  surface radioactivity using a direct frisk Ludlum Model 43-89 detector or a 

Ludlum Model 44-93 detector.

 Removable  and  surface radioactivity by sample collection with smears. Smears were 

counted on a Ludlum 2929 with a Model 43-10-1 portable scaler/ratemeter and detector.

To properly evaluate survey data, surveys were also performed in areas outside the influence of 

the facility to determine natural background.

2.1.2 Field Sampling Activities

2.1.2.1 Scope

DEP sampled solids, liquids, and gas during the study to understand the movement and potential 

exposure pathways of TENORM from O&G operations. The sampling and analysis of 

environmental media provides data that are informative in determining radionuclides of concern 

as well as their potential mobility. The media sampled during this study included:

 Solid samples:

− Drill cuttings

− Wastewater treatment sludge/filter cake

− Wastewater treatment discharge sediment

− Soil samples

− Filter sock residuals

 Liquid samples:

− Flowback and produced water

− Accumulated liquids from production equipment

− Wastewater treatment influent and effluent

− Landfill leachate influent and effluent

 Gas samples:

− Natural gas (for Rn-222 concentration)

− Ambient air (for Rn-222 concentration)

 Removable / radioactivity surface samples:

− Removable  radioactivity by smear sampling
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− Removable  radioactivity by smear sampling

Collected samples, with the exception of smear samples, were transported to the DEP Bureau of 

Laboratories (DEP Laboratory) under chain-of-custody control. Five percent of samples were 

split by Perma-Fix and forwarded by the DEP Laboratory to the independent QC laboratory 

(GEL Laboratory of Charleston, SC) for filtration, as needed, and analyses. Smear samples were 

transported to the Perma-Fix laboratory, and 10 percent of the smear samples were forwarded to 

the DEP Laboratory for duplicate analysis.

2.1.2.2 Solid Sample Methods

Solid samples were collected using clean sampling equipment. Samples were collected using 

stainless steel trowels and bowls, then promptly transferred into laboratory-approved containers 

and immediately labeled to maintain identification.

2.1.2.3 Liquid Sample Methods

When sampling tanks through a valve, samples were collected directly into the clean sample 

container. Otherwise, representative tank samples were collected using a clean high-density 

polyethylene (HDPE) dipper. The sampled liquids were transferred to clean, laboratoryapproved containers. Two consecutive 4-liter (L) samples were obtained at each sample 

location.

When the samples were received at the DEP Laboratory, they were preserved. Sample 

preservation is the measure or measures taken to prevent reduction or loss of target analytes.

Analyte loss can occur between sample collection and laboratory analysis because of physical, 

chemical, and biological processes that result in chemical precipitation, adsorption, oxidation, 

reduction, ion exchange, degassing, or degradation. Preservation stabilizes analyte 

concentrations for a limited period of time. The first sample was analyzed after preservation

without filtration. The second sample was preserved and subsequently filtered in the laboratory 

using a 0.45-micron mixed cellulose ester filter. The filtered sample was placed into a clean

container. The filtrates were maintained for analysis.

2.1.2.4 Gas Sample Methods

Radon concentration in ambient air was measured by various technologies. The technology used 

was dependent on several factors, including the location, the collection period/detector 

deployment period, and atmospheric conditions such as relative humidity. Sampling 

technologies used for this study included:

 Electret ion chambers (EICs)

 Alpha track detectors (ATDs)

Natural gas grab samples were also collected to measure Rn concentrations. Natural gas was 

collected directly into scintillation cells, referred to as Lucas cells. Two Lucas cells were 

connected in sequence, which provided a duplicate sample at each sample location. An in-line

Millipore®Type HA, 0.45-micron glass fiber filter was used prior to natural gas entering the first 

cell. This filter prevents sample contamination by Rn particulate progeny.
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The natural gas was flowed through the cells for 10 minutes. This provided for purging of the 

gas lines and the scintillation cells, resulting in the collection of new discrete samples for 

analysis.

2.1.2.5 Removable Alpha/Beta Surface Radioactivity Smear Sample Method

Smear samples of removable  and  surface radioactivity were collected by pressing a 

47-millimeter diameter filter paper to the sampling surface and smearing with moderate pressure 

approximately 100 cm2of surface area.

2.2 Laboratory Methods

2.2.1 Solid Matrix

The following sample types were classified as solid matrices: surface soil impacted by 

sediments, filter cakes, soils, sludge, drill cuttings, drilling muds, proppant sand, and filter socks,

including the materials inside the socks. Upon arrival at the DEP Laboratory, the samples were 

scanned for radiological activity using a GM pancake probe. The samples were logged with the 

appropriate standard analysis code that designated the requested radiological analyses.

2.2.1.1 Gamma Spectroscopy

The samples were dried in a Presier Scientific Model 91-2290-83 100°C oven, ground to a fine 

powder (~80 mesh), weighed into a new 0.5-L Marinelli, sealed with general purpose 

polyethylene tape, and analyzed by high purity germanium gamma spectroscopy. The following 

radionuclides were identified or inferred using gamma spectroscopy:

Ra-226 Direct Energy Line 186 keV

Ra-228 Inferred Energy Line 911 keV (Ac-228)

U-235 Direct Energy Line 143 keV

Ac-228 Direct Energy Line 911 keV

Th-232 Inferred Energy Line 911 keV (Ac-228)

U-238 Inferred Energy Line 63.3 keV (Th-234)

Pb-212 Direct Energy Line 238 keV

Pb-214 Direct Energy Line 351 keV

Bi-212 Direct Energy Line 727 keV

Bi-214 Direct Energy Line 609 keV

K-40 Direct Energy Line 1,460 keV

The sample was counted again using gamma spectroscopy after a minimum of 21 days from the 

first analysis date. The same radionuclides were identified or inferred. Prior to the start of 

analysis, a daily background and instrument QC check was completed, reviewed, and validated.

The gamma spectroscopy reference method is U.S. Department of Energy (DOE) 4.5.2.3.

2.2.1.2 X-ray Fluorescence

After gamma spectroscopy analyses were complete, the dried solid samples were analyzed for 

various elements using X-ray fluorescence (XRF). The samples were weighed into XRF sample 
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cups, covered with a Prolene®film, and analyzed using an X-ray spectrometer. Forty-eight

elements were analyzed using XRF. The XRF analyses were conducted using a DEP 

Laboratory-developed method. Standard QC calibration verification instrument checks were 

performed using National Institute of Standards and Technology (NIST) primary traceable

standards.

2.2.1.3 Alpha Spectroscopy

One percent of solid samples analyzed by gamma spectroscopy were selected and analyzed using

alpha spectroscopy for U-238, U-235, U-234, Th-232, Th-230, and Th-228. Prior to analysis, the 

samples were digested using Health and Environmental Chemistry: Analytical Techniques, Data 

Management, and Quality Assurance ER200 and ER230 sample preparation methods. A 

10-gram (g) aliquot of the original solid sample matrix was digested and diluted to a final 

volume of 4 L, resulting in a concentration of 2.5 g/L. The isotopes and iron (Fe) carrier added 

were precipitated from the liquid as hydroxides, re-solubilized in hydrochloric acid (HCl), and 

then passed over a column of anion exchange resin, which removed the Fe and other interfering

isotopes. Each isotopic fraction was concentrated, converted to the nitrate salt, and applied to a 

second anion exchange column. After washing the resin, the isotope was eluted, 

electrodeposited, and analyzed for isotopic U and Th. Instrument background, secondary, and 

pulser counts were obtained at the beginning and end of every sample batch. The alpha 

spectroscopy reference method is Standard Methods 7500-U C.

2.2.2 Liquid Matrix

The following sample types received at the DEP Laboratory were classified as liquid matrices:

 WWTP influent and effluent liquids

 Landfill leachates

 Well site liquids/fluids including:

 Hydraulic fracturing fluid

 Flowback fluid

 Produced water

Based on solid content, a portion of the drilling mud samples were analyzed as liquids. Upon 

arrival at the DEP Laboratory, the samples were scanned for radiological activity using a GM

pancake probe. The samples were preserved with nitric acid (HNO3) to a potential hydrogen 

(pH) less than 2 and logged with the appropriate standard analysis code that designates the 

requested radiological analyses. After being acidified, samples were maintained a minimum of 

16 hours prior to analysis. Samples were vacuum filtered using a 0.45-micron mixed cellulose 

ester filter. The filtrate was collected and transferred into a clean gallon cubitainer. The filtered 

solids were analyzed for gamma-emitting radionuclides using gamma spectroscopy (see solid 

matrix). The liquid samples were counted for gross -, gross -, and gamma-emitting 

radionuclides.
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2.2.2.1 Gamma Spectroscopy

The liquid samples were measured to 3 L, placed into a clean 4-L Marinelli, sealed with general 

purpose polyethylene tape, and analyzed. The following radionuclides were identified or 

inferred using gamma spectroscopy:

Ra-226 Direct Energy Line 186 keV

Ra-228 Inferred Energy Line 911 keV (Ac-228)

U-235 Direct Energy Line 143 keV

Ac-228 Direct Energy Line 911 keV

Th-232 Inferred Energy Line 911 keV (Ac-228)

U-238 Inferred Energy Line 63.3 keV (Th-234)

Pb-212 Direct Energy Line 238 keV

Pb-214 Direct Energy Line 351 keV

Bi-212 Direct Energy Line 727 keV

Bi-214 Direct Energy Line 609 keV

K-40 Direct Energy Line 1,460 keV

The samples were counted again using gamma spectroscopy after a minimum of 21 days from 

the date of their first analysis. The same radionuclides were identified or inferred each day 

analyses were performed. Prior to the start of analysis, a background and standard QC 

calibration verification check was completed, reviewed, and validated.

2.2.2.2 Gross Alpha Gross Beta Analyses

An aliquot of sample was evaporated to less than 5 milliliters. The evaporated volume was

transferred to a 2-inch diameter planchet using 10 percent HNO3 and dried. The dried sample 

was placed in a desiccator for 72 hours. The samples were flamed to convert the hydroscopic 

salts to oxides. The samples were counted for gross - and gross -emitting radionuclides using

a gas proportional counter. Standard QC calibration verification and daily background checks

were completed, reviewed, and validated at the beginning and end of analysis. The gross  and 

gross  reference method is EPA 900.0.

2.2.2.3 X-Ray Fluorescence

The liquid samples were analyzed for various metals using XRF. The samples were weighed 

into XRF sample cups, covered with a Prolene®film, and analyzed using an X-ray spectrometer.

Forty-eight elements were identified using XRF. The XRF analyses were conducted using a 

DEP Laboratory-developed method. Standard QC calibration verification instrument checks

were performed using NIST primary traceable standards.

2.2.2.4 Inorganic Analyses

During the third round of sampling, additional analyses including basic inorganic analyses were 

included as part of the study. The samples were received by the DEP Laboratory and logged 

with the appropriate standard analysis code that designated the requested inorganic analyses.

The analyses included hardness (SM2340 B), pH (SM4500H-B), specific conductance at 25.0°C
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(SM2510B), total chloride (SM4500-CL E), total sulfate (EPA 375.2), total dissolved solids at

180°C (USGS I-1750), and total suspended solids (USGS I-3765).

2.2.3 Gas Matrix

Natural gas samples were collected at various locations using scintillation cells with 

photomultiplier tubes and analyzed for Rn concentration. The scintillation cells were counted in 

one of two counters: the Pylon AB-5 Portable Radiation Monitor or the Ludlum Model 2200 

Scaler-Ratemeter. The counter used was dependent upon the type of scintillation cell used to 

collect the sample. All samples were allowed to equilibrate for a minimum of four hours before 

being counted. In all cases, the first count was not used in the calculations to allow for “dark 

adaptation” of the instruments. The next three counts were each individually calculated and the 

average and standard deviation calculated. The average result, plus or minus (±) two standard 

deviations, and the minimum detectable activity are reported in the data tables.

Natural gas is composed mostly of methane, which is lighter and less dense than air. Alpha 

counting efficiency is directly proportional to the density of the gas counted. Because the 

scintillation cells were calibrated using a known concentration of Rn in ambient air, density 

correction was applied to all Rn in natural gas results. A correction factor (Jenkins et al., 2014) 

was used for this effect to prevent biasing the results. The final calculated Rn concentrations

were divided by 1.054. This reduced all results by five percent to correct for the bias.

2.2.4 Filter Matrix – Smears

All smear samples were collected by Perma-Fix technicians and transported to the Perma-Fix 

Laboratory for analysis. All smear samples were counted for gross  and gross  radioactivity.

Ten percent of those smear samples were then forwarded to the DEP Laboratory for duplicate 

analysis as a QC measure.

Upon arrival at the Perma-Fix laboratory, the samples were logged. The smear samples were 

placed on a 2-inch diameter planchet and analyzed for gross  and gross  particles using a 

Ludlum Model 2929 Meter equipped with a Ludlum Model 43-10-1 Smear Counter (zinc-sulfide 

scintillation detector). A standard QC background and calibration verification count was

performed each day the smear counter was used.

Upon receipt at the DEP Laboratory, the samples were logged. The smear samples were placed 

on a 2-inch diameter planchet and analyzed for gross  and gross  particles using a gas 

proportional counter. Prior to the start of analysis, an instrument source check and background 

check were completed, reviewed, and validated. The gross  and gross  filter analyses were

conducted using the DEP Laboratory-developed method. A standard QC calibration verification

instrument check was performed with NIST traceable sources.

2.3 Survey and Sample Analyses Data Management

All of the solid and liquid samples were analyzed by the DEP Laboratory using gamma 

spectroscopy. The result, the standard two-sigma error (95 percent confidence level) and the 

minimum detectable concentration (MDC) were reviewed for each of the following 

radionuclides as reported:
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 Natural Uranium Decay Series Results (U-238, Ra-226, Pb-214, and Bi-214)

 Natural Thorium Decay Series Results (Th-232, Ra-228, Ac-228, Pb-212, and Bi-212)

 Natural Actinium Decay Series Results (U-235)

 Miscellaneous (K-40)

2.3.1 Limitations on Gamma Spectroscopy Results

The following limitations on gamma spectroscopy of radioactive samples were considered when 

reviewing the analytical results for solid and liquid samples:

 Gamma spectroscopy cannot directly measure radium (Ra)-228. Rather, Ra-228 is inferred 

from a short-lived progeny of Ra-228, Ac-228, which is readily detected by gamma 

spectroscopy when the radionuclides are in secular equilibrium. Due to the relative half-lives 

of Ra-228 (5.8 years) and Ac-228 (6.1 hours) after 24 hours, this is always the case for the 

samples collected as part of the study.

 Gamma spectroscopy cannot directly measure Th-232. Consequently, Th-232 is inferred 

from the short-lived progeny of Th-232, Ra-228, when the radionuclides are in secular 

equilibrium. Due to the difference in solubility between Th and Ra, this is not the case in 

liquid samples or in solid samples of wastewater residue, sludge and filter cake. Only the 

soluble Ra and progeny of Ra are present in those samples. Consequently, knowledge of the 

status of the secular equilibrium of the Th decay series within the sample matrix is necessary 

to properly evaluate gamma spectroscopy results.

 Uranium-238 can be detected by gamma spectroscopy, but the gamma emission used is of 

low energy and low yield, resulting in a high MDC and high standard error compared to the 

other radionuclides in the environment. Consequently, the U-238 result is not used as 

positive identification of U-238 without knowledge of the status of U series secular 

equilibrium and the identification of additional, more statistically robust U progeny.

 Uranium is insoluble in water while Ra is water soluble. Therefore, wastewater, produced

and flowback fluids, and wastewater treatment solids (sludge and filter cake) contain Ra and

its progeny but do not include U.

Only the radionuclides present in a given sample are reported in the following sections. The 

average, median, standard deviation, and minimum and maximum values are also provided at the 

bottom of each table for each set of results. Please note:

 When the reported result is less than the MDC, a value equal to 1⁄2 the MDC is used in the 

derivation of average, median, standard deviation, and minimum and maximum values.

 When “<” precedes the reported result, the value is the MDC.

Appendix C contains the gamma spectroscopy analytical analysis results for each radionuclide 

identified along with their associated standard two-sigma counting error (error) and the MDC for 

the analyses.

2.3.2 Radium-226 Quantification by Gamma Spectroscopy

Radium-226 may be measured directly by detection of its 186.2 kilo-electron volt (keV) energy 

line, 3.28 percent yield. For liquid samples and sludge/filter cake samples that do not contain U,
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January 2015 2-10

this yields an accurate Ra-226 result. However, in soil and drill cutting samples, the presence of 

U-235 causes interference with direct Ra-226 detection because one of its gamma lines is of 

similar energy, 185.7 keV at 54 percent yield. In solid samples where natural U including U-238 

and Ra-226 are at equal activity and U-235 is at 1/22 the activity of U-238, the theoretical 

overestimation of Ra-226 was quantified assuming the gamma peaks for Ra-226 and U-235 

completely overlap. The theoretical overestimation of Ra-226 is presented in Table 2-1. 

The short-lived equilibrium progeny of Ra, Pb-214 and Bi-214, may be used to infer Ra-226 

concentrations in soil or drill cuttings when U-235 is present in the sample. The parent of these 

progeny, Rn-222, is a gas and has a half-life of 3.8 days. When the soil or drill cuttings sample 

is collected, some of the Rn gas escapes the solid matrix. Therefore, samples are sealed to allow 

the Rn gas to develop for three weeks of progeny ingrowth to reestablish equilibrium after the 

sample has been sealed. 

2.3.3 Criteria for Comparison to Analytical Analyses Results

Table 2-2 presents criteria against which the analytical results and assessments of this study 

were evaluated.

2.3.4 Normal Background Radioactivity Values

Table 2-3 presents average, minimum, and maximum background radioactivity values for soil in 

the U.S. used as a reference point when reviewing analytical results of solid samples.

2.3.5 Data Presentation

A large volume of survey and sample analytical analyses data were generated. The next five 

sections present the survey and sampling data for Well Sites, WWTPs, Landfills, Gas

Distribution and End Use, and Brine-Treated Roads.
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January 2015 2-11

Table 2-1. Theoretical Overestimation of Ra-226 Activity in Solid Samples with 

Natural Uranium Analyzed by Gamma Spectroscopy

Radionuclide (pCi/g) (pCi/g) (pCi/g) (pCi/g) (pCi/g) (pCi/g) (pCi/g)

U-238 1.00 2.00 3.00 4.00 5.00 10.0 20.0

U-235 0.05 0.09 0.14 0.18 0.23 0.45 0.91

Ra-226 1.00 2.00 3.00 4.00 5.00 10.0 20.0

Excess Ra-226a0.75 1.51 2.26 3.02 3.77 7.54 15.1

Reported Ra-226 1.75 3.51 5.26 7.02 8.77 17.5 35.1

Excess U-235b0.06 0.12 0.18 0.24 0.30 0.60 1.21

Reported U-235 0.11 0.21 0.32 0.42 0.53 1.06 2.11

aExcess Ra-226 is calculated by converting the U-235 value to Ra-226 activity by a factor equal to the 

ratio of the gamma yields, i.e., 50.4/3.28.

bExcess U-235 is calculated by converting the Ra-226 value to Ra-226 activity by a factor equal to the 

ratio of the gamma yields, i.e., 3.28/50.4.
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January 2015 2-12

Table 2-2. Criteria for Comparison

Parameter Criteria Reference Potentially Apply to:

Volumetric Solids 3 pCi/g Total Radium 

(Ra-226 + Ra-228) 

above background

American National 

Standards Institute 

(ANSI)/Health 

Physics Society (HPS)

N13.53-2009, Control 

and Release of 

Technologically 

Enhanced NORM 

(TENORM) (2009) 

Sediment, Beneficial 

Use Surface Soil, 

Surface Soil on Well 

Sites

Volumetric Solids 5 pCi/g Total Radium 

(Ra-226 + Ra-228) 

above background

EPA Directive No. 

9200.4-35, 

Remediation Goals 

for Radioactively 

Contaminated 

CERCLA Sites (2000)

Sediment, Beneficial 

Use Surface Soil, 

Surface Soil on Well 

Sites

Volumetric Solids 270 pCi/g Total 

Radium (Ra-226 + 

Ra-228) 

U.S. Department of 

Transportation 

(DOT), 49 CFR

173.436, Radioactive 

Material (in regards to 

transportation)

Sludge, Filter Cake, 

Filter Socks, Scale, 

Cuttings

Volumetric Liquids 5 pCi/L Total Radium 

(Ra-226 + Ra-228) in 

drinking water

EPA Drinking Water 

Standard, 40 CFR 

141.66

Effluent Water from 

Well Sites

Volumetric Liquids 60 pCi/L Total 

Radium (Ra-226 + 

Ra-228) direct 

discharge

U.S. Nuclear 

Regulatory 

Commission (NRC),

10 CFR Part 20 

Appendix B, Table 2, 

Liquid Effluent

Effluent Water from 

Well Sites and 

Wastewater Facilities

Volumetric Liquids 600 pCi/L Total 

Radium (Ra-226 + 

Ra-228) discharge to 

sanitary sewer

U.S. NRC, 10 CFR

Part 20 Appendix B, 

Table 2, Liquid 

Effluent (assumes 

dilution and solubility 

of Ra)

Effluent Water from 

Well Sites and 

Wastewater Facilities

Total Alpha Surface 

Contamination

100 dpm/100 cm2 U.S. NRC, Regulatory 

Guide 1.86, 

Termination of 

Operating Licenses 

for Nuclear Reactors 

(1974)—Criteria for 

Ra-226

Structural surfaces on 

well sites and within 

wastewater facilities, 

and equipment 

released from sites
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January 2015 2-13

Table 2-2. Criteria for Comparison

Parameter Criteria Reference Potentially Apply to:

Total Beta Surface 

Contamination

1,000 dpm/100 cm

2 U.S. NRC, Regulatory 

Guide 1.86, 

Termination of 

Operating Licenses 

for Nuclear Reactors 

(1974)—Criteria for 

natural Th including 

Ra-228

Structural surfaces on 

well sites and within 

wastewater facilities, 

and equipment 

released from sites

Removable Alpha 

Surface 

Contamination

20 dpm/100 cm

2

(of 

surface area smear 

sampled)

U.S. NRC, Regulatory 

Guide 1.86, 

Termination of 

Operating Licenses 

for Nuclear Reactors 

(1974)—Criteria for 

Ra-226

Structural surfaces on 

well sites and within 

wastewater facilities, 

and equipment 

released from sites

Removable Beta 

Surface 

Contamination

200 dpm/100 cm

2

(of 

surface area smear 

sampled)

U.S. NRC, Regulatory 

Guide 1.86, 

Termination of 

Operating Licenses 

for Nuclear Reactors 

(1974)—Criteria for 

natural Th including 

Ra-228

Structural surfaces on 

well sites and within 

wastewater facilities, 

and equipment 

released from sites

Volumetric Gas 4 pCi/L EPA, 402/K-12/002, 

A Citizen’s Guide to 

Radon (2012)

Buildings, General 

Public

Volumetric Gas 30 pCi/L Derived Air 

Concentration (DAC)

U.S. NRC, 10 CFR

Part 20 Appendix B, 

Table 1, Col 3

Occupational 

Exposure

Volumetric Gas 100 pCi/L Occupational Safety and 

Health Administration 

(OSHA) 29 CFR 

1910.1096

General Public 

Workforce

Annual Exposure 25 mrem/year plus as 

low as reasonably 

achievable (ALARA)

U.S. NRC, 10 CFR 

20.1402-20.1403, 

Radiological Criteria 

for Unrestricted Use

General Public

Annual Exposure 100 mrem/year U.S. NRC, 10 CFR 

20.1301, Radiation 

Dose Limits for 

Members of the 

Public

General Public

Workers not trained 

as Radiation Workers, 

i.e., well site and 

water facilities 

workers
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Table 2-2. Criteria for Comparison

Parameter Criteria Reference Potentially Apply to:

Annual Exposure 5,000 mrem/year U.S. NRC, 10 CFR 

20.1201, 

Occupational Dose 

Limits for Adults

Radiation Workers

Table 2-3. Natural Background Radioactivity Values for U.S. Soil

Material U-238 (pCi/g) Ra-226 (pCi/g) Th-232 (pCi/g) K-40 (pCi/g)

Soil (Average)a0.95 1.1 0.95 10

Soil (Minimum)a0.11 0.22 0.11 2.7

Soil (Maximum) a3.8 4.3 3.5 19

aUNSCEAR, Sources and Effects of Ionizing Radiation (UNSCEAR 2000).
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January 2015 3-1

3.0 WELL SITES

Thirty-eight well sites, including four conventional wells and 34 unconventional wells, were 

sampled from June 2013 through July 2014. Data from five phases of well development and 

completion were collected: vertical drilling, horizontal drilling, hydraulic fracturing, flowback,

and production. A listing of the well types, formations, phases, and geographic regions is 

provided below.

 4 Conventional Wells

 Formations

 1 in the Lower Devonian/Oriskany

 3 in the Upper Devonian

 Phase

 Production Phase

 34 Unconventional Wells

 Formations

 29 in the Lower Devonian/Marcellus

 2 in the Lower Devonian/Marcellus Sandstone

 1 in the Upper Devonian/Burket

 2 in the Middle Ordovician/Utica

 Phases

 10 sampled during the vertical drilling phase

 10 sampled during the horizontal drilling phase

 10 sampled during the hydraulic fracturing phase

 9 sampled during the flowback phase

 19 sampled during the production phase

 9 sampled for fluids and Rn

 10 sampled for just Rn

 Regions

 1 in the Northeast Region

 17 in the North-central Region

 4 in the Northwest Region

 16 in the Southwest Region

3.1 Radiological Survey Results

Radiological surveys were conducted at each well site resulting in four data sets:

 Removable / surface radioactivity measurements recorded in units of dpm/100 cm2

 Total / surface radioactivity measurements recorded in units of dpm/100 cm

2

 Gross Gamma Radiation Scan measurements recorded in units of cpm

 Gamma Radiation Exposure Rate measurements recorded in units of μR/hr

3.1.1 Removable Alpha/Beta Surface Radioactivity Measurement Results

Measurements of removable / surface radioactivity were performed to assess potential internal 

radiation worker exposure through ingestion and/or inhalation. The results were evaluated using 
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January 2015 3-2

the NRC Regulatory Guide 1.86 (RG 1.86) guidelines. RG 1.86 Table 1 requires that  and 

levels be evaluated separately. The primary emitter of concern is Ra-226 with a removable 

criterion of 20 dpm /100 cm2. The primary  emitter of concern is Ra-228 of the natural Th 

decay series with a removable criterion of 200 dpm /100 cm2. The average removable  and 

levels at each well site were below the RG 1.86 criteria. The maximum removable  and 

levels were 15 dpm/100 cm2and 76 dpm/100 cm2, also below the RG 1.86 criteria. The 

summary results of removable / radioactivity for each of the well sites surveyed are presented

in Table 3-1. Individual smear sample removable / results are presented in Appendix D.

3.1.2 Total Alpha/BetaSurface Radioactivity Measurement Results

Measurements of total / surface radioactivity were performed to assess potential worker 

internal radiation exposure through ingestion and/or inhalation. The results were evaluated using 

the RG 1.86 Table 1 guidelines. RG 1.86 requires that  and  activity be evaluated separately.

The primary emitter of concern is Ra-226 with a total criterion of 100 dpm /100 cm2. The 

primary  emitter of concern is Ra-228 of the natural Th decay series with a total criterion of 

1,000 dpm /100 cm2. The maximum average total andlevels measured at any single well 

site were 93.0 dpm/100 cm2and 1,630 dpm/100 cm2. The maximum total and levels 

measured were 754 dpm/100 cm2and 2,503 dpm/100 cm2. The summary results of total and 

surface radioactivity for each of the well sites surveyed are presented in Table 3-2. Individual

total / measurement results are presented in Appendix D.

3.1.3 Gross Gamma Radiation Scan Results

Gross gamma radiation scans recorded in cpm were performed on well sites to identify areas of 

radioactivity above local background levels. Summary results for each of the well sites surveyed 

and each phase surveyed are presented in Table 3-3. The highest average gross gamma radiation 

count rate was 14,519 cpm (approximately 18 μR/h), and the maximum gamma radiation scan 

result measured was 30,823 cpm (approximately 39 μR/h). A graphic display of the gamma 

radiation scan results (figures) at each facility was prepared using geographic information system 

(GIS) software. Figures are presented in Appendix E.

3.1.4 Gamma Radiation Exposure Rate Results

Gross gamma radiation scan results in units of cpm presented in Table 3-3 were converted to 

R/hr using the 800 cpm per R/hr conversion factor appropriate for Ra-226 gamma energy as 

detected with 2-inch by 2-inch NaI detectors, rounded to one significant figure (Table 6.4, NaI 

Scintillation Detector Scan MDCs for Common Radiological Contaminants, NUREG-1507, 

Minimum Detectable Concentrations With Typical Radiation Survey Instruments for Various 

Contaminants and Field Conditions, USNRC June 1998). The exposure rate results for each well 

site are presented in Table 3-4. The highest average exposure rate measured at any single site 

was 18.1 R/hr, and the maximum gamma exposure rate measured was 38.5 R/hr.
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-3

3.2 Solid Sample Results

3.2.1 Vertical Phase Drill Cuttings

Vertical cuttings were sampled at 11 unconventional well sites and analyzed using gamma 

spectroscopy to identify gamma-emitting members of the natural U, Th, and Ac decay series.

The gamma spectroscopy results are presented in Table 3-5. XRF analysis was also performed 

on the vertical drill cuttings to identify non-gamma-emitting isotopes of U-238 and Th-232.

XRF ppm concentration data for Th was converted to pCi/g of Th-232 using the specific activity

of 0.110 pCi/g Th-232 per ppm of Th. XRF ppm concentration data for U was converted to 

pCi/g of U-238 using the specific activity of 0.334 pCi/g U-238 per ppm of U. Both the ppm and 

the pCi/g results for 10 well sites are presented in Table 3-6. All of the XRF analytical results 

are presented in Appendix F.

There were two methods for managing drill cuttings at the well sites. The first method, called a 

“half round,” accumulates cuttings in a large mixing container where the materials were

stabilized prior to shipment to the landfill. This method does not provide an opportunity to 

collect samples at discrete depths; consequently, a composited sample was collected during 

vertical drilling. This method was used at nine of the 10 well sites.

The second method loads the cuttings into roll-off containers from the shaker tables. This

method enables sampling of cuttings from discrete depths. Each container was labeled with the 

start and end depth of the collected material. The formations sampled are presented in Table 3-6

for these vertical drill cuttings. This method was used at one well site.

The U series activities are variable because the vertical cuttings represent different geologic 

formations lying above the target natural gas-containing shale. These vertical drill cuttings are 

mostly siltstones and sandstones. Potassium-40 (K-40) concentrations provide an indication of 

the type of formation. Shale has higher levels of K-40 than sandstone. Shale is typically in the 

range of 25-30 pCi/g of K-40 while sandstone typically contains approximately 5 pCi/g of K-40.

The U-238 measured using XRF and the Ra-226 measured using gamma spectroscopy were 

compared to confirm secular equilibrium of the U decay series within drill cuttings. Figure 3-1

provides a graphic representation of this comparison and shows agreement between the two U

series radionuclides, indicating secular equilibrium. Although the gamma spectroscopy results 

for Ra-226 are consistently higher than the XRF results for U-238, both values trend together, 

i.e., increase and decrease together. The high bias of the Ra-226 gamma spectroscopy results is 

due in part from the U-235 interference when identifying Ra-226 using gamma spectroscopy of 

the 186 keV gamma line. (Refer to Section 2.3.2 for a complete discussion of Ra-226 detection 

using gamma spectroscopy.) U-235, which is also present in drill cuttings, also emits gamma at 

186 keV, causing a consistent positive bias of Ra-226 results.

Th-232 and Ra-228 do not emit gamma rays identifiable by gamma spectroscopy; consequently, 

the levels were inferred from the Ac-228 gamma rays. The Th-232 series radionuclide activity 

levels all typify natural background for soil (reference Table 2-3).
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-4

Figure 3-1. Comparison of Ra-226 Gamma Spectroscopy Results to U-238 XRF Results in 

Vertical Drill Cuttings

The Th-232 identified using XRF and the Ra-228 inferred using gamma spectroscopy were 

compared to confirm secular equilibrium of the Th decay series within drill cuttings. Figure 3-2

provides a graphic representation of this comparison and shows agreement between the two Th

series radionuclides.

Figure 3-2. Comparison of Ra-228 Gamma Spectroscopy Results to Th-232 XRF Results in 

Vertical Drill Cuttings

The Th-232 to Ra-228 values for most samples trend together, i.e., when the activity 

concentration of one increases, there is a comparable increase in the other.

3.2.2 Horizontal Phase Drill Cuttings

The same two cuttings management methods described for vertical drill cuttings were also used 

for horizontal drill cuttings. A total of 18 samples were collected from the horizontal well bore 

target formations on 10 well sites. The gamma spectroscopy and XRF results are presented in

Tables 3-7 and 3-8.

Figure 3-3 presents the analytical results for vertical and horizontal cutting samples. The 

horizontal drill cuttings had higher concentrations of Ra-226 than the vertical drill cuttings as

0.0 pCi/g

2.0 pCi/g

4.0 pCi/g

6.0 pCi/g

8.0 pCi/g

10.0 pCi/g

12.0 pCi/g

14.0 pCi/g

16.0 pCi/g

18.0 pCi/g

20.0 pCi/g

Ra-226 (Gamma Spec)

U-238 (XRF)

0.00 pCi/g

1.00 pCi/g

2.00 pCi/g

3.00 pCi/g

4.00 pCi/g

5.00 pCi/g

Ra-228 (Gamma Spec)

Th-232 (XRF)
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-5

Figure 3-3. Comparison of Analytical Analyses Results for Horizontal and Vertical Drill 

Cutting Samples

determined using a student t-test. The two-sample student t-test was used to compare the 

horizontal drill cuttings Ra-226 results with the vertical drill cuttings Ra-226 results. ProUCL 

version 5.0 was used to perform the student t-test on the data. The Null Hypothesis tested is that 

the mean value of the vertical drill cuttings Ra-226 results and the mean value of the horizontal 

drill cuttings Ra-226 results are statistically different at the 95 percent confidence level. The 

Null Hypothesis was accepted; mean values are statistically different at the 95 percent 

confidence level. The same t-test was run on the U-238 results for vertical and horizontal drill 

cuttings. Again, the difference between the mean values of U-238 for vertical and horizontal 

drill cuttings is statistically different at the 95 percent confidence level. Appendix G presents 

the t-test output files.

The U concentration (ppm) measured using XRF was converted to pCi/g of U-238 using the 

specific activity of 0.334 pCi/g U-238 per ppm of U. The U-238 measured using XRF and the 

Ra-226 measured using gamma spectroscopy were compared to confirm secular equilibrium of 

the U decay series within drill cuttings. Figure 3-4 provides a graphic representation of this 

comparison and shows agreement between the two U series radionuclides, indicating secular 

equilibrium.

Figure 3-4. Comparison of Ra-226 Gamma Spectroscopy Results to U-238 XRF Results in 

Horizontal Drill Cuttings

 pCi/g

1 pCi/g

2 pCi/g

3 pCi/g

4 pCi/g

5 pCi/g

6 pCi/g

7 pCi/g

8 pCi/g

9 pCi/g

U-238 Ra-226 Th-232 Ra-228

Radionuclide

Vertical Cuttings

Horizontal Cuttings

0.0 pCi/g

5.0 pCi/g

10.0 pCi/g

15.0 pCi/g

20.0 pCi/g

25.0 pCi/g

30.0 pCi/g

Ra-226 (Gamma Spec)

U-238 (XRF)
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-6

The Th concentration (ppm) measured using XRF was converted to pCi/g of Th-232 using the 

specific activity of 0.110 pCi/g Th-232 per ppm of Th. The Th-232 measured using XRF and the 

Ra-228 inferred using gamma spectroscopy were compared to confirm secular equilibrium of the 

Th decay series within drill cuttings. Figure 3-5 provides a graphic representation of this 

comparison.

Figure 3-5. Comparison of Ra-228 Gamma Spectroscopy Results to Th-232 XRF Results in 

Horizontal Drill Cuttings

The Th-232 to Ra-228 values trend together, i.e., when the activity concentration of one 

increases, there is a comparable increase in the other.

3.2.3 Drilling Mud

In addition to drill cuttings, drilling mud was also collected when in use on the sites. A total of 

14 drilling mud samples were collected during both the vertical and horizontal phases of drilling.

The drilling mud was evaluated as a drilling solid or a drilling liquid as determined when 

received by the laboratory. Nine of those samples were analyzed as solids and the other five as 

liquids. The gamma spectroscopy results for solids are presented in Table 3-9.

Analytical results for the drilling mud demonstrate secular equilibrium within the U and Th 

natural decay series, i.e., the activity concentrations within the natural series radionuclides 

identified are approximately equal. All results were within the range of typical natural 

background found in surface soils (reference Table 2-3), given the overestimation of Ra-226 in 

the presence of U-235 as discussed in Section 2.3.2.

3.2.4 Hydraulic Fracturing Proppant Sand

During hydraulic fracturing, 10 well sites were surveyed and sampled. The proppant sand was 

collected from the sand hoppers prior to being mixed with fluids and injected into the well. The 

gamma spectroscopy results are presented in Table 3-10.

The sand contained nominal concentrations of U and Th series. The sand did not contain 

radioactivity exceeding that of natural background levels found in surface soil (reference 

Table 2-3).

0.00 pCi/g

1.00 pCi/g

2.00 pCi/g

3.00 pCi/g

4.00 pCi/g

5.00 pCi/g

Ra-228 (Gamma Spec)

Th-232 (XRF)
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-7

3.2.5 Flowback Solids

A total of eight well sites were surveyed and sampled during the flowback phase. From the eight 

well sites, sufficient volumes to perform analytical analysis of solids were only present at four of 

the eight well sites. The gamma spectroscopy results are presented in Table 3-11.

Uranium and Th are at or below background activity levels. Radium-226 was elevated above 

background levels for soil (reference Table 2-3) ranging from 0.77 to 7.7 pCi/g.

3.3 Liquid Sample Results

Liquid sampling included drilling mud, hydraulic fracturing fluids, flowback fluids, and 

produced water.

3.3.1 Drilling Liquid (Mud)

A total of 14 drilling mud samples were collected from both vertical and horizontal phases. The 

drilling mud was evaluated as a drilling solid or a drilling liquid as determined when received by 

the laboratory. Five of the samples were analyzed as liquids. Because of the large concentrations

of solids in the samples, gross  and gross  analyses were performed on only one sample. The 

results for Ra-226, Ra-228, K-40, gross  and gross  are presented in Table 3-12.

3.3.2 Hydraulic Fracturing Fluid

Hydraulic fracturing fluid was sampled prior to injection into the well. The well sites sampled

during the study utilized hydraulic fracturing fluid made up of either fresh water, reused 

flowback liquid, produced water, or a combination of the three to perform the hydraulic 

fracturing phase. If a combination of fluids was used for fracturing, only the produced water was 

collected as a sample because it was not possible to collect a sample after the hydraulic 

fracturing fluid had been mixed for injection. The results for Ra-226, Ra-228, K-40, gross  and 

gross  are presented in Table 3-13.

Radium-226 was detected within the hydraulic fracturing fluid ranging from 64.0 to 21,000 

pCi/L. Ra-228 was also detected ranging from 4.5 to 1,640 pCi/L. Table 2-2 contains several 

volumetric liquids criteria for relative comparison: 5 pCi/L total Ra EPA drinking water,

60 pCi/L total Ra USNRC direct discharge, and 600 pCi/L total Ra USNRC discharge to sanitary 

sewer.

3.3.3 Flowback Fluid

Flowback fluid is the injected hydraulic fracturing fluid and other fluids returning to the surface

of the well prior to the well entering production. The results for Ra-226, Ra-228, K-40, gross 

and gross  are presented in Table 3-14.

Radium-226 concentrations were elevated, ranging from 551 to 25,500 pCi/L. Radium-228 was 

also elevated, ranging from 248 to 1,740 pCi/L. Table 2-2 contains several volumetric liquids 

criteria for relative comparison: 5 pCi/L total Ra EPA drinking water, 60 pCi/L total Ra USNRC 

direct discharge, and 600 pCi/L total Ra USNRC discharge to sanitary sewer.
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-8

3.3.4 Produced Water

Twelve wells were sampled for produced water, including four conventional and eight 

unconventional wells. The results for unfiltered and filtered Ra-226, Ra-228, K-40, gross  and 

gross  are presented in Tables 3-15 and 3-16.

Radium-226 concentrations in unfiltered samples were elevated, ranging from 40.5 to

26,600 pCi/L. Radium-228 concentrations were also elevated, ranging from 26.0 to 1,900 pCi/L.

Radium-226 concentrations were also elevated in filtered samples, ranging from 87.0 to 

24,100 pCi/L. Radium-228 concentrations were also elevated, ranging from 44.0 to 1,860 pCi/L.

3.4 Radon Sample Results

3.4.1 Ambient Air Samples During Flowback

Seventeen ambient air samples for evaluation of Rn concentration were collected during 

flowback at four different well sites. The EICs were distributed around the well site

approximately 3 feet (ft) above grade and at available locations as close as 6 ft and as far as 40 ft 

from the well head. The EICs collected data from four to seven days. The results are presented in 

Table 3-17. The Rn analytical reports are presented in Appendix H.

The Rn measurement results are within the range of typical ambient background Rn

concentrations (0.2 to 0.7 pCi/L in outdoor ambient air in the U.S.).

3.4.2 Production Gas Radon

Twenty-two production site natural gas samples were collected in eight counties (Washington, 

Tioga, Lycoming, McKean, Forest, Sullivan, Bradford and Jefferson). Seventeen of the natural 

gas samples were collected from Marcellus Shale, and five natural gas samples were collected

from other geologic formations.

The production site natural gas samples for Rn were collected between the well head and the 

separator unit(s). A typical sampling location is shown in Figure 3-6. All natural gas samples 

were collected directly into scintillation cells, referred to as Lucas Cells. Section 2.0 describes 

the sample collection in detail.

The sample results are presented in Table 3-18. The results ranged from 3.0 to 147.5 pCi/L. 

The median Rn concentration in natural gas is 40.8 pCi/L. The Rn analysis analytical reports are 

presented in Appendix H.

3.5 Well Site Worker Exposure Assessment

The study included radiation measurements collected on 21 well sites to provide a 

comprehensive evaluation of potential personnel radiation exposure from working on well sites.

The measurements included:
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-9

Figure 3-6. Natural Gas Radon Sampling Location

 Gamma radiation count rate using a NaI detector (gross cpm), converted to exposure rate 

potential, to estimate potential external gamma exposure.

 Total / surface radioactivity measurements using a scintillation detector to evaluate 

potential  external exposure as well as / surface activity having the potential to become 

removable and, therefore, becoming a potential internal exposure.

 Removable / surface radioactivity measurements (dpm/100 cm

2

) by smear samples 

counted on an / counter to estimate potential  and  internal exposure.

 Ambient air samples analyzed for Rn concentration to estimate Rn inhalation exposure.

The measurements were taken during four work phases on natural gas well sites to ensure

appropriate evaluation of potential exposure to TENORM present on well sites. The phases are:

 Vertical/Horizontal Drilling – personnel are potentially exposed to drill cuttings while 

working on the site.

 Hydraulic Fracturing – personnel are potentially exposed to radioactivity in hydraulic 

fracturing fluid while working on the site.

 Flowback – personnel are potentially exposed to radioactivity in flowback water while 

working on the site.

 Production – personnel are potentially exposed to radioactivity in produced water while 

working on the site.
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-10

3.5.1 External Gamma Exposure

Gross gamma scan results in units of cpm presented in Table 3-3 were converted to R/hr using 

the 800 cpm per R/hr conversion factor appropriate for Ra-226 gamma energy as detected with 

2-inch by 2-inch NaI detectors [Table 6.3, NaI Scintillation Detector Count Rate Versus 

Exposure Rate (cpm/R/hr), NUREG-1507, Minimum Detectable Concentrations With Typical 

Radiation Survey Instruments for Various Contaminants and Field Conditions, USNRC June 

1998]. The local background gamma exposure rate across all well sites surveyed was measured 

at 5 μR/hr. The exposure rate results are presented in Table 3-4.

The lowest exposure rates measured and the maximum exposure time were during drilling. The 

highest exposure rates measured were in the proximity of holding tanks for produced water. The 

gamma dose rates during drilling ranged from background (measured at 5 μR/hr) to a maximum 

of 38.5 μR/hr, and the highest average exposure rate at any of the well sites was 18.1 μR/hr. 

Assuming the time period of exposure is a full occupational year of 2,000 hours, the average well 

site external gamma exposure was estimated as follows:

Maximum Average Well Site External Gamma Exposure Estimate

(18.1 – 5) μR/hr x 2000 hr/yr x (1 mrem/1,000 μR gamma) = 26 mrem/yr

The result is less than the 100 mrem/yr dose equivalent limit for a member of the public. Actual 

exposure is dependent upon the actual exposure rates and occupancy time for individual workers.

3.5.2 Internal Alpha/Beta Exposure

Results for / surface radioactivity measurements are provided in Sections 3.1.1 and 3.1.2. Ten 

of the 491  measurements and 69 of the 491  measurements of total surface radioactivity 

exceeded the RG 1.86 criteria. Only one of 493 removable surface activity measurements and 

one of 493  surface radioactivity measurements exceeded RG 1.86 criteria, indicating the total 

/ surface radioactivity measured is fixed to the surface and not readily available for inhalation 

or ingestion.

3.5.3 Internal Radon Exposure

The Rn in ambient air measurement results during flowback are within the range of typical 

ambient background Rn concentrations (0.2 to 0.7 pCi/L in outdoor ambient air in the U.S.).

3.6 Well Site Data Assessments

3.6.1 Comparison of Different Geological Formations Based on X-Ray Fluorescence Data

Eighteen drill cutting samples were collected and analyzed for Th and U using XRF. The 

samples were collected from the Lower Devonian/Marcellus, Upper Devonian/Burket, and the 

Middle Ordovician/Utica geologic formations. The data for the three geologic formations,

including the average, median, standard deviation, and ratios of Th to U are presented in 

Table 3-19.
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-11

XRF ppm concentration data for Th was converted to pCi/g of Th-232 using the specific activity 

value of 0.110 pCi/g Th-232 per ppm of Th. XRF ppm concentration data for U was converted 

to pCi/g of U-238 using the specific activity value of 0.334 pCi/g of U-238 per ppm of U. Ratios 

of U/Th are also presented in Table 3-19.

3.6.2 Filtered Versus Unfiltered Sample Data Evaluation

Appendix I contains the assessment of filtered and unfiltered liquid sample results for the entire 

TENORM study. The conclusion from this evaluation is that there is no apparent trend or bias 

that filtering produces. There were some subsets of data where either the unfiltered results or the 

filtered results appear to be significantly higher. There was no statistically significant correlation 

found within any sample group. Because the liquid samples were preserved by addition of acid 

prior to filtering, the radioactive particulates may have entered solution and were therefore not 

removed by filtering.

3.6.3 Conventional Versus Unconventional Produced Water Data Evaluation

There was a significant difference observed in the produced water from conventional and 

unconventional O&G well sites. Tables 3-15 and 3-16 present gamma spectroscopy results for 

conventional and unconventional produced water for both filtered and unfiltered samples. Two 

distinct differences in magnitude of activity and in the ratio of Ra-226 to Ra-228 are summarized 

in Figure 3-7.

Figure 3-7. Conventional vs Unconventional Produced Water Radium Concentrations

O&G 

Production

Filtered 

Samples

No. of 

Samples

Average 

Ra-226 (pCi/L)

Average 

Ra-228 (pCi/L)

Ratio of 

Ra-226/Ra-228

Conventional No 4 336 295 1.1

Unconventional No 9 8,340 986 8.5

Conventional Yes 4 334 288 1.2

Unconventional Yes 9 8,220 985 8.3

The Ra-226 activity in unconventional well site produced water is approximately 20 times 

greater than that observed in conventional well site produced water. The ratio of Ra-226 to 

Ra-228 in unconventional well site produced water is approximately eight times greater than that 

found in conventional well site produced water. The higher ratio of Ra-226 to Ra-228 for 

unconventional well site produced water reflects the higher ratio of U to Th observed in 

Marcellus Shale horizontal cuttings sample results. The U to Th ratio is approximately six.

Filtering of the samples does not appreciably change the activity concentration or the 

relationship between Ra-226 and Ra-228.

3.7 Potential Off-site Environmental Impact

A potential off-site environmental impact could result from the removal of materials and/or 

equipment with total and/or removable / surface radioactivity above applicable guidelines.

The highest total  surface radioactivity measurement was 754 dpm/100 cm2. Additional

measurements exceeded the RG 1.86 Ra-226 total surface contamination guideline of 

100 dpm/100 cm2. The highest total  measurement was 2,503 dpm/100 cm2. This and several 

other measurements exceeded the RG 1.86 Th-232 total surface contamination guideline of 
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-12

1,000 dpm/100 cm2. These readings were on equipment associated with wastewater

handling/storage, and this equipment is likely to be reused.
PA DEP TENORM Study Report 

– Section 3.0 Rev. 0

January 2015 3-13

Table 3-1. Removable Alpha and Beta Surface Radioactivity Measurement Results Summarya,b

Facility 

ID

No. of 

Data 

Points

Removable Alpha (dpm/100 cm2) Removable Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

WP-01-

FS-045 12 4.24 12.4 2.36 4.92 93.7 93.7 0.00 93.7

WP-01-

FS-081 7 4.24 4.24 0.00 4.24 102 102 0.00 102

WP-01-

FS-128 3 4.24 12.4 4.79 6.96 118 118 0.00 118

WP-02-

FS-083 27 4.24 4.24 0.00 4.24 102 102 0.00 102

WP-03-

FS-029 15 4.15 4.15 0.78 4.15 109 109 0.00 109

WP-03-

FS-082 14 4.24 4.24 0.00 4.24 86.7 86.7 0.00 86.7

WP-04-

FS-014 10 4.24 7.24 1.07 4.24 93.7 93.7 0.00 93.7

WP-04-

FS-084 22 4.24 4.24 0.18 4.24 95.7 95.7 0.00 95.7

WP-04-

FS-085 29 4.24 4.24 0.00 4.24 108 108 0.00 108

WP-05-

FS-077 3 4.15 4.15 0.00 4.15 113 113 0.00 113

WP-05-

FS-089 26 4.15 4.15 0.00 4.15 98.9 98.9 0.00 98.9

WP-06-

FS-026 3 4.14 4.14 0.00 4.14 112 112 0.00 112

WP-06-

FS-091 29 4.24 4.24 0.00 4.24 102 102 0.00 102

WP-06-

FS-092 23 4.24 4.24 0.00 4.24 95.5 95.5 0.00 95.5

WP-06-

FS-093 4 4.15 4.15 0.00 4.15 111 111 0.00 111

WP-07-

FS-094 12 4.24 4.24 0.00 4.24 102 102 0.00 102
PA DEP TENORM Study Report 

– Section 3.0 Rev. 0

January 2015 3-14

Table 3-1. Removable Alpha and Beta Surface Radioactivity Measurement Results Summarya,b

Facility 

ID

No. of 

Data 

Points

Removable Alpha (dpm/100 cm2) Removable Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

WP-08-

FS-010 5 4.24 4.24 0.00 4.24 123 123 0.00 123

WP-08-

FS-095 5 4.24 4.24 0.00 4.24 102 102 0.00 102

WP-09-

FS-097 7 4.15 4.15 0.00 4.24 102 102 0.00 102

WP-09-

FS-098 3 4.24 4.24 0.00 4.24 113 113 0.00 113

WP-10-

FS-003 21 4.24 4.24 0.00 4.24 93.7 93.7 0.00 93.7

WP-10-

FS-004 21 4.14 4.15 0.00 4.15 93.7 93.7 0.00 93.7

WP-10-

FS-009 8 4.15 4.15 0.00 4.15 113 113 0.00 113

WP-11-

FS-023 17 4.15 4.15 0.00 4.15 109 109 0.00 109

WP-11-

FS-037 15 4.15 4.15 0.00 4.15 113 113 0.00 113

WP-11-

FS-102 17 4.15 4.15 0.00 4.15 109 109 0.00 109

WP-12-

FS-017 23 4.24 4.24 0.00 4.24 93.7 93.7 0.00 93.7

WP-12-

FS-018 4 4.14 4.14 0.00 4.14 113 113 0.00 113

WP-12-

FS-019 19 4.24 4.24 0.00 4.24 93.7 93.7 0.00 93.7

WP-13-

FS-041 17 4.24 4.24 0.00 4.24 123 123 0.00 123

WP-13-

FS-042 18 4.24 4.24 0.00 4.24 123 123 0.00 123

WP-14-

FS-035 20 4.15 12.2 2.47 4.96 114 114 0.00 114
PA DEP TENORM Study Report 

– Section 3.0 Rev. 0

January 2015 3-15

Table 3-1. Removable Alpha and Beta Surface Radioactivity Measurement Results Summarya,b

Facility 

ID

No. of 

Data 

Points

Removable Alpha (dpm/100 cm2) Removable Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

WP-14-

FS-036 23 4.15 14.9 2.36 4.62 114 114 0.00 114

WP-14-

FS-107 4 4.15 4.15 0.00 4.15 114 114 0.00 114

WP-15-

FS-028 7 4.15 4.15 0.00 4.15 114 114 0.00 114

a

Smear samples were performed on facility, system, and structure surfaces.

bDuring the calculations to convert from raw counts to dpm, the calculated value was compared to half of the MDC. If the value was below this 

number, half of the MDC was inserted into the tables. Where the standard deviation is zero and the minimum, maximum, and average are the 

same, then all measurements were below half of the MDC. 
PA DEP TENORM Study Report 

– Section 3.0 Rev. 0

January 2015 3-16

Table 3-2. Total Alpha and Beta Surface Radioactivity Measurement Results Summarya,b

Facility 

ID

No. of 

Data 

Points

Total Alpha (dpm/100 cm2) Total Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

WP-01-FS045 12 30.5 30.5 0.00 30.5 364 2500 618 1190

WP-01-FS081 7 19.0 19.0 0.00 19.0 279 1710 460 777

WP-02-FS083 27 7.44 14.9 2.84 8.82 288 676 75.5 305

WP-03-FS029 16 30.5 30.5 0.00 30.5 357 884 137 587

WP-03-FS082 14 7.44 79.0 19.2 16.0 266 364 28.6 282

WP-04-FS014 10 30.5 30.5 0.00 30.5 364 2220 812 1170

WP-04-FS084 22 7.46 69.6 16.4 13.7 325 325 0.00 325

WP-04-FS085 29 7.46 29.8 7.06 11.3 317 651 69.6 337

WP-05-FS077 3 30.5 30.5 0.00 30.5 513 698 96.0 592

WP-05-FS089 26 7.46 164 46.6 26.0 280 542 59.0 299

WP-06-FS026 30.5 30.5 30.5 0.00 30.5 646 1920 652 1200

WP-06-FS091 29 7.46 24.9 4.00 8.92 297 297 0.00 297

WP-06-FS092 23 7.44 44.6 8.00 9.38 278 527 54.0 292

WP-06-FS093 4 30.5 30.5 0.00 30.5 268 268 0.00 268

WP-07-FS094 12 7.44 19.8 4.16 9.71 291 988 201 349

WP-08-FS010 5 30.5 30.5 0.00 30.5 557 721 65.0 624
PA DEP TENORM Study Report 

– Section 3.0 Rev. 0

January 2015 3-17

Table 3-2. Total Alpha and Beta Surface Radioactivity Measurement Results Summarya,b

Facility 

ID

No. of 

Data 

Points

Total Alpha (dpm/100 cm2) Total Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

WP-08-FS095 5 19.0 19.0 0.00 19.0 279 279 0.00 279

WP-09-FS097 7 7.44 29.8 8.69 13.5 285 285 0.00 285

WP-09-FS098 3 30.5 30.5 0.00 30.5 268 268 0.00 268

WP-10-FS003 21 30.5 754 167 93.0 268 1580 417 676

WP-10-FS004 21 30.5 258 69.4 60.0 268 1580 410 709

WP-10-FS009 8 30.5 30.5 0.00 30.5 1390 1890 145 1630

WP-11-FS023 17 30.5 30.5 0.00 30.5 364 1410 294 966

WP-11-FS037 15 30.5 30.5 0.00 30.5 268 1020 223 583

WP-11-FS102 17 30.5 30.5 0.00 30.5 268 1410 294 960

WP-12-FS017 23 30.5 30.5 0.00 30.5 268 884 145 374

WP-12-FS018 4 30.5 30.5 0.00 30.5 839 951 51 910

WP-12-FS019 19 30.5 30.5 0.00 30.5 268 1550 378 513

WP-13-FS041 17 30.5 30.5 0.00 30.5 371 1430 303 1010

WP-13-FS042 18 30.5 30.5 0.00 30.5 275 1380 273 799

WP-14-FS035 20 30.5 30.5 0.00 30.5 268 721 130 315

WP-14-FS036 23 30.5 30.5 0.00 30.5 268 483 55 284
PA DEP TENORM Study Report 

– Section 3.0 Rev. 0

January 2015 3-18

Table 3-2. Total Alpha and Beta Surface Radioactivity Measurement Results Summarya,b

Facility 

ID

No. of 

Data 

Points

Total Alpha (dpm/100 cm2) Total Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

WP-14-FS107 4 27.8 27.8 0.00 27.8 69.3 69.3 0.00 69.3

WP-15-FS028 6 30.5 30.5 0.00 30.5 268 268 0.00 268

a

Static measurements were performed on facility, system, and structure surfaces.

bDuring the calculations to convert from raw counts to dpm, the calculated value was compared to half of the MDC. If the value was below this 

number, half of the MDC was inserted into the tables. Where the standard deviation is zero and the minimum, maximum, and average are the 

same, then all measurements were below half of the MDC.
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-19

Table 3-3. Gross Gamma Scan Results Summarya

Site Phase Scan Maxb

(cpm)

Scan Minb

(cpm)

Scan

Averageb

(cpm)

Scan

Std Dev 

(cpm)

No. Data 

Points

WP-01 Fracturing 16,608 7,209 13,028 1,349 4,857

WP-01 Flowback 17,299 6,653 14,519 1,246 4,474

WP-01 Production 16,641 9,019 13,787 1,075 4,891

WP-02 Horizontal 9,363 4,262 5,371 1,041 8,318

WP-03 Vertical 13,650 4,758 7,254 1,531 7,438

WP-04 Vertical 15,961 7,249 13,378 902 7,083

WP-04 Horizontal 16,099 7,210 13,260 1,139 6,470

WP-04 Fracturing 22,724 8,055 14,322 1,234 4,554

WP-04 Flowback 17,057 10,982 13,938 750 5,411

WP-04 Production 17,031 8,545 13,019 895 3,624

WP-05 Horizontal 9,394 3,181 7,236 724 5,552

WP-05 Fracturing 8,293 3,925 6,668 825 3,033

WP-06 Vertical 8,906 4,424 6,357 560 8,518

WP-06 Horizontal 8,280 4,756 6,097 356 8,562

WP-06 Flowback 8,231 4,722 6,014 464 5,037

WP-06 Fracturing 10,803 3,049 8,033 692 2,532

WP-07 Vertical 8,437 4,675 6,318 483 12,519

WP-08 Fracturing 7,454 3,710 5,387 470 4,602

WP-09 Fracturing 30,823 2,686 5,380 1,146 4,354

WP-10 Horizontal 15,258 8,924 12,916 970 3,440

WP-10 Flowback 16,013 8,508 13,817 790 1,856

WP-10 Production 16,528 10,447 13,257 835 2,946

WP-11 Vertical 15,603 10,050 12,412 771 3,091

WP-11 Horizontal 14,781 4,368 12,075 1,252 2,960

WP-11 Production 13,505 9,914 12,281 503 1,168

WP-12 Vertical 11,479 5,543 8,005 1,144 3,204

WP-12 Horizontal 11,360 5,328 8,034 1,073 3,525

WP-13 Vertical 15,088 8,068 13,096 628 2,924

WP-13 Horizontal 15,357 8,119 12,916 966 3,234

WP-14 Vertical 6,772 1,992 3,854 684 2,840

WP-14 Horizontal 5,891 2,302 3,449 468 1,821

WP-14 Flowback 7,421 3,181 4,421 648 3,273

WP-15 Vertical 8,557 4,398 6,093 573 2,230

WP-16 Production 10,833 4,623 7,753 1,361 290

WP-17 Production 8,797 4,183 6,179 907 277

WP-19 Production 7,046 2,494 4,314 1,013 238

WP-20 Production 5,422 2,790 4,166 537 366
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-20

Table 3-3. Gross Gamma Scan Results Summarya

Site Phase Scan Maxb

(cpm)

Scan Minb

(cpm)

Scan

Averageb

(cpm)

Scan

Std Dev 

(cpm)

No. Data 

Points

WP-21 Production 5,307 2,677 3,870 572 182

a Gross gamma scans were performed on site ground surfaces outside facilities, structures, and systems,

and include soil, asphalt, gravel, and concrete matrices.

bConvert count rate data to exposure rate by dividing count rate by 800 to yield μR/hr.

Table 3-4. Results Summary of NaI Count Rate Data Converted to Exposure Rates

Site Phase Scan Max 

(μR/hr)

Scan Min 

(μR/hr)

Scan Average 

(μR/hr)

Scan Std Dev 

(μR/hr)

No. Data 

Points

WP-01 Fracturing 20.8 9.00 16.3 1.70 4,857

WP-01 Flowback 21.6 8.30 18.1 1.60 4,474

WP-01 Production 20.8 11.3 17.2 1.30 4,891

WP-02 Horizontal 11.7 5.30 6.70 1.30 8,318

WP-03 Vertical 17.1 5.90 9.10 1.90 7,438

WP-04 Vertical 20.0 9.10 16.7 1.10 7,083

WP-04 Horizontal 20.1 9.00 16.6 1.40 6,470

WP-04 Fracturing 28.4 10.1 17.9 1.50 4,554

WP-04 Flowback 21.3 13.7 17.4 0.900 5,411

WP-04 Production 21.3 10.7 16.3 1.10 3,624

WP-05 Horizontal 11.7 4.00 9.00 0.900 5,552

WP-05 Fracturing 10.4 4.90 8.30 1.00 3,033

WP-06 Vertical 11.1 5.50 7.90 0.700 8,518

WP-06 Horizontal 10.4 5.90 7.60 0.400 8,562

WP-06 Flowback 10.3 5.90 7.50 0.600 5,037

WP-06 Fracturing 13.5 3.80 10.0 0.900 2,532

WP-07 Vertical 10.5 5.80 7.90 0.600 12,519

WP-08 Fracturing 9.30 4.60 6.70 0.600 4,602

WP-09 Fracturing 38.5 3.40 6.70 1.40 4,354

WP-10 Horizontal 19.1 11.2 16.1 1.20 3,440

WP-10 Flowback 20.0 10.6 17.3 1.00 1,856

WP-10 Production 20.7 13.1 16.6 1.00 2,946

WP-11 Vertical 19.5 12.6 15.5 1.00 3,091

WP-11 Horizontal 18.5 5.50 15.1 1.60 2,960

WP-11 Production 16.9 12.4 15.4 0.600 1,168

WP-12 Vertical 14.3 6.90 10.0 1.40 3,204

WP-12 Horizontal 14.2 6.70 10.0 1.30 3,525

WP-13 Vertical 18.9 10.1 16.4 0.800 2,924

WP-13 Horizontal 19.2 10.1 16.1 1.20 3,234
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-21

Table 3-4. Results Summary of NaI Count Rate Data Converted to Exposure Rates

Site Phase Scan Max 

(μR/hr)

Scan Min 

(μR/hr)

Scan Average 

(μR/hr)

Scan Std Dev 

(μR/hr)

No. Data 

Points

WP-14 Vertical 8.5 2.50 4.80 0.900 2,840

WP-14 Horizontal 7.4 2.90 4.30 0.600 1,821

WP-14 Flowback 9.3 4.00 5.50 0.800 3,273

WP-15 Vertical 10.7 5.50 7.60 0.700 2,230

WP-16 Production 13.5 5.80 9.70 1.70 290

WP-17 Production 11.0 5.20 7.70 1.10 277

WP-19 Production 8.8 3.10 5.40 1.30 238

WP-20 Production 6.8 3.50 5.20 0.700 366

WP-21 Production 6.6 3.30 4.80 0.700 182

Table 3-5. Vertical Solids, Drill Cuttings – Gamma Spectroscopy Results

Sample ID Ra-226 

(pCi/g)

Ra-228 

(pCi/g)

K-40 

(pCi/g)

U-238 

(pCi/g)

U-235 

(pCi/g)

Th-232 

(pCi/g)

WP-03-SL-038 2.09 1.21 23.4 < 0.370 0.127 1.18

WP-04-SL-001 1.99 < 0.181 9.01 < 0.900 < 0.037 < 0.181

WP-04-SL-002 2.09 1.09 20.2 < 0.617 < 0.149 1.07

WP-04-SL-003 2.04 1.16 20.3 < 0.616 < 0.033 1.14

WP-04-SL-004 2.34 1.10 18.1 < 0.553 < 0.181 1.08

WP-04-SL-005 2.39 1.20 20.2 1.67 < 0.029 1.18

WP-04-SL-006 2.11 1.23 24.4 0.827 < 0.061 1.20

WP-04-SL-007 2.05 0.994 22.5 < 0.934 < 0.070 0.971

WP-04-SL-008 2.75 1.19 23.6 1.30 0.097 1.16

WP-05-SL-028 2.13 1.08 21.6 1.56 < 0.138 1.05

WP-05-SL-029 1.75 1.07 17.3 < 1.31 0.198 1.05

WP-05-SL-030 1.61 0.939 15.9 < 0.565 < 0.092 0.920

WP-05-SL-031 1.81 1.05 21.7 0.835 < 0.107 1.03

WP-05-SL-033 1.84 0.701 12.6 < 1.62 < 0.136 0.687

WP-06-SL-014 2.93 1.06 22.7 1.27 0.178 1.05

WP-06-SL-015 2.22 1.04 21.0 < 0.749 < 0.165 1.03

WP-06-SL-016 3.21 0.885 26.9 2.07 < 0.031 0.871

WP-06-SL-017 2.73 0.991 24.0 < 0.571 0.166 0.976

WP-06-SL-018 0.900 0.181 3.26 < 1.13 < 0.081 0.177

WP-06-SL-019 1.19 0.242 6.81 0.469 < 0.058 0.238

WP-06-SL-020 5.15 0.654 8.90 < 0.923 < 0.096 0.642

WP-06-SL-021 0.698 0.107 18.8 0.164 0.016 < 0.006

WP-06-SL-022 2.96 0.802 18.4 1.29 < 0.121 0.782
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-22

Table 3-5. Vertical Solids, Drill Cuttings – Gamma Spectroscopy Results

Sample ID Ra-226 

(pCi/g)

Ra-228 

(pCi/g)

K-40 

(pCi/g)

U-238 

(pCi/g)

U-235 

(pCi/g)

Th-232 

(pCi/g)

WP-06-SL-023 0.899 0.208 4.97 < 1.29 < 0.097 0.197

WP-06-SL-024 1.79 0.416 12.3 < 0.790 < 0.067 0.407

WP-06-SL-025 2.94 0.769 18.4 0.987 < 0.025 0.751

WP-06-SL-026 2.24 0.592 14.2 < 1.21 < 0.171 0.578

WP-07-SL-039 2.03 1.09 20.1 < 1.45 < 0.194 1.07

WP-07-SL-040 2.43 1.32 23.6 0.788 0.025 1.29

WP-07-SL-041 1.33 1.33 20.8 < 0.869 < 0.172 1.30

WP-10-SL-045 1.94 0.885 16.5 0.959 < 0.106 0.866

WP-11-SL-047 2.32 0.472 12.7 < 0.949 < 0.082 0.191

WP-12-SL-052 17.2 2.80 17.6 < 3.01 < 0.311 2.74

WP-12-SL-053 1.39 1.39 16.6 < 2.25 < 0.302 1.37

WP-13-SL-059 1.83 1.09 20.4 < 1.75 < 0.231 1.07

WP-14-SL-073 6.97 2.23 20.9 < 1.54 < 0.210 2.18

WP-14-SL-074 2.88 0.140 22.2 1.41 0.104 1.37

WP-15-SL-075 7.82 2.48 19.5 < 1.39 < 0.126 2.45

Average 2.82 1.01 18.0 0.960 0.085 1.01

Std. Dev. 2.79 0.572 5.64 0.484 0.046 0.555

Median 2.10 1.06 19.8 0.819 0.074 1.05

Minimum 0.698 0.107 3.26 0.164 0.016 0.110

Maximum 17.2 2.80 26.9 2.07 0.198 2.74

a Values reported as < are the method MDC.

bDuring the calculations to convert from raw counts to dpm, the calculated value was compared to half of 

the MDC. If the value was below this number, half of the MDC was inserted into the tables. Where the 

standard deviation is zero and the minimum, maximum, and average are the same, then all measurements 

were below half of the MDC.

Table 3-6. XRF Uranium and Thorium for Vertical Cuttings

Sample ID Date Formation

Thorium 

Result 

(ppm)

Thorium 

Error 

(ppm)

Th-232 

(pCi/g)

Uranium 

Result 

(ppm)

Uranium 

Error 

(ppm)

U-238 

(pCi/g)

WP-03-SL-038 07/26/13 Varies 20.1 0.400 2.21 2.90 0.200 0.969

WP-04-SL-001 06/17/13 Varies 17.9 0.400 1.97 5.30 0.300 1.77

WP-04-SL-002 06/17/13 Varies 16.4 0.400 1.80 3.00 0.200 1.00

WP-04-SL-003 06/17/13 Varies 17.5 0.400 1.93 4.00 0.300 1.34

WP-04-SL-004 06/17/13 Varies 15.5 0.400 1.71 3.60 0.200 1.20

WP-04-SL-005 06/17/13 Varies 16.0 0.400 1.76 2.60 0.200 0.868

WP-04-SL-006 06/17/13 Varies 18.3 0.400 2.01 4.20 0.300 1.40
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-23

Table 3-6. XRF Uranium and Thorium for Vertical Cuttings

Sample ID Date Formation

Thorium 

Result 

(ppm)

Thorium 

Error 

(ppm)

Th-232 

(pCi/g)

Uranium 

Result 

(ppm)

Uranium 

Error 

(ppm)

U-238 

(pCi/g)

WP-04-SL-007 06/17/13 Varies 14.5 0.400 1.60 3.00 0.200 1.00

WP-04-SL-008 06/17/13 Varies 16.8 0.400 1.85 5.30 0.300 1.77

WP-05-SL-028 07/08/13 Varies 17.4 0.400 1.91 4.50 0.300 1.50

WP-05-SL-029 07/08/13 Varies 15.5 0.400 1.71 3.70 0.200 1.24

WP-05-SL-030 07/08/13 Varies 14.5 0.400 1.60 3.50 0.200 1.17

WP-05-SL-031 07/08/13 Varies 16.5 0.400 1.82 2.60 0.200 0.868

WP-05-SL-033 07/08/13 Varies 11.2 0.400 1.23 2.30 0.200 0.768

WP-06-SL-014 07/01/13 Varies 16.5 0.400 1.82 6.40 0.300 2.14

WP-06-SL-015 07/01/13 Varies 17.8 0.400 1.96 3.80 0.300 1.27

WP-06-SL-016 07/01/13 Varies 15.2 0.400 1.67 7.10 0.300 2.37

WP-06-SL-017 07/01/13 Varies 16.3 0.400 1.79 6.10 0.300 2.04

WP-06-SL-018 07/01/13 Varies 6.50 0.400 0.715 3.00 0.200 1.00

WP-06-SL-019 07/01/13 Varies 8.60 0.400 0.946 2.80 0.200 0.935

WP-06-SL-020 07/01/13 Varies 10.9 0.400 1.20 13.4 0.500 4.48

WP-06-SL-021 07/01/13 Varies 8.50 0.400 0.935 4.40 0.200 1.47

WP-06-SL-022 07/01/13 Varies 15.6 0.400 1.72 5.80 0.300 1.94

WP-06-SL-023 07/01/13 Oriskany 6.30 0.300 0.693 1.50 0.100 0.501

WP-06-SL-024 07/08/13 Varies 11.5 0.400 1.27 4.80 0.300 1.60

WP-06-SL-025 07/08/13 Varies 16.0 0.400 1.76 5.40 0.300 1.80

WP-06-SL-026 07/08/13 Varies 17.7 0.500 1.95 8.80 0.500 2.94

WP-07-SL-039 08/05/13 Varies 17.3 0.400 1.90 2.50 0.200 0.835

WP-07-SL-040 08/05/13 Varies 17.8 0.400 1.96 1.50 0.100 0.501

WP-07-SL-041 08/05/13 Varies 17.7 0.400 1.95 2.30 0.200 0.768

WP-10-SL-045 08/26/13 Varies 11.8 0.400 1.30 3.00 0.200 1.00

WP-11-SL-047 08/27/13 Varies 7.00 0.400 0.770 2.40 0.100 0.802

WP-12-SL-052 09/05/13 Varies 17.7 0.500 1.95 12.4 0.500 4.14

WP-12-SL-053 09/05/13 Varies 17.9 0.400 1.97 6.30 0.300 2.10

WP-13-SL-059 10/15/13 Varies 16.2 0.400 1.78 2.00 0.200 0.668

WP-14-SL-073 01/31/14 Varies 17.1 0.400 1.88 3.10 0.200 1.04

WP-14-SL-074 01/31/14 Varies 17.3 0.400 1.90 3.20 0.200 1.07

Average 15.0 1.64 4.39 1.47

Std. Dev. 3.66 0.403 2.64 0.881

Median 16.3 1.79 3.60 1.20

Minimum 6.30 0.693 1.50 0.501

Maximum 20.1 2.21 13.4 4.48
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-24

Table 3-7. Horizontal Solids, Drill Cuttings – Uranium Series Gamma Spectroscopy Results

Sample ID Ra-226 

(pCi/g)

Ra-228 

(pCi/g)

K-40 

(pCi/g)

U-238 

(pCi/g)

U-235 

(pCi/g)

Th-232 

(pCi/g)

WP-02-SL-036 13.0 0.621 18.3 4.96 0.789 0.608

WP-03-SL-065 9.76 0.797 26.2 4.19 0.265 0.786

WP-04-SL-009 3.69 0.581 12.6 0.803 0.130 0.568

WP-04-SL-010 3.96 0.535 12.6 0.917 0.240 0.524

WP-04-SL-011 2.37 0.668 16.8 0.575 0.144 0.654

WP-04-SL-012 5.43 0.727 15.3 < 0.684 < 0.046 0.712

WP-05-SL-027 3.31 0.772 18.3 1.88 0.201 0.755

WP-05-SL-032 1.50 0.711 14.2 < 2.09 < 0.036 0.696

WP-05-SL-034 3.17 0.861 20.1 < 1.32 < 0.085 0.841

WP-06-SL-037 1.17 0.346 6.33 < 0.731 < 0.085 0.339

WP-10-SL-048 4.92 0.694 13.9 < 0.968 < 0.038 0.680

WP-11-SL-068 1.06 0.241 7.41 < 0.835 < 0.091 0.237

WP-12-SL-055 < 0.183 < 0.031 1.47 < 0.485 < 0.058 < 0.031

WP-12-SL-056 3.56 0.535 11.7 < 0.600 < 0.026 0.527

WP-13-SL-062 10.3 0.487 8.70 3.11 0.391 0.478

WP-14-SL-077 8.09 0.702 17.5 2.78 0.384 0.689

WP-14-SL-078 9.60 0.828 20.4 3.09 0.302 0.813

WP-14-SL-079 8.97 1.16 16.7 2.24 0.277 1.14

Average 5.22 0.627 15.3 1.76 0.223 0.615

Std. Dev. 3.80 0.254 7.13 1.36 0.180 0.249

Median 3.83 0.681 16.0 1.21 0.211 0.667

Minimum 0.092 0.016 1.47 0.243 0.029 0.016

Maximum 13.0 1.16 31.5 4.96 0.789 1.14
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-25

Table 3-8. XRF Uranium and Thorium for Horizontal Cuttings

Sample ID Date

Target 

Formation / 

Gas Type

Thorium 

Result 

(ppm)

Thorium 

Error 

(ppm)

Th-232 

(pCi/g)

Uranium 

Result 

(ppm)

Uranium 

Error 

(ppm)

U-238 

(pCi/g)

WP-02-SL036 07/24/13 Marcellus / 

Wet 12.2 0.400 1.34 28.6 0.500 9.55

WP-03-SL065 11/08/13 Marcellus / 

Wet 11.8 0.400 1.30 20.1 0.600 6.71

WP-04-SL009 06/20/13 Marcellus / 

Dry 12.0 0.500 1.32 8.70 0.400 2.91

WP-04-SL010 06/20/13 Marcellus / 

Dry 10.8 0.500 1.19 9.90 0.400 3.31

WP-04-SL011 06/20/13 Marcellus / 

Dry 12.5 0.400 1.38 5.90 0.300 1.97

WP-04-SL012 06/20/13 Marcellus / 

Dry 12.4 0.400 1.36 14.6 0.500 4.88

WP-05-SL027 07/08/13 Burkett / Wet 16.2 0.400 1.78 9.70 0.400 3.24

WP-05-SL032 07/08/13 Burkett / Wet 11.1 0.400 1.22 5.20 0.300 1.74

WP-05-SL034 07/08/13 Burkett / Wet 16.4 0.500 1.80 6.60 0.400 2.20

WP-06-SL037 07/25/13 Utica / Wet 17.4 1.30 1.91 80.8 1.30 27.0

WP-10-SL048 08/30/13 Marcellus / 

Dry 13.8 0.800 1.52 49.4 1.00 16.5

WP-11-SL068 11/14/13 Utica / Dry 7.70 0.500 0.847 17.6 0.500 5.88

WP-12-SL055 09/11/13 Marcellus / 

Dry 13.0 0.800 1.43 11.3 0.500 3.77

WP-12-SL056 09/11/13 Marcellus / 

Dry 20.3 1.20 2.23 36.6 1.20 12.2

WP-13-SL062 10/21/13 Marcellus / 

Dry 9.40 0.500 1.03 33.1 0.6 11.1

WP-14-SL077 02/07/14 Marcellus / 

Dry 11.0 0.500 1.21 31.4 0.700 10.5

WP-14-SL078 02/07/14 Marcellus / 

Dry 13.3 0.500 1.46 33.8 0.700 11.3

WP-14-SL079 02/07/14 Marcellus / 

Dry 11.7 0.700 1.29 49.4 0.900 16.5

Average 12.9 1.42 25.2 8.40

Std. Dev. 3.01 0.331 20.0 6.70

Median 12.3 1.35 18.9 6.30

Minimum 7.70 0.847 5.20 1.74

Maximum 20.3 2.23 80.8 27.0
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-26

Table 3-9. Drilling Solids, Mud – Gamma Spectroscopy Results

Sample ID Ra-226 

(pCi/g)

Ra-228 

(pCi/g)

K-40 

(pCi/g)

U-238 

(pCi/g)

U-235 

(pCi/g)

Th-232 

(pCi/g)

WP-03-SL-066 1.51 0.178 4.93 < 0.436 < 0.085 0.176

WP-04-SL-013 1.58 0.221 4.31 < 0.866 < 0.073 0.216

WP-05-SL-035 0.675 0.182 3.54 < 0.375 < 0.054 0.179

WP-10-SL-046 3.66 0.266 6.91 < 0.640 < 0.034 0.261

WP-10-SL-049 3.35 0.335 7.32 < 0.732 < 0.035 < 0.870

WP-11-SL-069 1.04 0.195 3.84 < 0.673 < 0.058 0.191

WP-12-SL-054 1.28 0.122 1.47 1.10 < 0.081 0.120

WP-13-SL-060 2.78 0.296 5.96 < 0.692 0.086 0.290

WP-13-SL-063 3.72 0.328 6.53 0.700 0.143 0.322

Average 2.18 0.236 4.98 0.651 0.063 0.243

Std. Dev. 1.20 0.074 1.89 0.504 0.038 0.095

Median 1.58 0.221 4.93 0.433 0.043 0.216

Minimum 0.675 0.122 1.47 0.188 0.027 0.120

Maximum 3.72 0.335 7.32 1.73 0.143 0.435

Table 3-10. Proppant Sand – Gamma Spectroscopy Results

Sample ID Ra-226 

(pCi/g)

Ra-228 

(pCi/g)

K-40 

(pCi/g)

U-238 

(pCi/g)

U-235 

(pCi/g)

Th-232 

(pCi/g)

WP-04-SL-050 0.180 0.053 0.733 0.139 < 0.025 0.047

WP-05-SL-058 0.225 0.135 7.25 < 0.200 < 0.037 0.115

WP-06-SL-070 0.170 0.026 0.069 0.323 < 0.018 0.025

WP-08-SL-044 0.246 0.065 0.162 < 0.020 < 0.004 0.045

WP-09-SL-043 0.301 0.045 0.199 < 0.426 < 0.050 0.044

WP-10-SL-067 0.218 0.018 0.136 < 0.369 < 0.036 0.018

WP-11-SL-072 0.275 0.025 0.070 < 0.203 < 0.033 0.025

WP-12-SL-064 0.358 0.038 0.386 < 0.426 < 0.042 0.037

WP-14-SL-081 0.266 < 0.026 4.99 < 0.442 < 0.035 0.102

WP-25-SL-042 0.188 0.018 < 0.061 < 0.267 < 0.029 < 0.013

Average 0.243 0.044 1.40 0.157 0.015 0.046

Std. Dev. 0.059 0.036 2.55 0.091 0.006 0.035

Median 0.236 0.032 0.181 0.159 0.017 0.041

Minimum 0.170 0.013 0.031 0.010 0.002 0.007

Maximum 0.358 0.135 7.25 0.323 0.025 0.115
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-27

Table 3-11. Flowback Solids, Sand – Gamma Spectroscopy Results

Sample ID Ra-226 

(pCi/g)

Ra-228 

(pCi/g)

K-40 

(pCi/g)

U-238 

(pCi/g)

U-235 

(pCi/g)

Th-232 

(pCi/g)

WP-04-SL-061 7.73 0.619 0.659 < 1.86 < 0.199 0.609

WP-09-SL-057 0.763 0.194 0.457 < 0.711 < 0.083 0.191

WP-11-SL-080 2.76 0.611 1.68 < 0.783 < 0.091 0.603

WP-12-SL-071 2.58 0.353 0.597 < 0.985 < 0.080 0.343

Average 3.46 0.444 0.848 0.542 0.057 0.437

Std. Dev. 2.99 0.208 0.561 0.265 0.029 0.205

Median 2.67 0.482 0.628 0.442 0.044 0.473

Minimum 0.763 0.194 0.457 0.356 0.040 0.191

Maximum 7.73 0.619 1.68 0.930 0.100 0.609

Table 3-12. Drilling Fluids – Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross Alphaa

(pCi/L)

Gross Betaa

(pCi/L)

WP-02-LQ-002 4,690 372 9,910 ND ND

WP-06-LQ-001 1,510 162 4,340 1,580 3,940

WP-06-LQ-003 2,010 216 5,220 ND ND

WP-12-LQ-009 1,800 184 420 3,820 1,250

WP-14-LQ-026 4,940 466 11,400 ND ND

Average 2,990 280 5,530 2,420 2,677

Std. Dev. 1,680 133 3,550 992 1,163

Median 2,010 216 5,220 2,142 2,595

Minimum 1,510 162 420 1,580 1,250

Maximum 4,940 466 11,400 3,820 3,940

aND – Sample Matrix was not suitable for analysis.
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-28

Table 3-13. Fracturing Fluids – Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross Alpha 

(pCi/L)

Gross Beta 

(pCi/L)

WP-04-LQ-008 21,000 1,640 < 565 37,000 11,200

WT-05-LQ-013 872 78.0 195 1,870 398

WP-06-LQ-016 64.0 < 9.00 < 21.0 < 1.39 4.41

WP-08-LQ-007 3,080 723 444 5,020 1,610

WP-09-LQ-006 2,000 442 338 3,400 < 879

WP-10-LQ-015 10,300 600 < 298 13,500 2,310

WP-11-LQ-023 115 14.0 44.0 < 3.76 < 1.63

WP-14-LQ-046 2,270 189 456 5,760 1,200

WP-14-LQ-047 2,160 218 423 5,650 1,010

WP-19-LQ-004 16,200 1,250 435 54,100 14,900

WP-19-LQ-005 105 < 9.00 25.0 < 113 < 186

Average 5,290 469 255 11,500 3,020

Std. Dev. 7,250 547 178 17,700 5,080

Median 2,160 218 283 5,020 1,010

Minimum 64.0 4.50 10.5 0.695 0.815

Maximum 21,000 1,640 456 54,100 14,900

Table 3-14. Flowback Fluids – Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross Alpha 

(pCi/L)

Gross Beta 

(pCi/L)

WP-01-LQ-010 7,310 589 151 15,300 4,070

WP-04-LQ-014 25,500 1,740 500 71,000 21,300

WP-06-LQ-017 551 248 416 < 576 742

WP-08-LQ-012 4,280 1,140 500 7,270 1,820

WP-09-LQ-011 2,880 863 448 10,700 4,380

WP-10-LQ-045 8,690 633 2,630 11,100 1,960

WP-11-LQ-035 1,540 564 927 2,250 1,320

WP-12-LQ-022 4,550 507 < 177 10,100 2,440

WP-14-LQ-052 21,100 1,430 461 32,000 5,400

Average 8,490 857 680 17,800 4,830

Std. Dev. 8,840 486 769 21,900 6,370

Median 4,550 633 461 10,700 2,440

Minimum 551 248 88.5 288 742

Maximum 25,500 1,740 2,630 71,000 21,300
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-29

Table 3-15. Unfiltered Produced Waters – Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross 

Alpha 

(pCi/L)

Gross 

Beta 

(pCi/L)

WP-01-LQ-048 Unconventional 2,050 366 132 3,890 < 225

WP-04-LQ-039 Unconventional 26,600 1,900 328 30,000 7,600

WP-08-LQ-021 Unconventional 5,020 1,280 592 11,300 3,270

WP-09-LQ-019 Unconventional 4,490 1,140 571 9,760 2,570

WP-10-LQ-050 Unconventional 7,730 434 191 14,000 3,620

WP-10-LQ-055 Unconventional 6,710 470 149 41,700 4,560

WP-11-LQ-043 Unconventional 1,700 636 852 2,420 1,500

WP-12-LQ-041 Unconventional 14,500 1,710 408 21,800 6,810

WP-16-LQ-027 Conventional 819 896 220 < 2570 1,140

WP-19-LQ-029 Conventional < 81.0 26.0 103 < 465 < 402

WP-20-LQ-031 Conventional 145 42.0 129 < 2440 < 987

WP-21-LQ-033 Conventional 340 214 < 31.0 < 1230 < 830

WP-05-LQ-037 Unconventional 6,300 941 667 10,700 2,300

Average 5,880 773 335 11,500 2,660

Std. Dev. 7,450 604 260 12,800 2,460

Median 4,490 636 220 9,760 2,300

Minimum 40.5 26.0 15.5 233 113

Maximum 26,600 1,900 852 41,700 7,600

Table 3-16. Filtered Produced Waters – Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross 

Alpha 

(pCi/L)

Gross 

Beta 

(pCi/L)

WP-01-LQ-049 Unconventional 1,930 373 129 2,750 933

WP-04-LQ-040 Unconventional 24,100 1,860 323 33,000 7,180

WP-08-LQ-020 Unconventional 4,940 1,350 518 11,200 4,050

WP-09-LQ-018 Unconventional 4,470 1,240 560 8,780 3,040

WP-10-LQ-051 Unconventional 8,060 466 164 19,900 4,050

WP-10-LQ-054 Unconventional 7,130 479 3,950 10,900 3,530

WP-11-LQ-044 Unconventional 1,520 602 751 2,440 1,500

WP-12-LQ-042 Unconventional 15,100 1,610 389 18,000 4,050

WP-16-LQ-028 Conventional 849 851 < 34.0 1,440 1,610

WP-19-LQ-030 Conventional 87.0 44.0 71.0 < 608 < 420

WP-20-LQ-032 Conventional 106 48.0 129 < 1,040 < 857

WP-21-LQ-034 Conventional 292 210 144 < 1,860 < 863

WP-05-LQ-038 Unconventional 6,720 883 485 11,400 3,370
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-30

Table 3-16. Filtered Produced Waters – Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross 

Alpha 

(pCi/L)

Gross 

Beta 

(pCi/L)

Average 5,970 770 587 9,900 2,790

Std. Dev. 6,980 591 1,030 9,970 2,040

Median 4,470 602 323 9,840 3,210

Minimum 87.0 44.0 17.0 304 210

Maximum 24,100 1,860 3,950 33,000 7,180

Table 3-17. Ambient Radon at Well Sites During Flowback

Sample ID County Date Radon Conc. +/- 2 S.D. 

(pCi/L) MDC (pCi/L)

WP-01-RA Sullivan 9/2013

<0.300 +/- 0.000 0.300

0.800 +/- 0.000 0.300

0.500 +/- 0.400 0.300

<0.300 +/- 0.000 0.300

<0.300 +/- 0.000 0.300

WP-09-RA Washington 9/2013

0.700 +/- 0.600 0.300

0.600 +/- 0.200 0.300

0.600 +/- 0.200 0.300

1.70 +/- 1.60 0.300

WP-08-RA Washington 9/2013

0.500 +/- 0.800 0.300

0.200 +/- 0.200 0.300

0.600 +/- 0.600 0.300

0.700 +/- 0.400 0.300

WP-04-RA Tioga 10/2013

0.500 +/- 0.200 0.300

0.200 +/- 0.200 0.300

0.500 +/- 0.600 0.300

0.700 +/- 0.200 0.300

E-PERM samples with short-term electrets were deployed. MDC for a four-day exposure at 50 percent 

error is 0.300 pCi/L.
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-31

Table 3-18. Natural Gas Samples from Production Sites

Sample ID County Gas Source Radon Conc. +/- 2 S.D. 

(pCi/L)

MDA 

(pCi/L)

WP 08 RG Washington Marcellus Shale 79.6 +/- 0.800 0.300

WP 09 RG Washington Marcellus Shale 78.8 +/- 4.20 0.300

WP 22 RG Tioga Marcellus Shale 42.8 +/- 0.200 0.100

WP 23 RG Tioga Marcellus Shale 39.6 +/- 0.800 0.200

WP 24 RG Tioga Marcellus Shale 73.8 +/- 0.400 0.200

WP 25 RG Tioga Marcellus Shale 44.4 +/- 2.60 0.200

WP 26 RG Lycoming Oriskany Sandstone 19.9 +/- 0.200 0.200

WP 27 RG Tioga Marcellus Shale 38.4 +/- 3.40 0.300

WP 28 RG Tioga Marcellus Shale 40.8 +/- 5.20 0.400

WP 16 RG Washington Marcellus Shale 50.0 +/- 5.20 0.300

WP 17 RG Washington Marcellus Shale 49.5 +/- 5.80 0.500

WP 19 RG McKean Upper Devonian Shale 18.3 +/- 4.40 0.400

WP 20 RG McKean Upper Devonian Shale 88.2 +/- 10.6 0.700

WP 21 RG Forest Upper Devonian Shale 92.2 +/- 6.40 0.400

WP 04 RG Tioga Marcellus Shale 49.6 +/- 29.6 1.20

WP 05 RG McKean Marcellus Shale 148 +/- 15.6 1.50

WP 12 RG Lycoming Marcellus Shale 37.6 +/- 33.4 2.20

WP 11 RG Tioga Utica 5.70 +/- 1.20 0.500

WP 29 RG Sullivan Marcellus Shale 23.4 +/- 4.00 0.240

WP 30 RG Bradford Marcellus Shale 25.5 +/- 2.70 0.200

WP 31 RG Bradford Marcellus Shale 3.00 +/- 1.20 0.300

WP 14 RG Jefferson Marcellus Shale 5.60 +/-0.100 0.140

Average 47.9

Median = 41.8

Standard Deviation 34.5

Note: All results adjusted to account for the fact that Rn was counted in methane, but the scintillation 

cells were calibrated for Rn in air. Range of  particles is greater in methane than in air. All results 

divided by 1.054, according to Jenkins et. al., Health Physics, Vol. 106, No. 3, March 2014.
PA DEP TENORM Study Report – Section 3.0 Rev. 0

January 2015 3-32

Table 3-19. Thorium and Uranium XRF Data for Drill Cuttings By Formation

Formation

Thorium 

Result 

(ppm)

Th-232 

Concentration 

(pCi/g)

Uranium 

Result 

(ppm)

U-238 

Concentration 

(pCi/g)

U/Th U-238/ 

Th-232

Marcellus 13.8 1.52 49.4 16.5 3.58 10.9

Marcellus 13.0 1.43 11.3 3.77 0.870 2.64

Marcellus 20.3 2.23 36.6 12.2 1.80 5.48

Marcellus 9.40 1.03 33.1 11.1 3.52 10.7

Marcellus 11.8 1.30 20.1 6.71 1.70 5.16

Marcellus 12.0 1.32 8.70 2.91 0.730 2.20

Marcellus 10.8 1.19 9.90 3.31 0.920 2.78

Marcellus 12.5 1.38 5.90 1.97 0.470 1.43

Marcellus 12.4 1.36 14.6 4.88 1.18 3.59

Marcellus 11.7 1.29 49.4 16.5 4.22 12.8

Marcellus 13.3 1.46 33.8 11.3 2.54 7.73

Marcellus 11.0 1.21 31.4 10.5 2.85 8.67

Marcellus 12.2 1.34 28.6 9.55 2.34 7.13

Average 12.6 1.40 25.6 8.60 2.10 6.20

Median 12.2 1.30 28.6 9.60 1.80 5.50

Standard Deviation 2.57 0.280 15.0 5.01 1.23 3.72

Burket 16.2 1.78 9.70 3.24 0.600 1.82

Burket 16.4 1.80 6.60 2.20 0.400 1.22

Burket 11.1 1.22 5.20 1.74 0.470 1.42

Average 14.6 1.60 7.17 2.39 0.490 1.49

Median 16.2 1.78 6.60 2.20 0.470 1.42

Standard Deviation 3.00 0.330 2.30 0.770 0.100 0.300

Utica 7.70 0.850 17.6 5.88 2.29 6.92

Utica 17.4 1.91 80.8 27.0 4.64 14.1

Average 12.6 1.38 49.2 16.4 3.46 10.5

Median 12.6 1.38 49.2 16.4 3.46 10.5

Standard Deviation 6.86 0.750 44.7 14.9 1.67 5.10
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-1

4.0 WASTEWATER TREATMENT PLANTS

A total of 29 WWTPs were surveyed and/or sampled. This included 10 POTWs, 10 CWTs and

nine ZLDs. The results, by wastewater facility, are presented in this section.

4.1 Publicly Owned Treatment Works

A total of 10 POTWs were surveyed and/or sampled. There were three rounds of surveys

conducted over a seven-month period (April 2013 through October 2013); however, not all 

POTWs were sampled in all three rounds. Six of the 10 POTWs are considered influenced

(POTW-I) by having received wastewater from the O&G industry, mainly the effluent of 

CWTs. Four POTWs are considered non-influenced (POTW-N) by having never received 

wastewater from the O&G industry. As such, surveying was conducted for the 10 POTWs as 

follows:

 5 POTW-I’s were surveyed in all three rounds,

 1 POTW-I was surveyed in two rounds, and

 4 POTW-N’s were surveyed one time.

4.1.1 Radiological Survey Results

Radiological surveys were conducted at each POTW-I, resulting in four data sets:

 Removable / surface radioactivity measurements recorded in units of dpm/100 cm

2

 Total / surface radioactivity measurements recorded in units of dpm/100 cm

2

 Gross Gamma Radiation Scan measurements recorded in units of cpm

 Gamma Radiation Exposure Rate measurements recorded in units of μR/hr

4.1.1.1 Removable Alpha/Beta Surface Radioactivity Measurement Results

Measurements of removable radioactivity were performed to assess potential internal radiation 

exposures of workers through ingestion and/or inhalation. The results were evaluated using the 

RG 1.86 guidelines, Table 1. RG 1.86 requires that  and  surface radioactivity levels be 

evaluated separately. The primary emitter of concern is Ra-226, with a removable criterion of 

20 dpm /100 cm2. The primary  emitter of concern is Ra-228 of the natural Th decay series 

with a removable criterion of 200 dpm /100 cm2. The average removable  and  surface 

radioactivity levels at each WWTP were below the RG 1.86 criteria. The maximum removable 

 and  surface radioactivity levels were 22 dpm/100 cm2and 161 dpm/100 cm2. The results of 

removable  and  surface radioactivity for the POTW-I plants are presented in Table 4-1.

Individual removable  and  surface radioactivity measurement results are presented in 

Appendix D.

4.1.1.2 Total Alpha/Beta Surface Radioactivity Measurement Results

Measurements of total radioactivity were performed to assess potential internal radiation 

exposures of workers through ingestion and/or inhalation. The results were evaluated using the 

RG 1.86 guidelines, Table 1. RG 1.86 requires that  and  surface radioactivity levels be
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-2

evaluated separately. The primary emitter of concern is Ra-226, with a total surface 

radioactivity criterion of 100 dpm /100 cm2. The primary  emitter of concern is Ra-228 of the 

natural Th decay series with a total surface radioactivity criterion of 1,000 dpm /100 cm2. The 

maximum average total  and  surface radioactivity measured at any single facility were 

313 dpm/100 cm2and 10,000 dpm/100 cm2, respectively. The maximum total  and 

concentrations measured at any single facility were 1,190 dpm/100 cm2and 38,000 dpm/

100 cm

2

. The summary results of total  and  surface radioactivity for the POTW-I plants

surveyed are presented in Table 4-2. Individual total  and  surface radioactivity measurement 

results are presented in Appendix D.

4.1.1.3 Gross Gamma Radiation Scan Results

Gross gamma radiation scans recorded in cpm were performed on open land areas and accessible 

areas of the WWTPs to identify areas with elevated gross gamma radiation levels. Summary 

results for the POTW-I are presented in Table 4-3. The highest average count rate for the plants 

was 29,034 cpm, and the maximum count rate recorded was 205,446 cpm. A graphic display of 

the gamma radiation scan results (figures) at each facility was prepared using geographic 

information system (GIS) software. Figures are presented in Appendix E.

4.1.1.4 Gamma Radiation Exposure Rate Results Summary

Gross gamma radiation scan results in units of cpm presented in Table 4-3 were converted to 

R/hr using 800 cpm per R/hr, a conversion factor appropriate for Ra-226 gamma energy as 

detected with 2-inch by 2-inch NaI detectors, rounded to one significant figure (Table 6.4, NaI 

Scintillation Detector Scan MDCs for Common Radiological Contaminants, NUREG-1507, 

Minimum Detectable Concentrations With Typical Radiation Survey Instruments for Various 

Contaminants and Field Conditions, USNRC June 1998). Table 4-4 presents statistical results

for each POTW-I. The highest average gamma radiation exposure rate was 36.3 R/hr, and the 

maximum gamma radiation exposure rate measured was 257 R/hr.

4.1.2 Solid Sample Results

4.1.2.1 Filter Cake Samples 

Filter cakes were sampled at POTW-I and POTW-N plants and analyzed using gamma 

spectroscopy for U, Th, and Ac series decay chains. The gamma spectroscopy results are 

presented in Tables 4-5 and 4-6.

The analytical results for POTW-I plants presented in Table 4-5 show Ra-226 and Ra-228 are 

present above typical background concentrations in soil. The average Ra-226 result was 

20.1 pCi/g with a large variance in the distribution, and the maximum result was 55.6 pCi/g. The 

average Ra-228 result was 8.32 pCi/g, and the maximum result was 32.0 pCi/g Ra-228.

The radioactivity levels at POTW-N plants presented in Table 4-6 were also above typical 

background concentrations in soil with Ra-226 average and maximum results of 8.89 pCi/g and 

35.4 pCi/g. The average and maximum Ra-228 results were 2.13 pCi/g and 7.26 pCi/g.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-3

4.1.2.2 Sediment-Impacted Soil Samples

Sampling was performed at only three of the POTW-I plants due to limited accessibility at the 

other plants. A total of seven samples were collected at the effluent discharge points and 

analyzed for U, Th, and Ac series decay chains by gamma spectroscopy. The gamma 

spectroscopy results are presented in Table 4-7.

The analytical results for POTW-I sediment-impacted soil samples indicate Ra-226 and Ra-228

are present at concentrations above typical background in soil. The average Ra-226 result was 

9.00 pCi/g, and the maximum result was 18.2 pCi/g. The average Ra-228 result was 3.52 pCi/g,

and the maximum result was 6.25 pCi/g.

4.1.3 Liquid Sample Results

Influent and effluent liquid sampling was performed at six POTW-I plants and four POTW-N

plants. Filtered and unfiltered samples were analyzed for U, Th, and Ac decay series, and for 

gross / radioactivity levels. The filtered and unfiltered analyses are presented separately in 

Tables 4-8 through 4-15 for both influenced and non-influenced POTWs. A comparison of the 

influenced and non-influenced POTW results and the filtered and unfiltered sample results is 

presented in Section 4.1.5.1.

4.1.4 Indoor Radon Sampling Results

ATDs were deployed in the POTW-I plants at various indoor locations such as break rooms, 

labs, offices, etc., to measure Rn concentrations. The results were evaluated using the EPA 

Action Level of 4.0 pCi/L. The ATDs were deployed in late July or early August 2013 and were 

all recovered from the field in February 2014. The results ranged from 0.2 to 8.7 pCi/L. One 

result exceeded the action level. The results are presented in Table 4-16. The Rn analytical 

reports are presented in Appendix H.

4.1.5 POTW Data Comparisons

4.1.5.1 POTW-I / POTW-N Comparison

Thirty-two influent and effluent sample radionuclide and gross / concentration results from 

POTW-I’s and POTW-N’s were compared to determine if there was a difference in the 

radionuclide activity content. Tables 4-17 through 4-20 present and compare the average Ra 

concentration results and gross / concentration results from all influent and effluent filtered 

and unfiltered samples for all POTW-I and POTW-N plants. Twenty-nine of the 32 average 

concentration results for both filtered and unfiltered influent and effluent samples were higher 

for POTW-I plants than the POTW-N plants.

4.1.5.2 Radium-226/Radium-228 Sediment-Impacted Soil and Effluent Results Comparison

The sediment-impacted soil radioactivity levels were compared to filtered and unfiltered effluent 

results for Ra-226 and Ra-228 and are presented in Table 4-21. In cases where no results were 

reported for a member of the data pair (sediment-effluent pair), or when a result was reported as 

less than MDC, the data pair comparison was not evaluated.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-4

The sediment-impacted soil sample results are above typical background for soil. However, 

there is no readily apparent relationship between the sediment-impacted soil sample and effluent 

sample results. The effluent wastewater discharged over time may contribute to the activity in 

the sediment-impacted soil, but a correlation between the sediment-impacted soil activity and the 

effluent samples could not be made from the study as performed.

The ratio of Ra-226 to Ra-228 was also calculated for a variety of sample types including 

sediments, filtered effluents, and unfiltered effluents from POTWs and CWTs. The results are

presented in Table 4-22. The average ratio ranged from 2.4 to 11.4.

4.1.6 POTW Worker Exposure Assessment

4.1.6.1 External Gamma Radiation Exposure

The gamma radiation exposure rate survey results are provided in Section 4.1.1.4. The 

maximum average gamma radiation exposure rate measured at any of the POTW plants was

36.3 R/hr. The lowest background gamma radiation exposure rate measured at any of the sites 

was 5 R/hr. Assuming the time period of exposure is a full occupational year of 2,000 hours, 

the maximum average POTW annual external gamma radiation exposure was estimated as 

follows:

Maximum Average POTW External Gamma Radiation Exposure Estimate

(36.3 – 5) μR/hr x 2,000 hr/yr x (1 mrem/1,000 μR gamma) = 62.6 mrem/yr

This is an estimate of the maximum average gamma radiation exposure at a single facility based 

on 2,000 hours in one year. The result is less than the 100 mrem/yr dose equivalent limit for a 

member of the public. Actual exposure is dependent upon the actual exposure rates and 

occupancy time for individual workers.

The maximum gamma radiation exposure rate measured at the POTWs was 257 R/hr on 

contact with the outside of a wastewater tank. Consequently, the public dose limit of 100 mrem 

per year could potentially be reached by a person working 400 hours within the immediate 

proximity of the tank. Actual annual exposure for a POTW worker is dependent upon the 

exposure rates and time worked in proximity to the tank.

4.1.6.2 Internal Alpha/Beta Radiation Exposure

The total and removable / survey surface radioactivity summary results are provided in 

Sections 4.1.1.1 and 4.1.1.2. Nine of the 566  measurements and 68 of the 566  measurements 

of total surface radioactivity exceeded the RG 1.86 criteria. One of the 286 removable 

measurements and none of the 286 removable  measurements exceeded the RG 1.86 criteria.

Fixed or removable  and  surface radioactivity may present a potential inhalation or ingestion 

hazard if disturbed during routine system maintenance.
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4.1.6.3 Internal Radon Exposure

The Rn measured in indoor air averaged 1.7 pCi/L. The average is above the average indoor 

level of 1.3 pCi/L in the U.S. as reported by EPA.

4.1.7 POTW Radiological Environmental Impacts

Seven sediment-impacted soil samples were collected at the effluent discharge points of three of 

the POTW-I’s. Radium-226 activity concentrations above typical soil background activity 

concentrations were identified in all sediment samples, with 156 pCi/g the maximum reported 

result.

The presence of Ra in sediment-impacted soil at effluent discharge points indicates effluent

wastewater contained Ra. Radium and gross  and  radioactivity were identified in effluent 

samples. Table 4-21 presents filtered and unfiltered effluent average sample results and 

sediment-impacted soil results for POTWs sampled during the study.

4.2 Centralized Wastewater Treatment Plants

Three survey rounds were conducted at nine of the 10 CWTs. The 10th facility was added after 

the first survey round was completed, resulting in only two surveys at that facility.

4.2.1 Survey Results

Radiological surveys were conducted at each CWT resulting in four data sets:

 Removable / surface radioactivity measurements recorded in units of dpm/100 cm

2

 Total / surface radioactivity measurements recorded in units of dpm/100 cm

2

 Gross Gamma Radiation Scan measurements recorded in units of cpm

 Gamma Radiation Exposure Rate measurements recorded in units of μR/hr

4.2.1.1 Removable Alpha/Beta Surface Radioactivity Measurement Results

Measurements of removable radioactivity were performed to evaluate potential internal radiation 

exposures of workers through ingestion and/or inhalation. The results were evaluated using the 

RG 1.86 surface radioactivity guidelines, Table 1. RG 1.86 requires that  and  surface 

radioactivity levels be evaluated separately. The primary emitter of concern is Ra-226, with a 

removable surface radioactivity criterion of 20 dpm /100 cm2. The primary  emitter of 

concern is Ra-228 of the natural Th decay series with a removable surface radioactivity criterion 

of 200 dpm /100 cm2. 

The average removable  and  surface radioactivity levels were all below the RG 1.86 criteria. 

The maximum removable  and  surface radioactivity levels were 38.1 dpm/100 cm2and 133

dpm/100 cm2. The summary results of removable  and  surface radioactivity are presented in 

Table 4-23. Individual removable  and  surface radioactivity measurement results are 

presented in Appendix D.
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4.2.1.2 Total Alpha/Beta Surface Radioactivity Measurement Results

Measurements of total  and  surface radioactivity were performed to evaluate potential 

internal radiation exposures of workers through ingestion and/or inhalation. The results were 

evaluated using the RG 1.86 surface radioactivity guidelines, Table 1. RG 1.86 requires that 

and  surface radioactivity levels be evaluated separately. The primary emitter of concern is 

Ra-226, with a total surface radioactivity criterion of 100 dpm /100 cm2. The primary  emitter 

of concern is Ra-228 of the natural Th decay series with a total surface radioactivity criterion of 

1,000 dpm /100 cm2.

Eighteen of the 31 average total  surface radioactivity measurements were below the RG 1.86 

surface radioactivity criterion. Three of the 31 average total  surface radioactivity 

measurements were below the RG 1.86 surface radioactivity criterion. The maximum total 

and  surface radioactivity levels were 3,220 dpm/100 cm2and 50,400 dpm/100 cm2. The 

summary results of total  and  surface radioactivity measurements are presented in 

Table 4-24. Individual total  and  surface radioactivity measurement results are presented in 

Appendix D.

4.2.1.3 Gross Gamma Radiation Scan Results

Gross gamma radiation scans recorded in cpm were performed on open land areas and accessible 

areas of the CWT facilities to identify any areas with levels above local background. The 

summary results of the gross gamma radiation scans for each plant are presented in Table 4-25.

The highest average count rate for the plants was 19,281 cpm, and the maximum count rate 

recorded was 401,688 cpm. A graphic display of the gamma radiation scan results at each 

facility was prepared using GIS software. The resulting figures are in Appendix E.

4.2.1.4 Gamma Radiation Exposure Rate Results Summary

Gross gamma radiation scan results in units of cpm presented in Table 4-25 were converted to 

R/hr by dividing by 800 cpm per R/hr, a conversion factor appropriate for Ra-226 gamma 

energy as detected with 2-inch by 2-inch NaI detectors rounded to one significant figure

(Table 6.4, NaI Scintillation Detector Scan MDCs for Common Radiological Contaminants, 

NUREG-1507, Minimum Detectable Concentrations With Typical Radiation Survey Instruments 

for Various Contaminants and Field Conditions, USNRC June 1998). Table 4-26 presents

statistical results for each CWT facility. The highest average gamma radiation exposure rate was 

24.1 R/hr, and the maximum gamma radiation exposure rate measured was 502 R/hr.

4.2.2 Solid Sample Results

4.2.2.1 Filter Cake Samples

Three survey rounds were conducted at nine of the 10 CWTs. The 10th facility was added after 

the first survey round was completed, resulting in only two surveys at that facility. Also, the 

10th facility is a primary treatment facility, so it does not produce a filter cake. A total of 25

filter cake samples were collected from the nine plants. The results are presented in Table 4-27.

The analytical results indicate all the CWT filter cake samples contain elevated Ra-226 and 
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Ra-228 above typical background levels for soil. The maximum results were 305 pCi/g of 

Ra-226 and 177 pCi/g of Ra-228.

4.2.2.2 Solids/Sediment Samples

Four of the CWTs surveyed and sampled as part of the study are permitted to discharge effluent

wastewater to the environment. If the discharge point was accessible, surface soil impacted by 

sediment was sampled. The gamma spectroscopy results are presented in Table 4-28. The 

Ra-226 results ranged from 2.50 to 421 pCi/g. The Ra-228 results ranged from 0.978 to 

86.9 pCi/g. Uranium and Th were also detected at surface soil typical background levels in some 

of the samples because of natural soil collected along with the sediment.

4.2.2.3 Solids/Biased Samples

Gamma radiation walkover scans identified areas with radioactivity above local background. At 

three of these locations, a biased soil sample was collected to determine the amount of activity at 

or near the surface. The gamma spectroscopy results are presented in Table 4-29. Radium 

above soil typical background levels to a maximum of 117 pCi/g Ra-226 and 83.1 pCi/g Ra-228 

was identified in biased soil samples.

4.2.3 Liquid Samples

Samples of influent and effluent, both filtered and unfiltered, were analyzed. Three survey 

rounds were conducted at nine of the 10 CWTs. The 10th facility was added after the first 

survey round was completed, resulting in only two surveys at that facility. Also, the 10th facility 

is only a primary treatment facility, with the influent and the effluent essentially the same.

Consequently, only the influent was sampled at the 10th facility. A total of 31 effluent and 

26 influent samples were collected for filtered and unfiltered analysis. The filtered and unfiltered 

analyses are presented separately. The gamma spectroscopy results, gross , and gross  are 

presented in Tables 4-30 through 4-33. Radium (Ra-226 and Ra-228) was routinely detected in 

all sample types with little difference between influent and effluent or between filtered and 

unfiltered results as presented for Ra-226 in Figure 4-1.

Figure 4-1. CWT Influent and Effluent Liquid Ra-226 Minimum, Maximum, and Average

Wastewater

Source Filtered or Not Min (pCi/L) Max (pCi/L) Ave (pCi/L)

Effluent Filtered 18.0 14,900 2,100

Effluent Unfiltered 42.0 15,500 1,840

Influent Filtered 57.0 14,100 2,350

Influent Unfiltered 17.5 13,400 1,870

4.2.4 Indoor Radon Sampling Results

ATDs were deployed in the CWT plants at various indoor locations such as break rooms, labs, 

offices, etc., and the results were evaluated using the EPA Action Level of 4.0 pCi/L. The 

results ranged from 0.9 to 5.0 pCi/L. One result exceeded the action level. The results of the 

analyses are presented in Table 4-34. The Rn analytical reports are presented in Appendix H.
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4.2.5 Filtered Versus Unfiltered Sample Data Evaluation

Appendix I presents a complete evaluation of filtered versus unfiltered liquid samples for the 

entire study. The conclusion from this evaluation is that there is no apparent trend or bias that 

filtering produces. There were some subsets of data where either the unfiltered results or the 

filtered results appear to be significantly higher. There was no statistically significant correlation 

found within any sample group. Because the liquid samples were preserved by addition of acid 

prior to filtering, the radioactive particulates may have entered solution and were therefore not 

removed by filtering.

4.2.6 CWT Exposure Assessment

4.2.6.1 CWT External Radiation Exposure

The maximum average gamma radiation exposure rate measured at any of the CWT plants was 

24.1 R/hr. The lowest background gamma radiation exposure rate measured at any of the sites 

was 5 R/hr. Assuming the time period of exposure is a full occupational year of 2,000 hours, 

the maximum average CWT annual external gamma radiation exposure was estimated as 

follows:

Maximum Average CWT External Gamma Radiation Exposure Estimate

(24.1 – 5) μR/hr x 2,000 hr/yr x (1 mrem/1,000 μR gamma) = 38 mrem/yr

This is an estimate of the maximum average gamma radiation exposure based on 2,000 hours in 

one year. The result is less than the 100 mrem/yr dose equivalent limit for a member of the 

public. Actual exposure is dependent upon the actual exposure rates and occupancy time for 

individual workers.

The maximum gamma radiation exposure rate measured was 502 rem/hr on contact with the 

outside of a wastewater tank. Work in proximity of the tank could potentially result in an 

exposure of 100 mrem in 200 hours of annual exposure or 10 percent of an employee’s 

2,000-hour occupational year. Actual annual exposure for a CWT worker is dependent upon 

actual exposure rates and actual time worked in the proximity of the tank.

4.2.6.2 CWT Potential Internal Alpha/Beta Radioactivity Exposure

The total and removable / surface radioactivity survey results are discussed in Sections 4.2.1.1 

and 4.2.1.2. One hundred eighty-six of the 777  measurements and 461 of the 777 

measurements of total surface radioactivity exceeded the RG 1.86 criteria. Seven of the 805 

removable  measurements and 6 of the 805 removable  measurements exceeded the RG 1.86 

criteria. The average of the  total surface radioactivity measurements exceeded the RG 1.86 

criteria in 10 of the 11 CWT facilities surveyed. The average of the  total surface radioactivity 

measurements exceeded the RG 1.86 criteria in four of the 11 CWT facilities surveyed. The 

corresponding removable radioactivity measurements are mostly less than the RG 1.86 criteria, 

indicating the total radioactive contamination measured is fixed to the surface and not 

immediately available for inhalation or ingestion. Fixed  and  surface radioactivity may 

present a potential inhalation or ingestion hazard if disturbed during routine system maintenance.
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4.2.6.3 Internal Radon Exposure

The Rn in ambient indoor area air averaged 2.0 pCi/L. The average is above the average typical 

background indoor level of 1.3 pCi/L in the U.S. as reported by EPA.

4.2.7 CWT Radiological Environmental Impacts

Sediment-impacted soil was collected at the accessible effluent discharge points at the CWTs. A 

total of nine samples were collected. Radium above typical soil background levels to a 

maximum of 508 pCi/g of total Ra was identified in the sediment-impacted soil samples.

Effluent wastewater also contained Ra and is the likely source of the Ra in sediment-impacted 

soil above soil typical background levels.

4.3 Zero Liquid Discharge Plants

4.3.1 Survey Results

Radiological surveys were conducted at each ZLD facility resulting in four data sets:

 Removable / surface radioactivity measurements recorded in units of dpm/100 cm

2

 Total / surface radioactivity measurements recorded in units of dpm/100 cm

2

 Gross Gamma Radiation Scan measurements recorded in units of cpm

 Gamma Radiation Exposure Rate measurements recorded in units of μR/hr

4.3.1.1 Removable Alpha/Beta Surface Radioactivity Measurement Results

Measurements of removable surface radioactivity were performed to evaluate potential internal 

radiation exposures of workers through ingestion and/or inhalation. The results were evaluated 

using the RG 1.86 guidelines, Table 1. RG 1.86 requires that  and  surface radioactivity levels 

be evaluated separately. The primary emitter of concern is Ra-226, with a removable surface 

radioactivity criterion of 20 dpm /100 cm2. The primary  emitter of concern is Ra-228 of the 

natural Th decay series with a removable surface radioactivity criterion of 200 dpm /100 cm2. 

The average removable  and  surface radioactivity levels were below the RG 1.86 criteria. 

The maximum removable  and  surface radioactivity levels were 294 dpm/100 cm2and 

342 dpm/100 cm2. The summary results of removable  and  surface radioactivity are 

presented in Table 4-35. Individual removable  and  surface radioactivity measurement 

results are presented in Appendix D.

4.3.1.2 Total Alpha/Beta Surface Radioactivity Measurement Results

Measurements of total  and  surface radioactivity were performed to evaluate potential 

internal radiation exposures of workers through ingestion and/or inhalation. The results were 

evaluated using the RG 1.86 guidelines, Table 1. RG 1.86 requires that  and  surface 

radioactivity levels be evaluated separately. The primary emitter of concern is Ra-226, with a 

total surface radioactivity criterion of 100 dpm /100 cm2. The primary  emitter of concern is 

Ra-228 of the natural Th decay series with a total surface radioactivity criterion of 1,000 dpm 

/100 cm2. The highest average total  and  surface radioactivity levels were 239 dpm/100 cm2
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and 3,080 dpm/100 cm2. The maximum total  and  surface radioactivity levels were 

1,410 dpm/100 cm2and 17,900 dpm/100 cm2. The summary results of total  and  surface 

radioactivity measurements are presented in Table 4-36. Individual total  and  surface 

radioactivity measurement results are presented in Appendix D.

4.3.1.3 Gross Gamma Radiation Scan Results

Gross gamma radiation scans recorded in cpm were performed on open land areas and accessible 

areas of the plant to identify levels of elevated gross gamma radiation. The results of the gross 

gamma radiation scans are presented in Table 4-37. The highest average count rate for the 

plants was 34,513 cpm, and the maximum count rate recorded was 356,274 cpm. A graphic 

display of the gamma radiation scan results (figures) at each facility was prepared using GIS 

software. The resulting figures are in Appendix E.

4.3.1.4 Gamma Radiation Exposure Rate Results Summary

Gross gamma radiation scan results in units of cpm presented in Table 4-37 were converted to 

R/hr by dividing by 800 cpm per R/hr, a conversion factor appropriate for Ra-226 gamma 

energy as detected with 2-inch by 2-inch NaI detectors rounded to one significant figure

(Table 6.4, NaI Scintillation Detector Scan MDCs for Common Radiological Contaminants, 

NUREG-1507, Minimum Detectable Concentrations With Typical Radiation Survey Instruments 

for Various Contaminants and Field Conditions, USNRC June 1998). Table 4-38 presents 

statistical results for each ZLD facility. The highest average gamma radiation exposure rate was 

43.1 R/hr, and the maximum gamma radiation exposure rate measured was 445 R/hr.

4.3.2 Solid Sample Results

4.3.2.1 Filter Cake Samples

Three survey rounds were conducted at each of the nine ZLD plants and a total of 31 filter cake 

samples were collected from the nine plants. The gamma spectroscopy results are presented in 

Table 4-39. Radium-226 and Ra-228 were measured in ZLD filter cake samples at 

concentrations above typical background levels for surface soils. Radium-226 concentrations 

ranged from 3.08 to 480 pCi/g, and Ra-228 concentrations ranged from 0.58 to 67.3 pCi/g.

4.3.2.2 Solids/Biased Samples

A single biased surface soil sample was collected. The gamma spectroscopy results are 

presented in Table 4-40. The Ra-226 and Ra-228 were measured in concentrations above 

typical background levels. The Ra-226 concentration was 37.1 pCi/g, and the Ra-228 

concentration was 7.47 pCi/g.

4.3.3 Liquid Samples

Three survey and sample events were conducted at each of the nine ZLD plants. A total of 30 

effluent samples and 26 influent samples were collected. The filtered and unfiltered sample 

analyses results are presented separately. The results of the U series, Th Series, and Ac series 

with K-40, gross , and gross  are presented in Tables 4-41 through 4-44. Radium (Ra-226 
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and Ra-228) was routinely detected in all sample types with an approximate 50 percent

difference between influent and effluent, but little difference between filtered and unfiltered 

results, as presented for Ra-226 results below in Figure 4-2.

Figure 4-2. ZLD Influent and Effluent Liquid Ra-226 Minimum, Maximum, and Average

Wastewater

Source Filtered or Not Min (pCi/L) Max (pCi/L) Ave (pCi/L)

Effluent Filtered 29.0 12,500 2,780

Effluent Unfiltered 33.0 11,900 2,610

Influent Filtered 38.5 20,900 4,660

Influent Unfiltered 134 17,100 4,400

4.3.4 Indoor Radon Sampling Results

ATDs were deployed in the ZLD plants at various indoor locations such as break rooms, 

laboratories, offices, etc., and the results were evaluated using the EPA Action Level of 

4.0 pCi/L. The results ranged from 0.5 to 4.9 pCi/L. Two results exceeded the action level. The 

results of the analyses are presented in Table 4-45. The Rn analytical reports are presented in 

Appendix H.

4.3.5 Filtered Versus Unfiltered Sample Data Evaluation

Appendix I contains a complete evaluation of filtered versus unfiltered liquid samples for the 

entire study. The conclusion from this evaluation is that there is no apparent trend or bias that 

filtering produces. There were some subsets of data where either the unfiltered results or the 

filtered results appear to be significantly higher. There was no statistically significant correlation 

found within any sample group. Since the liquid samples were preserved by addition of acid 

prior to filtering, the radioactive particulates may have entered solution and were therefore not 

removed by filtering.

4.3.6 ZLD Worker Exposure Assessment

4.3.6.1 ZLD Worker Potential External Gamma Radiation Exposure

The maximum average gamma radiation exposure rate measured at any of the ZLD plants was 

43.1 R/hr. The lowest background gamma radiation exposure rate measured at any of the sites 

was 5 R/hr. Assuming the time period of exposure is a full occupational year of 2,000 hours, 

the maximum average ZLD annual external gamma radiation exposure was estimated as follows:

Maximum Average ZLD External Gamma Radiation Exposure Estimate

(43.1 – 5) μR/hr x 2,000 hr/yr x (1 mrem/1,000 μR gamma) = 76 mrem/yr

This is an estimate of the maximum average gamma radiation exposure based on 2,000 hours in 

one year. The result is less than the 100 mrem/yr dose equivalent limit for a member of the 

public. Actual exposure is dependent upon the actual exposure rates and occupancy time for 

individual workers.
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The maximum gamma radiation exposure rate measured was 445 rem/hr on contact with the 

outside of a wastewater tank. Work performed in the immediate proximity to the tank could 

potentially result in an exposure of 100 mrem in 225 hours of annual exposure, or about 

10 percent of an employee’s 2,000-hour occupational year. Actual annual exposure for a ZLD 

worker is dependent upon actual exposure rates and actual time worked in the proximity of the 

tank.

4.3.6.2 ZLD Worker Potential Internal Alpha/Beta Exposure

The total and removable / survey surface radioactivity results are discussed in Sections 4.3.1.1 

and 4.3.1.2. One hundred fifty-nine of the 566  measurements and 175 of the 566 

measurements of total surface radioactivity exceeded the RG 1.86 criteria. Fourteen of the 589 

removable  measurements and two of the 589 removable  measurements exceeded the RG 

1.86 criteria. The highest average total  and  surface radioactivity levels were 239 dpm/100 

cm

2

and 4,740 dpm/100 cm2. The maximum total  and  surface radioactivity levels were 

1,410 dpm/100 cm2and 49,700 dpm/100 cm2. The corresponding removable surface 

radioactivity measurements are mostly less than the RG 1.86 criteria, indicating the total surface 

radioactivity measured is fixed to the surface and not immediately available for inhalation or 

ingestion. Fixed  and  surface radioactivity may present a potential inhalation or ingestion 

hazard if disturbed during routine system maintenance.

4.3.6.3 ZLD Worker Potential Internal Radon Exposure

The Rn in ambient indoor area air averaged 2.3 pCi/L. The average is above the average typical 

background indoor level of 1.3 pCi/L in the U.S. as reported by EPA.

4.3.6.4 Gamma Radiation Exposure during Transport of Wastewater and Wastewater 

Sludge

Gamma radiation exposure was estimated for the transport of wastewater from well sites to 

WWTPs, and sludge from WWTPs to landfills. This was done for the driver of the transport 

truck. The truck driver spends the most time near the TENORM-influenced wastewater during 

transport.

It was assumed a truck driver hauled full containers with either wastewater or sludge/filter cake 

for four hours per day and made return trips with empty containers for four hours per day. The 

driver was assumed to work 40 hours per week for 10 weeks per year hauling O&G wastewater 

or sludge. Therefore, the total exposure time was assumed to be 200 hours per year as calculated 

below:

Estimated Duration of Gamma Radiation Exposure for Truck Driver per Year

4 hr/day x 5 days/wk x 10 wks/yr = 200 hrs/yr

Radiation exposure rates to the driver were not measured; they were modeled using the computer 

program MicroShield®. The MicroShield®output files are presented in Appendix J. Two 

external exposure scenarios were evaluated:
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1. Exposure rate to a driver hauling wastewater based on the maximum measured 

concentrations of Ra-226 and Ra-228 in wastewater.

2. Exposure rate to a driver hauling sludge or filter cake based on the maximum measured 

concentrations of Ra-226 and Ra-228 in sludge.

The input and output of MicroShield®based on the two scenarios are summarized in Figure 4-3.

Figure 4-3. MicroShield® External Exposure Scenarios Input/Output

Parameter

Scenario

Wastewater Truck Maximum 

Measured Concentration, 

Scenario 1

Sludge/Filter Cake Roll-off 

Maximum Measured 

Concentration, Scenario 2

Volume 3,800 gallons 20 cubic yards

Shielding Material Stainless steel, 0.5 cm thick Iron, 0.3 cm thick

Ra-226 and Progeny Input

Concentration

18,400 pCi/L 480 pCi/g

Ra-228 and Progeny Input 

Concentration

1,440 pCi/L 183 pCi/g

Resulting Driver Exposure 

Rate (μrem/hr) 14.7 1,340

Exposure Rate per Radium 

Concentration

0.000741 rem/hr / pCi/L of total 

Ra

2.02 rem/hr / pCi/g of total Ra

Maximum Wastewater Truck Driver External Gamma Radiation Exposure Estimate

0.000741 μrem/hr / pCi/L x 2,380 pCi/L x 200 hr/yr x (1 mrem/1,000 μrem gamma) = 

0.35 mrem/yr

This is an estimate of the maximum annual gamma radiation exposure based on the maximum

total Ra activity concentration of influent wastewater measured and 200 hours exposure in one 

year. The result is less than the 100 mrem/yr dose equivalent limit for a member of the public.

Actual exposure is dependent upon the actual exposure rates and occupancy time for individual 

workers.

Maximum Sludge Truck Driver External Gamma Radiation Exposure Estimate

2.02 μrem/hr / pCi/g x 129 pCi/g x 200 hr/yr x (1 mrem/1,000 μrem gamma) = 52 mrem/yr

This is an estimate of the maximum annual gamma radiation exposure based on the maximum

total Ra activity concentration in sludge measured and 200 hours of exposure in one year. The 

result is less than the 100 mrem/yr dose equivalent limit for a member of the public. Actual 

exposure is dependent upon the actual exposure rates and occupancy time for individual workers.

The sludge truck driver assessment is conservative due to the following: solid samples were 

dried prior to gamma spectroscopy analysis, artificially increasing the activity concentration 

results in direct proportion to the moisture content of the sample, i.e., after removal of the weight 

of the wastewater within the sludge sample. In addition, the MicroShield®activity input includes 
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all of the Ra progeny in secular equilibrium. Often the sludge is “fresh,” i.e., progeny ingrowth 

has not progressed to secular equilibrium and the progeny activity is only a fraction of the Ra 

activity.

4.3.7 Alpha Spectroscopy Analysis of Filter Cake

Elevated Ra-226 and Ra-228 and progeny activity were detected in CWT and ZLD filter cake 

samples analyzed by gamma spectroscopy. Due to the low solubility in water of U and Th, 

relative to Ra, U and Th were not present in wastewater and resulting filter cake at the elevated 

levels observed for Ra. Because gamma spectroscopy analysis of solid and liquid samples is 

limited in regards to the quantification of U and Th isotopes (Section 2.3),  spectroscopy 

analysis to measure U (U-238, U-234, and U-235) and Th (Th-232, Th-230, and Th-228), isotope

activity levels was performed on 10 filter cake samples. The results are presented in Table 4-46.

The U-238, U-234, and Th-230, all members of the natural U decay series above Ra-226, were 

measured at approximately 1/3 of typical background activity in soil. Uranium-235 is only 

identified once > MDC. Th-232, a member of the natural Th decay series above Ra-228, was 

measured at approximately 1⁄4 of typical background activity in soil. Only Th-228, a progeny of 

Ra-228, was measured at activity concentrations comparable to Ra-228 identified by gamma 

spectroscopy. The  spectroscopy results confirm the low solubility of U and Th, resulting in 

low activity levels in wastewater and sludge/filter cake.
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Table 4-1. POTW-I Removable Alpha and Beta Surface Radioactivity Measurement Results Summary

Type

No. of 

Data 

Points

Removable Alpha (dpm/100 cm2) Removable Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

WT-12-

FS-024 10 8.15 8.15 0.00 8.15 38.0 38.0 0.00 38.0

WT-12-

FS-074 19 6.90 6.90 0.00 6.90 60.5 60.5 0.00 60.5

WT-12-

FS-075 17 9.15 9.15 0.00 9.15 34.8 34.8 0.00 34.8

WT-13-

FS-034 17 9.15 9.15 0.00 9.15 38.5 38.5 0.00 38.5

WT-13-

FS-119 32 6.40 16.4 1.76 6.71 56.0 56.0 0.00 56.0

WT-13-

FS-120 20 9.10 9.10 0.00 9.10 34.8 34.8 0.00 34.8

WT-14-

FS-027 12 9.10 9.10 0.00 9.10 41.5 41.5 0.00 41.5

WT-14-

FS-121 20 4.25 4.25 0.00 4.25 65.0 65.0 0.00 65.0

WT-14-

FS-122 20 8.85 8.85 0.00 8.85 30.0 30.0 0.00 30.0

WT-15-

FS-031 8

8.85 8.85 0.00 8.85 30.0 30.0 0.00 30.0

WT-15-

FS-032 14 6.40 22.0 4.93 6.00 56.0 161 27.9 63.5

WT-15-

FS-033 5 9.15 9.15 0.00 9.15 38.5 38.5 0.00 38.5

WT-16-

FS-043 16 9.10 9.10 0.00 9.10 41.5 41.5 0.00 41.5

WT-16-

FS-123 19 7.30 7.30 0.00 7.30 65.5 65.5 0.00 65.5

WT-16-

FS-124 22 9.10 9.10 0.00 9.10 35.0 35.0 0.00 35.0
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Table 4-1. POTW-I Removable Alpha and Beta Surface Radioactivity Measurement Results Summary

Type

No. of 

Data 

Points

Removable Alpha (dpm/100 cm2) Removable Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

WT-17-

FS-051 20 8.00 8.00 0.00 8.00 30.8 30.8 0.00 30.8

WT-17-

FS-125 15 8.70 8.70 0.00 8.70 38.3 38.3 0.00 38.3

Note: During the calculations to convert from raw counts to dpm, the calculated value was compared to half of the MDC. If the value was below

this number, half of the MDC was inserted into the tables. Where the standard deviation is zero and the minimum, maximum, and average are the 

same, then all measurements were below half of the MDC.
PA DEP TENORM Study Report 

– Section 

4.0 Rev. 0

January 2015

4-17

Table 4-2. POTW-I Total Alpha and Beta Surface Radioactivity Measurement Results Summary

Type

No. of 

Data 

Points

Total Alpha (dpm/100 cm2) Total Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

WT-12-

FS-024 10 29.4 29.4 0.00 29.4 100 563 144 413

WT-12-

FS-074 19 7.30 43.7 10.1 19.7 308 308 0.00 308

WT-12-

FS-075 17 7.45 54.5 14.2 18.27 269 1,550 268 870

WT-13-

FS-034 17 30.5 74.4 13.7 37 847 2,130 325 1,290

WT-13-

FS-119 15 18.6 875 220 88.8 305 728 117 337

WT-13-

FS-120 20 19.0 164 33.9 30.2 280 1,530 391 811

WT-14-

FS-027 13 30.5 30.5 0.00 30.5 773 1,540 197 1,130

WT-14-

FS-121 20 18.6 112 26.1 37.0 254 1,490 352 515

WT-14-

FS-122 20 30.5 89.3 20.3 38.8 268 1,630 359 784

WT-15-

FS-031 8 30.5 1,190 437 313 268 38,000 14,800 10,000

WT-15-

FS-032 4 18.6 18.6 0.00 18.6 263 466 102 313

WT-15-

FS-033 5 30.5 30.5 0.00 30.5 735 1,360 259 1,070

WT-16-

FS-043 16 30.5 30.5 0.00 30.5 676 29,800 7,170 2,930

WT-16-

FS-123 19 7.45 24.9 6.39 11.4 276 1,140 272 498

WT-16-

FS-124 22 7.45 34.7 10.2 12.7 273 1,200 295 593

WT-17-

FS-051 20 7.45 54.5 13.4 16.0 313 929 159 363
PA DEP TENORM Study Report 

– Section 

4.0 Rev. 0

January 2015

4-18

Table 4-2. POTW-I Total Alpha and Beta Surface Radioactivity Measurement Results Summary

Type

No. of 

Data 

Points

Total Alpha (dpm/100 cm2) Total Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

WT-17-

FS-125 15 29.8 134 32.8 61 313 2,760 704 773

Note: During the calculations to convert from raw counts to dpm the calculated value was compared to half of the MDC. If the value was below 

this number, half of the MDC was inserted into the tables. Where the standard deviation is zero and the minimum, maximum, and average are the 

same then all measurements were below half of the MDC. 
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-19

Table 4-3. POTW-I Gross Gamma Radiation Scan Results Summary

Site GWS Maxa

(cpm)

GWS Mina

(cpm)

GWS 

Averagea

(cpm)

GWS Std 

Dev (cpm)

No. Data 

Points

12 9,514 4,966 7,184 633 7,129

13 9,362 3,404 5,072 829 4,408

13 20,761 3,608 6,019 2,694 8,553

13 18,203 3,486 5,418 2,082 5,474

14 33,141 3,112 5,582 2,517 7,638

14 29,220 3,867 6,110 2,272 7,302

14 32,253 3,680 6,435 3,812 3,275

15 131,626 3,804 20,392 14,569 3,508

15 162,535 5,684 18,319 16,130 7,334

15 205,446 5,452 29,034 36,865 3,052

16 10,005 3,463 5,671 870 9,390

16 13,915 3,723 5,628 1,050 9,520

16 13,597 3,473 6,871 1,722 2,026

17 150,649 3,305 9,194 10,116 4,509

17 156,738 3,478 11,137 17,801 3,003

aConvert count rate data to exposure rate by dividing count rate by 800 to yield μR/hr.

Table 4-4. POTW-I Results Summary of NaI Count Rate Data 

Converted to Exposure Rates

Site GWS Max 

(μR/hr)

GWS Min 

(μR/hr)

GWS 

Average 

(μR/hr)

GWS Std 

Dev (μR/hr)

No. Data 

Points

12 11.9 6.21 8.98 0.791 7,129

13 11.7 4.26 6.34 1.04 4,408

13 26.0 4.51 7.52 3.37 8,553

13 22.8 4.36 6.77 2.60 5,474

14 41.4 3.89 6.98 3.15 7,638

14 36.5 4.83 7.64 2.84 7,302

14 40.3 4.60 8.04 4.77 3,275

15 165 4.76 25.5 18.2 3,508

15 203 7.11 22.9 20.2 7,334

15 257 6.82 36.3 46.1 3,052

16 12.5 4.33 7.09 1.09 9,390

16 17.4 4.65 7.04 1.31 9,520

16 17.0 4.34 8.59 2.15 2,026

17 188 4.13 11.5 12.6 4,509

17 196 4.35 13.9 22.3 3,003
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-20

Table 4-5. POTW-I Filter Cake Results Summary – Gamma Spectroscopy Results

Sample ID Ra-226 

(pCi/g)

Ra-228 

(pCi/g)

K-40 

(pCi/g)

WT-12-SL-030 6.37 1.56 4.04

WT-12-SL-048 9.75 1.87 6.94

WT-12-SL-085 5.16 0.854 2.69

WT-13-SL-021 6.50 3.08 3.96

WT-13-SL-060 21.3 2.99 9.38

WT-13-SL-065 17.4 8.69 3.93

WT-14-SL-017 55.6 32.0 7.77

WT-14-SL-052 9.27 2.80 14.3

WT-14-SL-068 13.1 6.73 6.71

WT-15-SL-057 41.9 19.7 12.9

WT-16-SL-026 5.01 1.29 6.95

WT-16-SL-044 52.6 5.21 7.78

WT-16-SL-073 2.71 0.894 0.822

WT-17-SL-059 35.1 19.2 6.14

Average 20.1 7.63 6.74

Std. Dev. 18.5 9.40 3.71

Median 11.4 3.04 6.83

Minimum 2.71 0.854 0.822

Maximum 55.6 32.0 14.3
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-21

Table 4-6. POTW-N Filter Cake Results Summary – Gamma Spectroscopy Results

Sample ID Ra-226 

(pCi/g)

Ra-228 

(pCi/g)

K-40 

(pCi/g)

WT-26-SL-094 3.97 1.31 5.47

WT-26-SL-095 3.61 1.46 5.41

WT-27-SL-096 2.33 0.817 6.51

WT-27-SL-097 5.76 1.12 4.31

WT-28-SL-098 7.36 1.84 6.57

WT-28-SL-099 3.78 1.07 6.55

WT-29-SL-100 35.4 7.26 7.66

WT-29-SL-101 15.6 3.28 7.34

Average 8.89 2.13 6.07

Std. Dev. 11.8 2.29 1.09

Median 3.97 1.31 6.51

Minimum 2.33 0.817 4.31

Maximum 35.4 7.26 7.66

Table 4-7. POTW-I Sediment Sample Results Summary – Gamma Spectroscopy Results

Sample ID Ra-226 

(pCi/g)

Ra-228 

(pCi/g)

K-40 

(pCi/g)

WT-14-SL-018 4.25 1.96 10.3

WT-14-SL-053 1.83 0.799 8.71

WT-14-SL-069 3.94 1.96 5.53

WT-15-SL-020 16.6 6.25 15.7

WT-15-SL-056 18.2 6.19 13.0

WT-15-SL-067 15.3 5.77 24.5

WT-17-SL-058 2.91 1.69 6.20

Average 9.00 3.52 12.0

Std. Dev. 7.29 2.42 6.58

Median 4.25 1.96 10.3

Minimum 1.83 0.799 5.53

Maximum 18.2 6.25 24.5
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-22

Table 4-8. POTW-I Filtered Effluent Results Summary –

Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross 

Alpha 

(pCi/L)

Gross 

Beta 

(pCi/L)

WT-12-LQ-098 < 118 < 18.0 < 66.0 < 196 < 392

WT-12-LQ-159 < 127 < 25.0 81.0 < 5.77 10.6

WT-12-LQ-295 77.0 < 13.0 42.0 195 365

WT-13-LQ-054 < 126 < 22.0 73.0 < 29.6 < 18.9

WT-13-LQ-193 < 79.0 < 16.0 46.0 < 114 < 198

WT-13-LQ-209 363 < 10.0 53.0 < 123 < 203

WT-14-LQ-044 < 130 < 24.0 56.0 < 25.8 < 163

WT-14-LQ-171 87.0 < 12.0 60.0 < 111 < 186

WT-14-LQ-215 104 < 13.0 71.0 < 118 < 202

WT-15-LQ-052 < 139 < 24.0 < 81.0 < 21.3 < 16.2

WT-15-LQ-185 < 139 < 25 < 98.0 < 5.67 8.70

WT-15-LQ-223 120 25.0 52.0 < 161 < 198

WT-16-LQ-079 101 < 8.00 34.0 < 2.26 5.77

WT-16-LQ-145 < 43.0 < 6.00 55.0 < 6.96 11.3

WT-16-LQ-241 335 < 9.00 < 32.0 4.64 10.7

WT-17-LQ-191 154 < 18.0 < 48.0 < 121 < 187

WT-17-LQ-217 116 12.0 < 33.0 < 127 < 203

Average 129 9.34 48.1 42.9 75.0

Std. Dev. 93.1 5.35 19.0 49.6 88.8

Median 101 8.50 50.5 35.12 87.3

Minimum 57.0 3.00 16.0 1.13 5.77

Maximum 363 25.0 81 195 365

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-23

Table 4-9. POTW-I Unfiltered Effluent Results Summary –

Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross 

Alpha 

(pCi/L)

Gross 

Beta 

(pCi/L)

WT-12-LQ-097 < 67.0 < 10.0 51.1 < 284 < 396

WT-12-LQ-160 < 58 < 11.0 41.0 9.63 10.9

WT-12-LQ-296 59.0 < 5.00 40.0 < 192 < 207

WT-13-LQ-053 113 < 8.00 37.0 < 36.5 < 135

WT-13-LQ-194 82.0 < 5.00 55.0 < 117 < 187

WT-13-LQ-210 < 35.0 < 23.0 < 11.0 < 144 < 194

WT-14-LQ-043 < 101 < 18.0 80.0 < 84.2 < 158

WT-14-LQ-172 340 < 15.0 < 58.0 < 464 < 218

WT-14-LQ-216 < 128 < 27.0 < 106 < 136 < 193

WT-15-LQ-051 80.0 < 9.00 53.0 < 177 < 163

WT-15-LQ-186 < 50.0 < 9.00 < 27.0 11.0 9.60

WT-15-LQ-224 < 79.0 27.0 64.0 < 235 < 209

WT-16-LQ-080 100 < 9.00 33.0 < 3.13 7.16

WT-16-LQ-146 < 67.0 < 11.0 < 41.0 < 2.16 7.71

WT-16-LQ-242 107 < 9.00 44.0 < 2.51 10.5

WT-17-LQ-192 100 < 9.00 < 51.0 1,110 337

WT-17-LQ-218 156 35.0 31.0 < 152 < 197

Average 103 9.57 42.6 125 82.0

Std. Dev. 73.7 9.32 21.5 269 79.3

Median 97.0 5.50 40.5 63.3 87.5

Minimum 17.5 2.50 5.50 1.08 7.16

Maximum 340 35.0 82.0 1,110 337

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-24

Table 4-10. POTW-N Filtered Effluent Results Summary –

Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross 

Alpha 

(pCi/L)

Gross 

Beta 

(pCi/L)

WT-26-LQ-300 < 74.0 15.0 60.0 < 7.65 5.29

WT-27-LQ-304 < 44.0 < 5.00 42.0 < 10.8 5.72

WT-28-LQ-308 < 23.0 < 5.00 53.0 < 4.78 7.64

WT-29-LQ-312 116 17.0 56.0 < 4.83 14.6

Average 46.6 9.25 52.8 3.51 8.31

Std. Dev. 47.4 7.84 7.72 1.43 4.31

Median 29.5 8.75 54.5 3.12 6.68

Minimum 11.5 2.50 42.0 2.39 5.29

Maximum 116 17.0 60.0 5.40 14.6

< – indicates a value less than the reported number which is the MDC.

Table 4-11. POTW-N Unfiltered Effluent Results Summary –

Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross 

Alpha 

(pCi/L)

Gross 

Beta 

(pCi/L)

WT-26-LQ-299 328 < 9.00 < 34.0 < 6.46 5.75

WT-27-LQ-303 115 < 7.00 57.0 < 7.48 7.48

WT-28-LQ-307 78.0 < 14.0 49.0 < 5.18 7.15

WT-29-LQ-311 59.0 5.00 66.0 < 191 < 209

Average 145 5.00 47.3 26.3 31.2

Std. Dev. 124 1.47 21.3 46.2 48.9

Median 96.5 4.75 53.0 3.49 7.32

Minimum 59.0 3.50 17.0 2.59 5.75

Maximum 328 7.00 66.0 95.5 105

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-25

Table 4-12. POTW-I Filtered Influent Results Summary –

Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross 

Alpha 

(pCi/L)

Gross 

Beta 

(pCi/L)

WT-12-LQ-096 66.0 < 7.00 49.0 < 5.64 < 7.91

WT-12-LQ-157 109 466 164 < 13.2 < 5.01a

WT-12-LQ-293 100 8.00 63.0 < 290 < 230

WT-13-LQ-056 < 154 < 29.0 137 < 207 < 394

WT-13-LQ-195 115 < 20.0 < 68.0 < 183 < 201

WT-13-LQ-211 58.0 6.00 53.0 < 13.2 < 8.48

WT-14-LQ-042 < 246 < 48.0 <171 < 16.8 < 15.5

WT-14-LQ-169 < 77.0 < 12.0 < 41 489 < 199

WT-14-LQ-213 82.0 10.0 63 < 323 < 230

WT-15-LQ-050 498 < 28.0 < 82 < 17.3 < 16.1

WT-15-LQ-183 < 236 103 < 141 11.0 9.60

WT-15-LQ-225 255 91.0 31.0 490 < 207

WT-16-LQ-077 < 84.0 < 17.0 119 < 2.63 6.24

WT-16-LQ-143 5,910 878 44.0 11,400 11,300

WT-16-LQ-243 66.0 5.00 43.0 < 3.31 6.75

WT-17-LQ-189 < 121 12.0 33.0 < 117 < 198

WT-17-LQ-219 < 74.0 20.0 49.0 < 154 < 196

Average 497 76.8 56.9 768 734

Std. Dev. 1,450 216 31.4 274 2,720

Median 91.0 12.0 49 58.5 99.0

Minimum 37.0 5.00 20.5 1.32 2.51a

Maximum 5,910 878 137 11,400 11,300

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-26

Table 4-13. POTW-I Unfiltered Influent Results Summary –

Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross 

Alpha 

(pCi/L)

Gross 

Beta 

(pCi/L)

WT-12-LQ-095 < 113 < 19.0 < 59.0 < 220 < 392

WT-12-LQ-158 < 78.0 < 15.0 < 54.0 6.28 10.1

WT-12-LQ-294 345 < 7.00 < 21.0 < 110 < 201

WT-13-LQ-055 < 71.0 < 16.0 69.0 < 14.4 76.4

WT-13-LQ-196 < 78.0 < 15.0 < 56.0 < 287 < 224

WT-13-LQ-212 96.0 < 9.00 54.0 < 13.4 14.5

WT-14-LQ-041 259 < 48.0 < 171 < 14.8 17.2

WT-14-LQ-170 57.0 < 13 65.0 < 118 < 199

WT-14-LQ-214 120 9.00 47.0 < 301 < 227

WT-15-LQ-049 < 73.0 < 15.0 < 50.0 < 4.32 4.89

WT-15-LQ-184 514 48.0 < 67.0 240 < 196

WT-15-LQ-226 479 227 < 102 1,190 493

WT-16-LQ-078 343 < 9.00 < 5.00 < 1.85 7.50

WT-16-LQ-144 < 49.0 < 9.00 30.0 < 3.91 9.94

WT-16-LQ-244 131 41.0 65.0 < 7.48 9.64

WT-17-LQ-190 100 14.0 56.0 < 120 < 200

WT-17-LQ-220 178 20.0 45.0 < 125 < 203

Average 190 28.1 46.1 125 85.9

Std. Dev. 146 52.9 22.4 283 114

Median 120 9.00 47.0 55.0 92.0

Minimum 36.5 3.50 2.50 0.925 4.89

Maximum 514 227 85.5 1,190 493

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-27

Table 4-14. POTW-N Filtered Influent Results Summary –

Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross 

Alpha 

(pCi/L)

Gross 

Beta 

(pCi/L)

WT-26-LQ-298 134 10.0 30.0 13.0 6.62

WT-27-LQ-302 64.0 < 5.00 38.0 15.2 11.6

WT-28-LQ-306 84.0 < 14.0 62.0 4.57 12.4

WT-29-LQ-310 58.0 < 4.00 52.0 < 5.29 8.38

Average 85.0 5.38 45.5 8.85 9.75

Std. Dev. 34.5 3.82 14.3 6.17 2.71

Median 74.0 4.75 45.0 8.79 9.99

Minimum 58.0 2.00 30.0 2.645 6.62

Maximum 134 10.0 62.0 15.2 12.4

< – indicates a value less than the reported number which is the MDC.

Table 4-15. POTW-N Unfiltered Influent Results Summary –

Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross 

Alpha 

(pCi/L)

Gross 

Beta 

(pCi/L)

WT-26-LQ-297 113 < 10.0 < 33.0 < 173 < 207

WT-27-LQ-301 92.0 32.0 44.0 < 192 < 209

WT-28-LQ-305 91.0 < 10.0 43.0 < 169 < 207

WT-29-LQ-309 114 < 9.00 < 29.0 < 4.21 8.63

Average 103 11.6 29.5 67.3 80.0

Std. Dev. 12.7 13.6 16.2 43.7 47.6

Median 103 5.00 29.8 85.5 104

Minimum 91.0 4.50 14.5 2.11 8.63

Maximum 114 32.0 44.0 96.0 105

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-28

Table 4-16. POTW-I Ambient Radon

Facility Location Radon (pCi/L) % error

WT-17-RA-001 Lab 2.2 4%

WT-17-RA-002 Filter Press Room 3.1 3%

WT-17-RA-003 Not Given 0.2 12%

WT-15-RA-001 Old Lab 0.7 7%

WT-12-RA-001 Filter Press Room 0.5 8%

WT-12-RA-002 Break Room 0.5 8%

WT-14-RA-001 Press Room Shelf 0.7 7%

WT-14-RA-002 Break Room 8.7 2%

WT-16-RA-001 Filter Press Room 0.6 9%

WT-16-RA-002 Break Room 1.2 7%

WT-13-RA-001 Load and Filter 0.9 6%

WT-13-RA-002 Lab 1.6 5%

Note: ATDs. Lower level of detection (LLD) for 10 pCi/L-day is 0.1 pCi/L for 90-day test, 0.3 pCi/L for 

30-day test.

Table 4-17. POTW-I vs POTW-N Average Concentrations Comparison for Filtered 

Filtered Sample Set 

Averages for:

Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

Gross Alpha 

(pCi/L)

Gross Beta 

(pCi/L)

POTW-I Effluent 129 9.34 42.9 75.0

POTW-N Effluent 46.6 9.25 52.8 8.31

POTW-I Influent 497 76.8 768 722

POTW-N Influent 85.0 5.38 8.85 9.75

Table 4-18. POTW-I vs POTW-N Average Concentrations Comparison for Unfiltered 

Unfiltered Sample Set 

Averages for:

Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

Gross Alpha 

(pCi/L)

Gross Beta 

(pCi/L)

POTW-I Effluent 103 10.4 125 82.1

POTW-N Effluent 145 5.00 26.3 31.2

POTW-I Influent 190 28.1 125 85.9

POTW-N Influent 103 11.6 67.3a80.0

aAll sample results were < MDC value reported.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-29

Table 4-19. Average Radium, Gross Alpha, and Gross Beta Concentrations for 

Filtered Influent and Effluent POTW Samples

Filtered Sample Set 

Averages for:

Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

Gross Alpha 

(pCi/L)

Gross Beta 

(pCi/L)

POTW-I Influent 497 76.8 768 722

POTW-I Effluent 129 9.34 42.9 75.0

POTW-N Influent 85.0 5.38 8.85 9.75

POTW-N Effluent 46.6 9.25 52.8 8.31

Table 4-20. Average Radium, Gross Alpha, and Gross Beta Concentrations for 

Unfiltered Influent and Effluent POTW Samples

Unfiltered Sample Set 

Averages for:

Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

Gross Alpha 

(pCi/L)

Gross Beta 

(pCi/L)

POTW-I Influent 190 28.1 125 85.9

POTW-I Effluent 103 10.4 125 82.1

POTW-N Influent 103 11.6 67.3a80.0

POTW-N Effluent 145 5.00 26.3 31.2

aAll sample results were < MDC value reported.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-30

Table 4-21. POTW-I Sediment and Effluent Results for Ra-226 and Ra-228

Sample 

Set Sample ID Sample Type Ra-226 Units Ra-228 Units

Ra-226/

Ra-228 

Ratio

POTW 1

Round 2

WT-17-SL-058 Sediment 2.91 pCi/g 1.69 pCi/g 1.72

WT-17-LQ-218 Effluent -

Unfiltered 156 pCi/L 35 pCi/L 4.46

WT-17-LQ-217 Effluent -

Filtered 116 pCi/L 12 pCi/L 9.67

POTW 2

Round 1

WT-14-SL-018 Sediment 4.25 pCi/g 1.96 pCi/g 2.17

WT-14-LQ-043a Effluent -

Unfiltered 50.5 pCi/L 9.00 pCi/L 5.61

WT-14-LQ-044a Effluent -

Filtered 65.0 pCi/L 12.0 pCi/L 5.42

POTW 2

Round 2

WT-14-SL-053 Sediment 1.83 pCi/g 0.799 pCi/g 2.29

WT-14-LQ-172a Effluent -

Unfiltered 51.5 pCi/L 7.50 pCi/L 6.86

WT-14-LQ-171 Effluent -

Filtered 87 pCi/L 8.00 pCi/L 10.90

POTW 2

Round 3

WT-14-SL-069 Sediment 3.94 pCi/g 1.96 pCi/g 2.01

WT-14-LQ-216 Effluent -

Unfiltered 106 pCi/L 23 pCi/L 4.61

WT-14-LQ-215 Effluent -

Filtered 104 pCi/L 10 pCi/L 10.40

POTW 3

Round 1

WT-15-SL-020 Sediment 16.6 pCi/g 6.25 pCi/g 2.66

WT-15-LQ-051 Effluent -

Unfiltered 80 pCi/L 8 pCi/L 10.00

WT-15-LQ-052a Effluent -

Filtered 69.5 pCi/L 12.0 pCi/L 5.79

POTW 3

Round 2

WT-15-SL-056 Sediment 18.2 pCi/g 6.19 pCi/g 2.94

WT-15-LQ-186a Effluent -

Unfiltered 25.0 pCi/L 4.50 pCi/L 5.56

WT-15-LQ-185a Effluent -

Filtered 118 pCi/L 18.0 pCi/L 6.56

POTW 3

Round 3

WT-15-SL-067 Sediment 15.3 pCi/g 5.77 pCi/g 2.65

WT-15-LQ-224 Effluent -

Unfiltered 53 pCi/L 27 pCi/L 1.96

WT-15-LQ-223 Effluent -

Filtered 120 pCi/L 25 pCi/L 4.80

a Result was not detected, 1⁄2 of the reported MDC was presented.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-31

Table 4-22. POTW Sediment and Effluent Ratios for Ra-226/Ra-228

Ratio 

Statistic

Sediments 

(CWT + 

POTW)

Sediments 

(CWT)

Sediments 

(POTW)

Unfiltered 

(CWT + 

POTW)

Unfiltered 

(CWT)

Unfiltered 

(POTW)

Filtered 

(CWT + 

POTW)

Filtered 

(CWT)

Filtered 

(POTW)

Average 3.0 3.4 2.4 8.4 11.4 5.3 5.7 3.8 8.3

Std Dev 0.9 0.9 0.4 6.7 8.3 3.4 3.9 3.6 3.0

Max 4.8 4.8 2.9 21.3 21.3 10.0 10.4 9.2 10.4

Min 1.7 2.3 1.7 1.0 1.0 2.0 1.1 1.1 4.8
January 2015

4-32

PA DEP TENORM Study Report 

– Section 

4.0 Rev. 0

Table 4-23. Summary of Removable Alpha and Beta Surface Contamination Results at CWT Plants

Type

No. of 

Data 

Points

Removable Alpha (dpm/100 cm2) Removable Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

WT-01-FS-021 22 7.30 18.6 2.90 8.27 62.5 62.5 0.00 62.5

WT-01-FS-108 38 8.00 18.6 2.61 8.05 62.5 62.5 0.00 62.5

WT-01-FS-109 25 8.00 18.1 2.02 8.40 30.8 30.8 0.00 30.8

WT-02-FS-012 20 7.30 15.8 1.33 7.51 62.5 62.5 0.00 62.5

WT-02-FS-066 41 8.15 8.15 0.00 8.15 38.0 38.0 0.00 38.0

WT-02-FS-067 29 8.00 29.4 4.56 9.18 30.8 30.8 0.00 30.8

WT-03-FS-040 5 6.90 6.90 0.00 6.90 60.5 60.5 0.00 60.5

WT-03-FS-110 10 8.00 8.00 0.00 8.00 31.0 31.0 0.00 31.0

WT-03-FS-111 16 6.90 6.90 0.00 6.90 60.5 60.5 0.00 60.5

WT-04-FS-025 19 9.15 9.15 0.00 9.15 113 113 0.00 113

WT-04-FS-112 37 7.70 38.1 4.94 8.50 62.0 62.0 0.00 62.0

WT-04-FS-113 25 9.10 9.10 0.00 9.10 69.6 69.6 0.00 69.6

WT-05-FS-044 25 9.11 9.11 0.00 9.11 41.5 41.5 0.00 41.5

WT-05-FS-114 45 6.40 13.6 1.07 6.56 56.0 56.0 0.00 56.0

WT-05-FS-115 23 9.10 9.10 0.00 9.10 32.5 32.5 0.00 32.5

WT-07-FS-022 14 9.15 9.15 0.00 9.15 23.3 23.3 0.00 23.3

WT-07-FS-071 35 7.30 7.30 0.00 7.30 62.5 62.5 0.00 62.5

WT-07-FS-072 15 8.00 8.00 0.00 8.00 36.6 36.6 0.00 36.6

WT-08-FS-015 25 9.10 9.10 0.00 9.10 41.5 41.5 0.00 41.5

WT-08-FS-062 46 7.70 7.70 0.00 7.70 62.0 62.0 0.00 62.0

WT-08-FS-063 32 9.10 9.10 0.00 9.10 41.5 41.5 0.00 41.5

WT-09-FS-013 17 9.10 9.10 0.00 9.10 41.5 41.5 0.00 41.5

WT-09-FS-060 27 4.25 31.1 5.40 5.77 65.0 133 13.1 67.5

WT-09-FS-061 20 8.85 8.85 0.00 8.85 30.0 30.0 0.00 30.0

WT-10-FS-002 22 8.15 8.15 0.00 8.15 38.0 38.0 0.00 38.0

WT-10-FS-046 34 6.90 6.90 0.00 6.90 60.5 60.5 0.00 60.5
January 2015

4-33

PA DEP TENORM Study Report 

– Section 

4.0 Rev. 0

Table 4-23. Summary of Removable Alpha and Beta Surface Contamination Results at CWT Plants

Type

No. of 

Data 

Points

Removable Alpha (dpm/100 cm2) Removable Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

WT-10-FS-047 20 9.10 9.10 0.00 9.10 32.5 32.5 0.00 32.5

WT-11-FS-005 15 8.15 8.15 0.00 8.15 36.0 36.0 0.00 36.0

Note: During the calculations to convert from raw counts to dpm, the calculated value was compared to half of the MDC. If the value was below this 

number, half of the MDC was inserted into the tables. Where the standard deviation is zero and the minimum, maximum, and average are the same,

then all measurements were below half of the MDC.
January 2015

4-34

PA DEP TENORM Study Report 

– Section 

4.0 Rev. 0

Table 4-24. Summary of Total Alpha and Beta Surface Contamination Results at CWT Plants

Type

No. of 

Data 

Points

Total Alpha (dpm/100 cm2) Total Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

WT-01-FS-021 22 30.5 1,540 315 211 929 50,400 10,900 8,780

WT-01-FS-108 30 7.30 476 133 172 283 32,700 7,030 5,310

WT-01-FS-109 25 14.9 448 113 152 287 13,200 3,870 4,090

WT-02-FS-012 20 30.5 332 77.9 58.9 268 8,220 1,710 1,690

WT-02-FS-066 41 7.30 403 120 92.6 240 8,260 2,060 1,590

WT-02-FS-067 29 19.1 473 114 74.5 286 9,040 1,900 1,140

WT-03-FS-040 5 19.0 347 144 115 334 6,310 2,710 2,410

WT-03-FS-110 10 7.45 487 204 194 288 7,120 2,070 1,940

WT-03-FS-111 13 18.6 3,220 877 348 249 30,200 8,170 3,150

WT-04-FS-025 20 30.5 565 157 123 268 8,560 2,290 3,210

WT-04-FS-112 38 18.6 540 137 142 297 14,600 3,720 3,200

WT-04-FS-113 25 7.45 1,600 310 144 291 14,200 3,940 3,480

WT-05-FS-044 25 7.44 179 44.6 61.5 325 3,370 771 1,230

WT-05-FS-114 32 7.30 180 45.1 53.2 257 3,060 829 1,340

WT-05-FS-115 23 19.0 243 82.2 71.9 306 7,380 1,480 1,290

WT-07-FS-022 14 30.5 922 250 132 891 6,650 1,490 2,480

WT-07-FS-071 36 18.6 1,000 206 130 249 5,330 1,210 1,140

WT-07-FS-072 13 19.0 1,390 399 213 310 6,620 1,990 1,740

WT-08-FS-015 25 30.5 208 43.9 50.9 572 3,270 780 1,920

WT-08-FS-062 46 19.1 194 39.5 56.0 284 3,880 1,010 1,370

WT-08-FS-063 32 7.45 94.2 27.5 40.8 290 2,580 696 1,050

WT-09-FS-013 18 30.5 258 56.0 51.0 728 11,900 2,540 2,260

WT-09-FS-060 26 18.6 117 27.3 35.3 354 7,120 1,600 1,280

WT-09-FS-061 20 35.7 35.7 0.00 35.7 286 6,640 1,540 1,690

WT-10-FS-002 22 29.4 224 54.9 53.1 121 2,730 623 395

WT-10-FS-046 34 18.6 476 81.9 44.0 288 5,770 972 623
January 2015

4-35

PA DEP TENORM Study Report 

– Section 

4.0 Rev. 0

Table 4-24. Summary of Total Alpha and Beta Surface Contamination Results at CWT Plants

Type

No. of 

Data 

Points

Total Alpha (dpm/100 cm2) Total Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

WT-10-FS-047 21 7.45 174 37.6 24.0 297 1,760 366 482

WT-11-FS-005 15 30.5 114 26.6 49.0 617 3,380 746 1,350

Note: During the calculations to convert from raw counts to dpm, the calculated value was compared to half of the MDC. If the value was below this 

number, half of the MDC was inserted into the tables. Where the standard deviation is zero and the minimum, maximum, and average are the same,

then all measurements were below half of the MDC.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-36

Table 4-25. Summary of NaI Count Rate Data at CWTs

Site GWS Maxa

(cpm)

GWS Mina

(cpm)

GWS 

Averagea

(cpm)

GWS Std Dev 

(cpm)

No. Data 

Points

1 152,322 4,717 18,543 19,037 2,192

1 252,693 3,273 12,750 24,179 9,513

1 178,291 4,843 17,806 23,505 2,077

2 69,545 4,844 13,849 10,904 2,360

2 33,174 3,850 8,141 2,490 4,743

2 203,895 4,909 19,281 29,028 2,057

3 12,172 5,208 8,375 916 1,162

3 13,983 4,579 7,790 1,655 3,741

3 111,523 5,120 13,819 14,182 2,950

4 288,000 5,448 11,725 24,058 6,492

4 401,688 5,445 15,883 38,194 6,720

4 20,932 7,065 9,310 1,114 3,015

5 20,666 4,751 7,273 752 12,166

5 10,640 5,766 7,532 650 7,274

5 10,369 5,805 7,414 625 5,977

7 9,397 5,124 6,742 796 825

8 27,735 2,611 6,927 3,495 2,924

8 9,915 2,718 5,223 975 6,552

8 24,840 2,723 7,302 3,383 1,812

9 33,141 3,112 5,582 2,517 7,638

9 29,220 3,867 6,110 2,272 7,302

10 12,455 4,175 5,880 1,093 5,790

10 13,200 7,756 5,708 1,398 7,756

11 150,649 3,305 9,194 10,116 4,509

11 156,738 3,478 11,137 17,801 3,003

aConvert count rate data to exposure rate by dividing count rate by 800 to yield μrem/hr.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-37

Table 4-26. Results Summary of NaI Count Rate Data Converted to Exposure Rates

Site GWS Max 

(μR/hr)

GWS Min 

(μR/hr)

GWS Average 

(μR/hr)

GWS Std Dev 

(μR/hr)

No. Data 

Points

1 190 5.90 23.2 23.8 2,192

1 316 4.09 15.9 30.2 9,513

1 223 6.05 22.3 29.4 2,077

2 86.9 6.06 17.3 13.6 2,360

2 41.5 4.81 10.2 3.11 4,743

2 255 6.14 24.1 36.3 2,057

3 15.2 6.51 10.5 1.15 1,162

3 17.5 5.72 9.74 2.07 3,741

3 139 6.40 17.3 17.7 2,950

4 360 6.81 14.7 30.1 6,492

4 502 6.81 19.9 47.7 6,720

4 26.2 8.83 11.6 1.39 3,015

5 25.8 5.94 9.09 0.940 12,166

5 13.3 7.21 9.42 0.813 7,274

5 13.0 7.26 9.27 0.781 5,977

7 11.7 6.41 8.43 1.00 825

8 34.7 3.26 8.66 4.37 2,924

8 12.4 3.40 6.53 1.22 6,552

8 31.1 3.40 9.13 4.23 1,812

9 41.4 3.89 6.98 3.15 7,638

9 36.5 4.83 7.64 2.84 7,302

10 15.6 5.22 7.35 1.37 5,790

10 16.5 9.70 7.14 1.75 7,756

11 188 4.13 11.5 12.6 4,509

11 196 4.35 13.9 22.3 3,003
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-38

Table 4-27. CWT Solids, Filter Cake – Gamma Spectroscopy Results

Sample ID Ra-226 

(pCi/g)

Ra-228 

(pCi/g)

K-40 

(pCi/g)

WT-01-SL-009 208 106 < 1.33

WT-01-SL-037 261 137 < 2.01

WT-01-SL-084 297 158 < 2.00

WT-02-SL-006 120 75.0 15.7

WT-02-SL-036 118 66.0 12.8

WT-02-SL-081 164 97.2 13.0

WT-03-SL-012 56.6 13.5 10.7

WT-04-SL-013 59.9 57.3 7.65

WT-04-SL-050 35.1 36.0 5.04

WT-04-SL-062 70.1 59.4 5.22

WT-04-SL-063 165 91.7 8.74

WT-05-SL-022 82.1 49.8 9.91

WT-05-SL-061 10.1 5.03 6.06

WT-05-SL-064 104 52.4 9.13

WT-08-SL-027 67.5 3.48 7.47

WT-08-SL-047 35.7 6.46 10.5

WT-08-SL-072 52.1 4.46 4.13

WT-08-SL-088 41.1 4.46 < 0.553

WT-08-SL-089 15.7 3.45 17.4

WT-09-SL-019 174 2.44 9.05

WT-09-SL-054 269 108 13.7

WT-09-SL-066 294 164 16.1

WT-10-SL-029 3.88 177 0.969

WT-10-SL-049 5.97 0.363 2.89

WT-06-SL-045 24.7 2.74 11.1

Average 126 65.3 8.34

Std. Dev. 102 59.6 5.13

Median 93.1 57.3 9.05

Minimum 3.88 0.363 0.277

Maximum 305 177 17.4

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-39

Table 4-28. CWT Solids, Sediment – Gamma Spectroscopy Results

Sample ID Ra-226 

(pCi/g)

Ra-228 

(pCi/g)

K-40 

(pCi/g)

WT-01-SL-010 105 29.7 8.44

WT-01-SL-038 37.2 12.4 7.17

WT-01-SL-083 76.8 20.0 8.31

WT-02-SL-007 5.86 2.59 4.55

WT-02-SL-035 3.60 1.37 4.67

WT-02-SL-082 2.50 0.978 9.26

WT-03-SL-011 4.72 1.54 6.34

WT-04-SL-014 101 22.7 10.1

WT-04-SL-051 421 86.9 10.0

Average 84.2 19.8 7.65

Std. Dev. 133 27.4 2.11

Median 37.2 12.4 8.31

Minimum 2.50 0.978 4.55

Maximum 421 86.9 10.1

Table 4-29. CWT Solids, Biased Soil – Gamma Spectroscopy Results

Sample ID Ra-226 

(pCi/g)

Ra-228 

(pCi/g)

K-40 

(pCi/g)

U-238 

(pCi/g)

U-235 

(pCi/g)

WT-01-SL-008 117 30.6 17.0 < 2.46 1.83

WT-02-SL-034 13.3 4.26 5.06 < 3.14 < 0.331

WT-04-SL-015 < 3.42 83.1 10.5 < 3.37 < 0.774

Average 44.0 39.3 10.9 1.50 0.794

Std. Dev. 63.5 40.1 5.98 0.24 0.904

Median 13.3 30.6 10.5 1.57 0.387

Minimum 1.71 4.26 5.06 1.23 0.166

Maximum 117 83.1 17.0 1.69 1.83

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-40

Table 4-30. CWT Filtered Effluent – Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross Alphaa

(pCi/L)

Gross Beta 

(pCi/L)

WT-01-LQ-023 110 < 19.0 334 < 1,270 < 847

WT-01-LQ-115 < 169 55.0 406 < 1,040 < 909

WT-01-LQ-281 287 < 18.0 235 < 2,040 < 879

WT-02-LQ-021 113 < 15.0 116 13.1 < 263

WT-02-LQ-111 86 < 16.0 140 < 1,340 < 872

WT-02-LQ-279 55 6.00 174 < 1,950 < 870

WT-03-LQ-029 23 < 5.00 52 25.1 45.7

WT-03-LQ-121 91 < 11.0 52 < 104 < 190

WT-03-LQ-287 86 < 9.00 62.0 < 192 < 208

WT-04-LQ-031 76 37.0 403 < 692 < 422

WT-04-LQ-165 104 94.0 618 < 2,200 < 940

WT-04-LQ-201 320 68.0 339 < 1,040 < 802

WT-05-LQ-058 215 118 595 < 762 504

WT-05-LQ-197 150 < 9.00 282 < 950 608

WT-05-LQ-207 181 80.0 607 < 1,810 < 938

WT-07-LQ-015 5,510 849 888 ND 7,660

WT-07-LQ-109 1,630 324 586 2,330 1,080

WT-07-LQ-273 8,810 1,740 360 21,400 8,700

WT-08-LQ-081 84 < 9.00 < 30 1.13 < 0.998

WT-08-LQ-085 12,700 110 304 22,800 5,810

WT-08-LQ-151 < 79 < 15.0 49.0 8.25 1.98

WT-08-LQ-153 14,900 1,300 598 22,700 4,570

WT-08-LQ-237 12,400 1,220 388 40,700 12,100

WT-09-LQ-046 < 73 < 12.0 148 < 2,830 < 1,040

WT-09-LQ-175 503 319 181 < 1,120 < 895

WT-09-LQ-227 273 164 188 < 2,550 < 989

WT-10-LQ-094 < 92 < 17.0 < 96 < 204 < 393

WT-10-LQ-161 363 10.0 203 < 126 < 187

WT-10-LQ-291 77 < 13.0 55.0 < 161 < 196

WT-11-LQ-187 1,700 943 238 5,520 1,670

WT-11-LQ-221 2,090 976 228 4,160 1,730

Average 2,100 316 285 4,460 1,410

Std. Dev. 4,250 510 221 9,700 2,800

Median 166 37.0 232 560 438

Minimum 18.0 2.50 15.0 1.13 0.499

Maximum 14,900 1,740 888 40,700 12,100

aND – Sample Matrix was not suitable for analysis.

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-41

Table 4-31. CWT Unfiltered Effluent – Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228a

(pCi/L)

K-40 

(pCi/L)

Gross Alpha 

(pCi/L)

Gross Beta 

(pCi/L)

WT-01-LQ-024 104 < 18.0 296 < 1,340 < 871

WT-01-LQ-116 < 196 < 22.0 381 < 1,130 < 844

WT-01-LQ-282 114 < 15.0 270 < 2,650 < 1,000

WT-02-LQ-022 64.0 < 5.00 113 < 689 < 444

WT-02-LQ-112 < 116 < 18.0 140 < 1,250 < 804

WT-02-LQ-280 108 < 10.0 162 < 2,600 < 994

WT-03-LQ-030 61.0 < 8.00 29 < 260 < 181

WT-03-LQ-122 126 < 13.0 36 < 142 < 191

WT-03-LQ-288 362 11.0 < 30.0 < 213 < 211

WT-04-LQ-032 < 82.0 84.0 406 -10.3 480

WT-04-LQ-166 117 112 568 < 1,030 1,280

WT-04-LQ-202 < 131 < 27.0 361 < 1,450 < 846

WT-05-LQ-057 357 133 565 < 595 < 453

WT-05-LQ-198 < 202 89.0 688 < 1,320 < 500

WT-05-LQ-208 240 92.0 648 < 912 < 845

WT-07-LQ-110 1,670 318 571 2,370 1,060

WT-07-LQ-274 8,050 1,740 1,450 33.6 5,380

WT-08-LQ-082 87.0 < 4.00 37 < 1.66 < 1.17

WT-08-LQ-086 10,300 912 371 18,900 4,900

WT-08-LQ-152 < 34.0 < 4.00 42.0 4.68 < 2.01

WT-08-LQ-154 15,500 1,250 414 17,100 4,440

WT-08-LQ-238 12,700 1,200 355 42,300 12,900

WT-09-LQ-045 161 28.0 118 0.260 < 341

WT-09-LQ-176 367 229 200 1,810 1,540

WT-09-LQ-228 404 166 233 1,410 < 869

WT-10-LQ-093 42.0 < 4.00 80.0 < 294 < 397

WT-10-LQ-162 < 138 < 27.0 217 < 205 202

WT-10-LQ-292 < 95 < 10.0 69.0 < 224 < 209

WT-11-LQ-188 1,840 ND 264 3,460 1,410

WT-11-LQ-222 1,470 1,100 252 3,880 1,320

Average 1,840 289 312 3,430 1,330

Std. Dev. 4,070 486 291 8,750 2,610

Median 121 27.0 258 565 423

Minimum 42.0 2.00 15.0 0.260 0.585

Maximum 15,500 1,740 1,450 42,300 12,900

aND – Sample Matrix was not suitable for analysis.

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-42

Table 4-32. CWT Filtered Influent – Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40

(pCi/L)

Gross Alphaa

(pCi/L)

Gross Beta 

(pCi/L)

WT-01-LQ-025 1,760 711 345 ND 3,040

WT-01-LQ-117 2,810 1,120 603 10,500 2,970

WT-01-LQ-283 1,900 961 304 3,940 1,950

WT-02-LQ-019 1,650 747 272 ND 141

WT-02-LQ-113 1,660 913 247 2,360 1,900

WT-02-LQ-277 1,770 962 300 3,930 2,760

WT-03-LQ-027 < 83.0 < 16.0 < 63.0 < 129 < 149

WT-03-LQ-119 121 < 19.0 < 54.0 < 205 < 202

WT-03-LQ-285 126 < 5.00 36.0 < 227 < 212

WT-04-LQ-033 175 172 419 < 369 276

WT-04-LQ-167 445 392 626 660 1,510

WT-04-LQ-203 216 173 394 < 1450 < 846

WT-05-LQ-060 57.0 56.0 < 111 < 2550 < 998

WT-05-LQ-199 118 48.0 547 < 579 587

WT-05-LQ-205 242 78.0 514 < 1040 < 802

WT-07-LQ-013 1,390 203 163 2,290 1,310

WT-07-LQ-107 1,930 322 505 3,420 893

WT-07-LQ-275 1,410 203 219 1,920 853

WT-08-LQ-083 87.0 411 37.0 6,110 1,570

WT-08-LQ-155 14,100 1,520 526 22,200 4,640

WT-08-LQ-239 7,080 615 203 28,400 7,820

WT-09-LQ-047 469 247 121 1,310 < 811

WT-09-LQ-173 300 238 176 1,950 1,360

WT-10-LQ-092 97.0 < 15.0 95 < 220 < 392

WT-10-LQ-163 132 < 10.0 345 < 294 276

WT-10-LQ-289 102 8.00 55.0 < 312 < 231

Average 2,350 361 276 3,862 1,430

Std. Dev. 3,015 431 188 7,086 1,760

Median 300 203 260 1,293 853

Minimum 57.0 2.50 27.0 64.5 74.5

Maximum 14,100 1,520 626 28,400 7,820

aND – Sample Matrix was not suitable for analysis.

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-43

Table 4-33. CWT Unfiltered Influent – Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross Alphaa

(pCi/L)

Gross Beta 

(pCi/L)

WT-01-LQ-026 1,430 740 333 4,830 1,780

WT-01-LQ-118 362 11.0 592 8,400 3,440

WT-01-LQ-284 1,820 984 243 2,940 1,420

WT-02-LQ-020 1,740 835 245 3,220 1,890

WT-02-LQ-114 3,630 1,920 < 373 47,100 12,800

WT-02-LQ-278 1,790 1,010 279 4,220 1,650

WT-03-LQ-028 100 < 8.00 33.0 < 188 < 163

WT-03-LQ-120 327 < 17.0 < 55.0 < 116 < 199

WT-03-LQ-286 66.0 6.00 48.0 < 158 < 212

WT-04-LQ-034 214 229 459 ND 1,030

WT-04-LQ-168 453 467 < 69.0 < 1,700 1,130

WT-04-LQ-204 286 228 433 < 883 < 842

WT-05-LQ-059 146 77.0 493 < 910 < 430

WT-05-LQ-200 492 86.0 550 < 575 591

WT-05-LQ-206 238 126 526 < 2,040 1,200

WT-07-LQ-014 1,360 184 171 1,890 485

WT-07-LQ-108 2,330 366 468 3,490 1,180

WT-07-LQ-276 1,030 203 227 1,740 638

WT-08-LQ-084 5,920 367 159 7,960 2,550

WT-08-LQ-156 13,400 1,520 544 27,700 6,870

WT-08-LQ-240 6,940 623 184 27,600 10,200

WT-09-LQ-048 950 328 < 99 < 746 343

WT-09-LQ-174 458 222 151 2,050 1,040

WT-10-LQ-091 < 37.0 < 6.00 67 < 198 < 393

WT-10-LQ-164 < 98.0 < 9.00 328 < 117 375

WT-10-LQ-290 < 35.0 < 6.00 59.0 < 123 < 203

Average 1,870 393 262 5,920 2,000

Std. Dev. 3,010 503 192 11,600 3,220

Median 458 222 227 1,380 1,030

Minimum 17.5 3.00 27.5 58.0 81.5

Maximum 13,400 1,920 592 47,100 12,800

aND – Sample Matrix was not suitable for analysis.

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-44

Table 4-34. CWT Radon Sample Results

Facility Location Radon (pCi/L) Percent Error

WT-05-RA-001 Conference Room 3.1 3

WT-05-RA-002 Near Filter Press 0.9 6

WT-04-RA-001 Filter Press 2 1.9 4

WT-04-RA-002 2nd Fl. Office 1.6 5

WT-04-RA-003 Break Room 1.6 5

WT-08-RA-001 On fuse panel 4.0 4

WT-08-RA-002 Lab 1.5 6

WT-09-RA-001 Office 2.0 4

WT-09-RA-002 Filter Press Area 3.0 3

WT-10-RA-001 Under Filter Press 1.2 5

WT-07-RA-001 Lab Fridge 1.4 7

WT-07-RA-002 Clarifier Elec. Panel 0.9 8

WT-03-RA-001 Influent Wastewater Pump 1.3 7

WT-03-RA-002 Wastewater Receiving Office 1.2 8

WT-02-RA-001 Office 1.2 7

WT-02-RA-002 Filter Press 1.3 7

WT-01-RA-001 Wastewater Receiving Off. 5.0 4

WT-01-RA-002 Top of Filter Press 2.9 5

ATDs. LLD for 10 pCi/L-day is 0.1 pCi/L for 90-day test, 0.3 pCi/L for 30-day test.
January 2015

4-45

Rev. 0 January 8, 2015 PA DEP TENORM Study Report Section 

4

– PREDECISIONAL DRAFT

Table 4-35. Summary of Removable Alpha and Beta Surface Contamination Results at ZLDs

Study Id

No. of 

Data 

Points

Removable Alpha (dpm/100 cm2) Removable Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

WT-06-

FS-039 24 7.30 7.30 0.00 7.30 61.5 61.5 0.00 61.5

WT-06-

FS-116 46 7.70 18.4 1.57 7.92 62.0 62.0 0.00 34.0

WT-06-

FS-117 33 9.35 25.1 3.22 10.1 34.0 34.0 0.00 34.0

WT-18-

FS-011 15 6.90 6.90 0.00 6.90 123 123 0.00 123

WT-18-

FS-058 31 7.30 7.30 0.00 7.30 65.5 193 22.8 69.6

WT-18-

FS-059 20 6.4 22.0 3.77 7.54 32.8 32.8 0.00 32.8

WT-19-

FS-078 13 9.15 9.15 0.00 9.15 38.5 38.5 0.00 38.5

WT-19-

FS-079 17 6.40 6.40 0.00 6.40 56.0 56.0 0.00 56.0

WT-19-

FS-080 18 6.40 6.40 0.00 6.40 32.8 32.8 0.00 32.8

WT-20-

FS-020 16 9.10 9.10 0.00 9.10 41.6 41.6 0.00 41.6

WT-20-

FS-068 39 6.40 30.5 4.91 7.93 56.0 56.0 0.00 56.0

WT-20-

FS-069 32 6.40 22.0 3.07 7.25 33.0 33.0 0.00 33.0

WT-21-

FS-030 4 7.85 17.7 2.05 8.28 36.4 36.4 0.00 36.4

WT-21-

FS-126 45 7.30 35.6 5.45 8.68 62.5 62.5 0.00 62.5

WT-21-

FS-127 39 8.00 294 3.42 8.55 36.6 36.6 0.00 36.6
January 2015

4-46

Rev. 0 January 8, 2015 PA DEP TENORM Study Report Section 

4

– PREDECISIONAL DRAFT

Table 4-35. Summary of Removable Alpha and Beta Surface Contamination Results at ZLDs

Study Id

No. of 

Data 

Points

Removable Alpha (dpm/100 cm2) Removable Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

WT-22-

FS-001 10 7.15 7.15 0.00 7.15 37.5 37.5 0.00 37.5

WT-22-

FS-048 28 7.30 38.4 5.88 8.41 63.0 342 52.8 72.5

WT-22-

FS-049 18 8.00 8.00 0.00 8.00 30.8 30.8 0.00 30.8

WT-23-

FS-007 23 8.70 30.4 4.53 9.64 76.5 76.5 0.00 76.5

WT-23-

FS-054 33 4.24 4.24 0.00 4.24 65.0 65.0 0.00 65.0

WT-23-

FS-055 25 9.10 9.10 0.00 9.10 32.5 32.5 0.00 32.5

WT-24-

FS-016 20 7.85 7.85 7.85 0.00 36.5 36.5 0.00 36.5

WT-24-

FS-064 21 8.00 8.00 0.00 8.00 30.8 30.8 0.00 30.8

WT-24-

FS-065 41 6.90 6.90 0.00 6.90 60.5 307 39.5 68.0

WT-25-

FS-006 23 7.15 70.7 17.6 12.7 37.5 37.5 0.00 37.5

WT-25-

FS-052 25 8.85 22.9 2.81 9.41 60.0 60.0 0.00 60.0

WT-25-

FS-053 25 6.40 36.2 8.18 9.58 32.8 65.9 6.61 34.1

Note: During the calculations to convert from raw counts to dpm, the calculated value was compared to half of the MDC. If the value was 

below this number, half of the MDC was inserted into the tables. Where the standard deviation is zero and the minimum, maximum, and 

average are the same, then all measurements were below half of the MDC.
January 2015

4-47

Rev. 0 January 8, 2015 PA DEP TENORM Study Report Section 

4

– PREDECISIONAL DRAFT

Table 4-36. Summary of Total Alpha and Beta Surface Contamination Results at ZLDs

Study ID No. of 

Data 

Points

Total Alpha (dpm/100 cm2) Total Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

WT-06-

FS-039 23 30.5 139 32.2 47.3 1,950 49,700 9,810 4,740

WT-06-

FS-116 46 19.1 691 134 103 474 7,760 1,420 2,540

WT-06-

FS-117 33 7.45 248 53.0 81.5 1,210 8,710 1,540 2,440

WT-18-

FS-011 15 18.6 194 44.4 75 415 4,200 1,131 2,100

WT-18-

FS-058 20 730 199 57.1 78.9 211 7,190 1,610 2,360

WT-18-

FS-059 20 19.1 249 60.3 69.1 277 4,670 1,080 1,720

WT-19-

FS-078 13 30.5 114 23.2 36.9 943 2,370 411 1,550

WT-19-

FS-079 17 7.30 72.9 22.2 27.3 277 1,490 369 553

WT-19-

FS-080 18 19.1 54.7 10.1 22.5 318 705 91.2 339

WT-20-

FS-020 16 30.5 719 215 222 268 6,990 2,230 3,080

WT-20-

FS-068 27 7.30 554 154 150 249 8,830 2,240 2,030

WT-20-

FS-069 32 19.1 741 165 174 321 8,800 1,840 1,550

WT-21-

FS-030 23 30.5 645 159 111 780 13,400 2,730 2,440

WT-21-

FS-126 44 18.6 452 127 127 264 17,900 3,420 2,540

WT-21-

FS-127 39 7.45 537 111 49.8 283 3,090 713 960
January 2015

4-48

Rev. 0 January 8, 2015 PA DEP TENORM Study Report Section 

4

– PREDECISIONAL DRAFT

Table 4-36. Summary of Total Alpha and Beta Surface Contamination Results at ZLDs

Study ID No. of 

Data 

Points

Total Alpha (dpm/100 cm2) Total Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

WT-22-

FS-001 10 30.5 273 87.0 85.2 269 3,180 1,050 1,620

WT-22-

FS-048 28 7.30 836 226 133 249 15,500 3,290 2,080

WT-22-

FS-049 18 19.1 1,410 350 239 265 6,380 1,640 1,730

WT-23-

FS-007 25 7.45 273 73.1 83.5 313 6,230 1,380 1,550

WT-23-

FS-054 32 18.6 72.9 14.6 25.1 250 2,660 537 920

WT-23-

FS-055 25 7.45 193 43.3 43.1 313 4,520 905 927

WT-24-

FS-016 20 305 466 123 107 268 4,420 977 2,150

WT-24-

FS-064 21 7.45 711 187 125 288 4,380 980 1,060

WT-24-

FS-065 41 18.6 476 90.8 69.2 260 9,410 1,530 985

WT-25-

FS-006 13 30.5 213 55.4 89.5 802 3,980 921 1,660

WT-25-

FS-052 25 7.45 373 109 97.3 307 3,820 1,040 1,120

WT-25-

FS-053 24 19.1 433 97.9 81.7 321 4,900 1,140 893

Note: During the calculations to convert from raw counts to dpm, the calculated value was compared to half of the MDC. If the value was 

below this number, half of the MDC was inserted into the tables. Where the standard deviation is zero and the minimum, maximum, and 

average are the same, then all measurements were below half of the MDC. 
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-49

Table 4-37. Summary of NaI Count Rate Data at ZLDs

Site GWS Maxa

(cpm)

GWS Mina

(cpm)

GWS 

Averagea

(cpm)

GWS Std Dev 

(cpm)

No. Data 

Points

6 11,264 3,689 6,618 1,435 1,077

6 11,273 4,157 6,315 1,037 4,716

18 7,446 2,692 4,507 714 3,570

18 34,596 2,748 7,432 5,069 2,032

19 15,542 10,665 13,449 573 3,379

19 15,603 11,347 13,667 560 4,098

19 52,815 4,506 13,153 3,995 2,813

20 11,574 3,266 5,966 1,814 7,086

20 73,475 3,771 8,426 8,110 9,495

21 66,958 4,752 12,383 7,293 1,911

21 34,908 4,335 6,912 2,613 15,435

21 46,611 4,351 7,797 4,423 8,792

22 42,518 4,857 10,358 5,297 1,544

22 39,712 4,065 6,937 4,905 5,063

23 12,198 5,546 8,585 1,250 6,265

23 13,938 5,662 9,014 1,348 7,512

24 12,234 5,164 7,419 1,279 1,712

24 11,844 6,541 8,985 1,211 2,959

25 28,597 7,558 12,955 2,243 5,371

25 31,290 2,819 12,524 2,352 8,019

25 356,274 4,464 34,513 63,202 2,006

aConvert count rate data to exposure rate by dividing count rate by 800 to yield μR/hr.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-50

Table 4-38. Results Summary of NaI Count Rate Data Converted to Exposure Rates

Site GWS Max 

(μR/hr)

GWS Min 

(μR/hr)

GWS Average 

(μR/hr)

GWS Std 

Dev (μR/hr)

No. Data 

Points

6 14.1 4.61 8.27 1.79 1,077

6 14.1 5.20 7.89 1.30 4,716

18 9.31 3.37 5.63 0.893 3,570

18 43.2 3.44 9.29 6.34 2,032

19 19.4 13.3 16.8 0.716 3,379

19 19.5 14.2 17.1 0.700 4,098

19 66.0 5.63 16.4 4.99 2,813

20 14.5 4.08 7.46 2.27 7,086

20 91.8 4.71 10.5 10.1 9,495

21 83.7 5.94 15.5 9.12 1,911

21 43.6 5.42 8.64 3.27 15,435

21 58.3 5.44 9.75 5.53 8,792

22 53.1 6.07 12.9 6.62 1,544

22 49.6 5.08 8.67 6.13 5,063

23 15.2 6.93 10.7 1.56 6,265

23 17.4 7.08 11.3 1.69 7,512

24 15.3 6.46 9.27 1.60 1,712

24 14.8 8.18 11.2 1.51 2,959

25 35.7 9.45 16.2 2.80 5,371

25 39.1 3.52 15.7 2.94 8,019

25 445 5.58 43.1 79.0 2,006
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-51

Table 4-39. ZLD Solids, Filter Cake – Gamma Spectroscopy Results

Sample ID Ra-226 

(pCi/g)

Ra-228 

(pCi/g)

K-40 

(pCi/g)

WT-06-SL-046 159 14.2 7.67

WT-06-SL-074 31.7 3.48 14.9

WT-18-SL-025 8.02 2.01 26.3

WT-18-SL-043 6.14 1.63 21.7

WT-18-SL-076 19.1 1.95 5.95

WT-19-SL-023 4.62 1.44 17.5

WT-19-SL-041 127 11.0 16.6

WT-19-SL-070 3.08 0.580 7.46

WT-20-SL-024 26.9 2.62 11.2

WT-20-SL-042 20.0 2.24 10

WT-20-SL-075 22.7 2.21 13.4

WT-20-SL-086 11.1 1.40 6.51

WT-20-SL-087 10.2 1.41 6.55

WT-21-SL-004 6.46 1.54 21.1

WT-21-SL-039 29.3 9.34 10.8

WT-21-SL-078 25.8 7.09 25.4

WT-21-SL-092 214 43.6 12.5

WT-21-SL-093 212 40.5 10.3

WT-22-SL-003 281 17.8 14.1

WT-22-SL-032 145 19.2 15.9

WT-22-SL-079 134 13.1 2.75

WT-23-SL-016 78.9 18.1 8.62

WT-23-SL-055 33.6 6.87 4.28

WT-23-SL-077 26.0 3.39 1.61

WT-24-SL-001 420 58.7 5.25

WT-24-SL-002 41.6 5.26 3.02

WT-24-SL-031 480 67.3 5.16

WT-24-SL-080 289 46.3 5.26

WT-25-SL-028 221 25.1 2.76

WT-25-SL-040 185 24.2 3.27

WT-25-SL-071 206 32.4 3.47

Average 112 15.7 8.53

Std. Dev. 128 18.6 6.09

Median 33.6 6.98 6.55

Minimum 3.08 0.580 1.61

Maximum 480 67.3 25.4

Table 4-40. ZLD Solids, Biased Soil – Uranium Series Gamma Spectroscopy Results

Sample ID Ra-226 

(pCi/g)

Ra-228 

(pCi/g)

K-40 

(pCi/g)

U-238 

(pCi/g)

U-235 

(pCi/g)

WT-21-SL-005 37.1 7.47 16.6 3.81 <2.84

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-52

Table 4-41. ZLD Filtered Effluent – Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross Alpha 

(pCi/L)

Gross Beta 

(pCi/L)

WT-06-LQ-076 12,100 953 < 552 19,600 4,840

WT-06-LQ-149 11,200 806 385 13,300 3,340

WT-06-LQ-245 8,360 571 273 13,700 2,100

WT-18-LQ-070 < 117 < 16.0 159 < 485 < 413

WT-18-LQ-139 86.0 < 10.0 648 < 383 435

WT-18-LQ-253 94.0 < 10.0 149 701 < 832

WT-19-LQ-062 < 127 < 21.0 56 0.097 135

WT-19-LQ-133 < 58.0 < 8 55 < 293 < 225

WT-19-LQ-229 126 < 11.0 338 < 412 < 234

WT-20-LQ-066 8,930 1,090 < 339 11,800 2,440

WT-20-LQ-135 12,500 941 206 31,100 6,190

WT-20-LQ-251 11,100 910 316 14,400 4,110

WT-21-LQ-011 3,470 503 807 6,830 2,160

WT-21-LQ-123 5,050 750 646 10,900 2,650

WT-21-LQ-261 4,690 725 885 10,200 2,890

WT-22-LQ-007 418 < 17.0 487 < 542 284

WT-22-LQ-105 3,280 241 738 5,040 1,530

WT-22-LQ-269 2,310 163 183 2,690 515

WT-23-LQ-038 580 111 186 1,660 602

WT-23-LQ-040 < 82.0 < 14.0 < 30 5.05 3.1

WT-23-LQ-177 110 12.0 54.0 < 145 < 191

WT-23-LQ-179 587 96.0 670 < 1,340 < 504

WT-23-LQ-257 < 69.0 < 7.00 < 41.0 23.6 < 4.03

WT-23-LQ-259 2,540 280 < 64.0 9,610 3,210

WT-24-LQ-001 1,830 277 429 2,540 655

WT-24-LQ-101 2,260 204 339 3,660 1,520

WT-24-LQ-265 292 120 799 < 2090 < 967

WT-25-LQ-088 173 < 12.0 190 < 1140 < 827

WT-25-LQ-127 163 < 8.00 113 < 1100 < 475

WT-25-LQ-235 59.0 < 10.0 134 < 479 < 424

Average 2,780 271 327 5,250 1,370

Std. Dev. 3,890 348 270 7,220 1,560

Median 580 111 206 1,660 515

Minimum 29.0 3.50 15.0 0.097 2.02

Maximum 12,500 1,090 885 31,100 6,190

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-53

Table 4-42. ZLD Unfiltered Effluent – Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross Alpha 

(pCi/L)

Gross Beta 

(pCi/L)

WT-06-LQ-075 12,100 914 275 13,700 3,770

WT-06-LQ-150 11,300 866 326 27,300 6,530

WT-06-LQ-246 7,950 523 256 37,600 12,600

WT-18-LQ-069 < 166 < 35.0 982 < 403 < 401

WT-18-LQ-140 < 80.0 < 20.0 674 < 140 573

WT-18-LQ-254 106 < 10.0 143 < 641 < 780

WT-19-LQ-061 130 < 19.0 102 < 314 < 189

WT-19-LQ-134 104 < 16.0 111 < 108 < 198

WT-19-LQ-230 < 66.0 < 11.0 333 < 280 231

WT-20-LQ-065 8,830 1,090 400 14,500 3,540

WT-20-LQ-136 1,580 221 4,310 40,900 8,340

WT-20-LQ-252 11,900 862 299 42,800 13,900

WT-21-LQ-012 3,770 552 821 5,540 1,850

WT-21-LQ-124 5,120 785 612 16,000 5,530

WT-21-LQ-262 4,370 721 926 13,100 4,020

WT-22-LQ-008 165 19.0 439 < 275 322

WT-22-LQ-106 2,730 250 723 8,940 1,630

WT-22-LQ-270 2,240 178 190 5,100 1,260

WT-23-LQ-037 531 121 160 1,570 358

WT-23-LQ-039 116 < 12.0 31.0 4.94 < 1.78

WT-23-LQ-178 < 85.0 < 16.0 < 60.0 < 217 < 203

WT-23-LQ-180 800 109 497 1,220 871

WT-23-LQ-258 87.0 < 12.0 < 42.0 5.12 26.1

WT-23-LQ-260 2,640 308 340 13,300 4,030

WT-24-LQ-002 2,040 269 431 2,750 < 424

WT-24-LQ-102 2,480 301 358 4,440 1,300

WT-24-LQ-266 293 102 748 < 810 < 836

WT-25-LQ-087 < 147 < 31.0 158 < 917 < 831

WT-25-LQ-128 601 305 4,840 < 448 < 417

WT-25-LQ-236 < 126 < 25.0 158 < 1030 < 475

Average 2,610 295 670 8,990 2,590

Std. Dev. 3,470 337 1120 13,000 3,740

Median 800 178 340 2160 722

Minimum 33.0 5.00 21.0 4.94 0.890

Maximum 11,900 1,090 4840 42,800 13,900

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-54

Table 4-43. ZLD Filtered Influent – Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross Alpha 

(pCi/L)

Gross Beta 

(pCi/L)

WT-06-LQ-073 12,100 1,100 393 21,400 4,530

WT-06-LQ-147 11,300 1,290 302 23,500 5,630

WT-06-LQ-247 3,910 230 215 13,100 4,340

WT-18-LQ-072 278 < 24.0 234 < 427 < 412

WT-18-LQ-141 < 77.0 < 14.0 848 < 175 592

WT-19-LQ-064 950 901 16,600 ND ND

WT-19-LQ-131 131 13.0 281 < 175 < 190

WT-19-LQ-231 1,140 91.0 718 4,770 1,860

WT-20-LQ-068 13,200 1,390 399 18,700 4,740

WT-20-LQ-137 20,900 < 85.0 < 187 59,400 10,700

WT-20-LQ-249 18,400 1,410 491 36,000 7,680

WT-21-LQ-009 2,580 338 517 ND 2,403

WT-21-LQ-125 3,360 515 584 4,750 1,340

WT-21-LQ-263 6,190 687 350 17,100 4,460

WT-22-LQ-005 106 10.0 299 < 257 2,400

WT-22-LQ-103 16,300 847 < 371 30,800 3,730

WT-22-LQ-271 590 51.0 105 754 < 198

WT-23-LQ-035 1,300 413 421 828 425

WT-23-LQ-181 564 94.0 135 2,080 492

WT-23-LQ-255 226 28.0 158 497 < 207

WT-24-LQ-003 2,580 332 552 3,630 1,530

WT-24-LQ-099 1,920 153 341 2,300 395

WT-24-LQ-267 832 380 568 < 1330 < 838

WT-25-LQ-090 6,650 660 202 8,920 1,030

WT-25-LQ-129 2,100 181 187 2,290 396

WT-25-LQ-233 903 127 169 3,220 1,320

Average 4,660 408 998 10,200 2,350

Std. Dev. 6250 448 3,260 15,000 2,730

Median 1,920 230 302 3,220 1,330

Minimum 38.5 7.00 93.5 87.5 95.0

Maximum 20,900 1,410 16,600 59,400 10,700

aND – Sample Matrix was not suitable for analysis.

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-55

Table 4-44. ZLD Unfiltered Influent – Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross Alphaa

(pCi/L)

Gross Betaa 

(pCi/L)

WT-06-LQ-074 12,200 1,090 7,210 17,700 5,920

WT-06-LQ-148 11,100 1,240 350 25,500 5,950

WT-06-LQ-248 4,300 250 243 7,700 1,570

WT-18-LQ-071 1,310 142 318 ND ND

WT-18-LQ-142 < 76.0 < 21.0 761 497 806

WT-19-LQ-063 1,470 777 13,300 ND ND

WT-19-LQ-132 11,700 1000 < 247 2,230 2,080

WT-19-LQ-232 1,600 81.0 701 2,800 1,180

WT-20-LQ-067 13,600 1,390 288 16,200 6,060

WT-20-LQ-138 210 < 17.0 123 49,200 10,600

WT-20-LQ-250 16,500 1,310 529 88,000 23,400

WT-21-LQ-010 3,030 429 605 6,590 1,610

WT-21-LQ-126 2,620 421 528 6,920 2,400

WT-21-LQ-264 6,560 727 415 18,900 4,530

WT-22-LQ-006 216 14.0 136 110 105

WT-22-LQ-104 17,100 903 332 52,400 11,500

WT-22-LQ-272 750 43.0 234 1,240 231

WT-23-LQ-036 1,280 437 410 ND 2,240

WT-23-LQ-182 665 95.0 160 1,300 535

WT-23-LQ-256 221 41.0 153 1,120 423

WT-24-LQ-004 2,700 457 651 3,640 1,320

WT-24-LQ-100 2,100 181 220 3,380 782

WT-24-LQ-268 632 388 558 < 1470 1,060

WT-25-LQ-089 6,870 628 269 9,270 977

WT-25-LQ-130 1,560 140 114 1,810 466

WT-25-LQ-234 1,930 199 161 4,470 1,400

Average 4,400 453 867 13,800 3,530

Std. Dev. 5,310 433 2,600 22,100 5,340

Median 1,930 388 318 4,060 1,400

Minimum 134 10.5 114 110 105

Maximum 17,100 1,390 13,300 88,000 23,400

aND – Sample Matrix was not suitable for analysis.

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 4.0 Rev. 0

January 2015 4-56

Table 4-45. ZLD Radon in Ambient Air Results

Facility Location Radon (pCi/L) Percent Error

WT-06-RA-001 Filter Press 2.2 5

WT-06-RA-002 Lab 2.4 5

WT-18-RA-001 Centrifuge 0.9 8

WT-18-RA-002 Lab 4.3 4

WT-20-RA-001 Transfer Panel 1.9 5

WT-20-RA-002 Break Area 2.6 5

WT-23-RA-001 Break Room 0.5 8

WT-23-RA-002 Ctrl Panel/Boiler Room 1.7 6

WT-23-RA-003 First Floor 0.9 8

WT-21-RA-001 Locker Room Shelf 3.7 4

WT-21-RA-002 Back of Filter Cake Room 2.6 5

WT-24-RA-001 Filter Press 2.9 5

WT-24-RA-002 Office 1.9 6

WT-22-RA-001 Filter Press Room 4.9 4

WT-22-RA-002 Wastewater Receiving Office 0.9 8

Note: ATDs. LLD for 10 pCi/L-day is 0.1 pCi/L for 90-day test, 0.3 pCi/L for 30-day test.

Table 4-46. ZLD and CWT Filter Cake Sample Alpha Spectroscopy Results

Study ID U238 

(pCi/g)

U234 

(pCi/g)

Th230 

(pCi/g)

Th232 

(pCi/g)

Th228 

(pCi/g)

U235 

(pCi/g)

WT-04-SL-063 0.306 0.361 0.307 < 0.205 76.2 < 0.134

WT-25-SL-028 < 0.0681 < 0.084 < 0.05 < 0.0406 9.87 < 0.0844

WT-22-SL-079 0.225 0.281 0.431 < 0.198 8.07 < 0.031

WT-19-SL-041 0.683 0.83 0.502 0.401 8.55 0.163

WT-01-SL-084 < 0.265 < 0.266 < 0.686 < 0.685 1.81 < 0.403

WT-08-SL-047 0.922 0.91 0.525 0.428 7.18 < 0.116

WT-06-SL-046 0.708 0.746 0.473 0.157 8.76 < 0.0787

WT-04-SL-050 < 0.246 < 0.248 < 0.237 < 0.145 6.03 < 0.25

WT-09-SL-054 < 0.0643 < 0.0526 < 0.16 < 0.159 48.3 < 0.0649

WT-23-SL-055 0.268 0.291 < 0.173 < 0.111 5.52 < 0.0524

Average 0.343 0.374 0.289 0.176 18.0 0.0770

St. Dev 0.314 0.334 0.195 0.154 24.319 0.0638

Median 0.247 0.286 0.325 0.101 8.31 0.0501

Min 0.0322 0.0263 0.0250 0.0203 1.81 0.0155

Max 0.922 0.910 0.525 0.428 76.2 0.202
PA DEP TENORM Study Report – Section 5.0 Rev. 0

January 2015 5-1

5.0 LANDFILLS

Leachate samples were collected at 51 PA landfills. Nine of the 51 landfills were selected to be 

surveyed and sampled in more detail due to the volume of waste accepted from the O&G 

industry. Surveys at the nine selected landfills included scans of gamma radiation and 

measurements of total and removable / surface radioactivity. Ambient air at the fence line of 

these landfills was sampled for Rn analysis, and filter cake was sampled from three of these

landfills.

5.1 Leachate

Samples of leachate were collected from 51 landfills and analyzed using gamma spectroscopy 

for Ra-226 and Ra-228. The gamma spectroscopy results are presented in Table 5-1 for the 42

landfills not selected based on volume of O&G waste accepted and Table 5-2 for the nine 

landfills selected based on the volume O&G waste accepted. Radium was detected above the 

MDC value in 34 of 51 samples. Sample results from the 42 unselected landfills showed Ra-226 

results that ranged from 54.0 to 416 pCi/L with an average of 112 pCi/L. Radium-226 results 

from the nine selected landfills ranged from 85 pCi/L to 378 pCi/L with an average of 106 pCi/L. 

Radium-228 results ranged from 2.5 to 55.0 pCi/L with an average of 11.9 pCi/L in the 42

unselected landfills. Radium-228 results from the nine selected landfills ranged from 10.0 pCi/L 

to 1,100 pCi/L with an average of 139 pCi/L.

Due to high solids content, the samples were not filtered in the field or at the laboratory. The 

aqueous portion was decanted from 10 of the 51 samples after they had been allowed to settle.

The aqueous portion was analyzed for Ra-226 and Ra-228. These results are presented in 

Table 5-3 along with the original gamma spectroscopy results for the entire sample. The entire 

sample results include dissolved and undissolved Ra-226 and Ra-228 and are generally one to 

two orders of magnitude higher than analyses of only the aqueous phase, indicating that the 

Ra-226 and Ra-228 in these samples were mostly in the form of undissolved solids.

5.2 Nine Selected Landfills

5.2.1 Influent and Effluent Leachate

Nine influent and seven effluent leachate samples were collected at the nine selected landfills.

All nine landfills treat leachate onsite. The samples were analyzed using gamma spectroscopy. 

The results of the Ra-226, Ra-228, K-40, as well as gross  and gross  activity levels are 

presented in Table 5-4 for effluent samples and in Table 5-5 for influent samples. Radium was 

detected in all of the leachate samples. Radium-226 results ranged from 67.0 to 378 pCi/L with 

an average of 142 pCi/L for effluent samples. Radium-228 results ranged from 3.00 to 

1,100 pCi/L with an average of 178.0 pCi/L for effluent samples. Radium-226 results ranged 

from 48.5 to 116 pCi/L with an average of 83.4 pCi/L for influent samples. Radium-228 results 

ranged from 4.00 to 15.0 pCi/L with an average of 7.94 pCi/L for influent samples. The influent 

and effluent samples from the same facility do not represent the same leachate at different times 

in treatment.
PA DEP TENORM Study Report – Section 5.0 Rev. 0

January 2015 5-2

5.2.2 Leachate Filter Cake

Filter cake from three of the nine landfills was sampled and analyzed using gamma spectroscopy.

The results of the Ra-226 and Ra-228 analyses are presented in Table 5-6. Radium was detected 

in all of the filter cake samples. Radium-226 results ranged from 8.73 to 53.0 pCi/g, with an 

average of 24.3 pCi/g. Radium-228 results ranged from 1.53 to 5.03 pCi/g, with an average of 

3.85 pCi/g.

5.2.3 Effluent Discharge Sediment-Impacted Soil

At three landfills that discharged effluent water to the environment, a sediment-impacted soil 

sample was collected at each of the three effluent outfalls. The gamma spectroscopy results are 

presented in Table 5-7. Radium was detected in all of the samples. Radium-226 results ranged 

from 2.82 to 4.46 pCi/g with an average of 3.57 pCi/g. Radium-228 results ranged from 0.979 to 

2.53 pCi/g with an average of 1.65 pCi/g.

5.2.4 Ambient Air

Ambient air was sampled at the fence line of each of the nine selected landfills and analyzed for 

Rn concentration. A combination of EIC and ATD monitors were used. Because it was 

impractical to place monitors on the actual working face of the landfill, monitors were deployed

at the fence line around the landfill in roughly the four cardinal directions. The exact locations 

of the monitors are depicted in Appendix E. Duplicate monitors were placed at each location, 

inside a single Tyvek®bag. The Tyvek®bag is permeable to Rn gas, but impermeable to 

particulate matter. The monitors were hung on the fence line approximately 5 ft above grade. 

Deployment of the Rn monitors ranged from 74 to 103 days. Monitor device selection was 

based upon availability at the time of deployment. The results are presented in Table 5-8.

Radon activity ranged from 0.2 to 0.9 pCi/L. The Rn monitor analytical reports are presented in 

Appendix H.

5.2.5 Surveys

Radiological surveys were conducted at each of the nine selected landfills, resulting in four data 

sets:

 Removable / surface radioactivity measurements recorded in units of dpm/100cm2

 Total / surface radioactivity measurements recorded in units of dpm/100 cm

2

 Gross Gamma Radiation Scan measurements recorded in units of cpm

 Gamma Radiation Exposure Rate measurements recorded in units of μR/hr

5.2.5.1 Removable Alpha/Beta Surface Radioactivity Measurement Results

Measurements of removable / surface radioactivity were performed to assess potential internal 

radiation exposures to workers through ingestion and/or inhalation. The results were evaluated 

using the RG 1.86 guidelines, Table 1. RG 1.86 requires that  and  radioactivity levels be 

evaluated separately. The primary emitter of concern is Ra-226, with a removable criterion of 

20 dpm /100 cm2. The primary  emitter of concern is Ra-228 of the natural Th decay series,

with a removable criterion of 200 dpm /100 cm2. The average removable  and  levels at each 
PA DEP TENORM Study Report – Section 5.0 Rev. 0

January 2015 5-3

landfill were below the RG 1.86 criteria. The maximum removable  and  levels were also 

below the RG 1.86 criteria. The results of removable  and  surface radioactivity for the 

subject landfills surveyed are presented in Table 5-9. Individual removable  and  surface 

radioactivity measurement results are presented in Appendix D.

5.2.5.2 Total Alpha/Beta Surface Radioactivity Measurement Results

Measurements of total / surface radioactivity were performed to assess potential internal 

radiation exposures to workers through ingestion and/or inhalation. The results were evaluated 

using the RG 1.86 guidelines, Table 1. RG 1.86 requires that  and  levels be evaluated 

separately. The primary emitter of concern is Ra-226, with a total criterion of 100 dpm /

100 cm2. The primary  emitter of concern is Ra-228 of the natural Th decay series, with a total 

criterion of 1,000 dpm /100 cm2. All average total  and  surface radioactivity levels were 

below the RG 1.86 criteria. The maximum total  and  concentrations were 84.6 dpm/100 cm2

and 3,630 dpm/100 cm2. The summary results of total  and  surface radioactivity for the nine 

selected landfills surveyed are presented in Table 5-10. Individual total  and  surface 

radioactivity measurement results are presented in Appendix D.

5.2.5.3 Gross Gamma Radiation Scan Results

Gross gamma radiation scans, recorded in cpm, were performed on open land areas and 

accessible areas of the nine selected landfills to identify areas with gamma radiation levels above 

local background. Summary results for the selected landfills are presented in Table 5-11. The 

highest average count rate at any of the nine selected landfills was 10,816 cpm, and the 

maximum count rate recorded at any of the nine selected landfills was 74,928 cpm. A graphic 

display of the gamma scan results at each facility was prepared using GIS software and is

presented in Appendix E.

5.2.5.4 Gamma Exposure Rate Results Summary

Gross gamma scan results in units of cpm presented in Table 5-11 were converted to R/hr by 

using 800 cpm per R/hr, a conversion factor appropriate for Ra-226 gamma energy as detected 

with 2-inch by 2-inch NaI detectors, rounded to one significant figure (Table 6.4, NaI 

Scintillation Detector Scan MDCs for Common Radiological Contaminants, NUREG-1507, 

Minimum Detectable Concentrations With Typical Radiation Survey Instruments for Various 

Contaminants and Field Conditions, USNRC June 1998). Table 5-12 presents statistical results 

for each of the nine selected landfills. The highest average exposure rate was 13.5 R/hr, and 

the maximum gamma exposure rate measured was 93.7 R/hr.

5.3 Radon Ingrowth Within Filter Cake From WWTP to Landfills

Radon in filter cake is the result of the decay of Ra, which is referred to as ingrowth. 

Radium-226 from the U series and Ra-228 from the Th series are present in flowback and 

produced water. Radioactive precursors to Ra (U-238 and Th-232) are not present due to their 

relative insolubility. When these wastewaters are processed at WWTPs, the Ra is removed and 

concentrated in the resulting filter cake or sludge.
PA DEP TENORM Study Report – Section 5.0 Rev. 0

January 2015 5-4

During handling and/or transport, the sludge or filter cake may be disturbed and some of the Rn

gas may escape, greatly reducing the gamma-emitting progeny that follow Rn-222 in the natural

decay series. Using the software program MicroShield®, the following source terms were 

evaluated to determine the resulting gamma exposure rate measured 6 inches from the outside of 

a standard roll-off container filled with sludge at a concentration of 13.4 pCi/g of Ra-226. The 

source terms assume that all of the Rn and progeny are removed at day zero. Ingrowth of Rn and

progeny was calculated for each time period in accordance with half-lives to determine the 

subsequent source terms, as follows:

a. 0-day ingrowth (13.4 pCi/g of Ra-226 only)

b. 1-day ingrowth (13.4 pCi/g of Ra-226 + 16 percent progeny)

c. 3-day ingrowth (13.4 pCi/g of Ra-226 + 41 percent progeny)

d. 10-day ingrowth (13.4 pCi/g of Ra-226 + 86 percent progeny)

e. 21-day ingrowth (13.4 pCi/g of Ra-226 + 100 percent progeny)

The results of the MicroShield® modeling are presented in Figure 5-1. The exposure rate 

increased rapidly to approximately 21 days post ingrowth, at which time the maximum exposure 

rate was achieved. Starting from zero Rn progeny to full equilibrium after 21 days, the exposure 

rate measured 6 inches from the outside of the roll-off container increased six-fold. Based on the 

MicroShield® modeling results, there may be an increase of six times the gamma exposure rate 

measured 6 inches from the surface of the roll-off container during the first 21 days after a 

wastewater treatment sludge is generated. This is a theoretical curve and assumes all of the Rn is 

removed when the sludge is formed at time zero.

Figure 5-1. Ra-226 Progeny Ingrowth (Days Post Removal) versus 

Exposure Rate from 13.34 pCi/g Ra-226
PA DEP TENORM Study Report – Section 5.0 Rev. 0

January 2015 5-5

To further evaluate the Rn and short-lived progeny ingrowth in wastewater sludge, a series of 

recently generated sludge samples were collected at six WWTPs and analyzed using gamma 

spectroscopy. The samples were analyzed when received and then 15 additional times over the 

next 24 days. The activity results versus time, post sample, were plotted. Radon ingrowth is 

demonstrated in each set of sample results. Figure 5-2 and Table 5-13 present the data from one 

of the sludge samples. The following was observed:

 The Pb-214 and Bi-214, short-lived progeny of Rn-222, increased from approximately 

50 percent of the Ra-226 activity in the sample to 85 percent of the Ra-226 activity. 

Radium-226 was identified directly from the 186 keV gamma line. The average of the 

Pb-214 and Bi-214 results was 70 pCi/g at day zero and 120 pCi/g at day 24 compared to the 

Ra-226 activity of 142 pCi/g each day.

 Radon gas progeny were present at 50 percent of the Ra-226 activity in the recently 

generated sludge. Only 50 percent of the Rn gas escapes the sludge during processing.

 The Rn gas only increased to 85 percent of the Ra-226 parent activity in three weeks. This 

could be due to leakage of Rn through the sample container seal.

 The reported U-235 activity (185.7 keV gamma line) was consistently measured at 8.6 pCi/g, 

matching the theoretical overestimation of 8.7 pCi/g of U-235 based on 142 pCi/g of Ra-226. 

See Section 2.3.2 and Table 2-1 for a detailed discussion of Ra-226 and U-235 identification 

and potential overestimation using gamma spectroscopy. The U-235 identified by the 

205 keV line was consistently 0 pCi/g.

Figure 5-2. Ra-226 Progeny Ingrowth versus Days (Days Post Removal)

5.4 Landfill Worker Exposure Assessment

5.4.1 Landfill External Radiation Exposure

The maximum average gamma radiation exposure rate measured at any of the nine selected 

landfills was 13.5 R/hr. The minimum, limiting local background measured was 5 R/hr.

Assuming the duration of exposure is a full occupational year of 2,000 hours, the external 

gamma radiation exposure at the landfill was estimated as follows:

0.00

25.00

50.00

75.00

100.00

125.00

150.00

0 5 10 15 20 25

pCi/g

Days

Wastewater Treatment Filter Cake 

Pb-212 (238 keV)

Pb-214 (351 keV)

Bi-214 (609 keV)

Ra-226 (186 keV)

Ac-228 (911 keV)

Ac-228 (969 keV)

U-235 (185 keV)

U-235 (205 keV)
PA DEP TENORM Study Report – Section 5.0 Rev. 0

January 2015 5-6

Maximum Average Landfill External Gamma Exposure Estimate

(13.5 – 5) μR/hr x 2,000 hr/yr x (1 mrem/1,000 μR gamma) = 17 mrem/yr

This is an estimate of the maximum average exposure based on 2,000 hours in one year. The 

result is less than the 100 mrem/yr dose equivalent limit for a member of the public. Actual 

exposure is dependent upon the actual exposure rates and occupancy time for individual workers.

The maximum exposure rate measured at any of the nine selected landfills was 93.7 R/hr.

Work in this area would result in an exposure of 100 mrem in 1,130 hours of annual exposure of 

an employee’s 2,000-hour occupational year. Actual annual exposure for a landfill worker is 

dependent upon actual exposure rates and actual time worked in the proximity of the tank.

5.4.1.1 Landfill Worker Potential Internal Alpha/Beta Radioactivity Exposure

The total and removable / survey results are presented in Sections 5.2.5.1 and 5.2.5.2. None 

of the 195  measurements and 17 of the 195  measurements of total surface radioactivity 

exceeded the RG 1.86 criteria. None of the 205 removable  or  surface radioactivity 

measurements exceeded the RG 1.86 criteria. The average values for total and removable  and 

 surface radioactivity are below the RG 1.86 criteria, indicating that there is little potential for 

internal  and  exposure to landfill workers.

5.4.1.2 Landfill Worker Internal Radon Exposure

The results of the landfill ambient air Rn samples are presented in Section 5.2.4. The Rn in 

ambient air at the fence line of the landfills ranged from 0.2 to 0.9 pCi/L consistent with U.S. 

background levels of 0.2 – 0.7 pCi/L in outdoor ambient air. Consequently, the potential for 

internal Rn exposure is low.
PA DEP TENORM Study Report – Section 5.0 Rev. 0

January 2015 5-7

Table 5-1. Landfill Leachate – Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/l)

Ra-228 

(pCi/l)

K-40 

(pCi/l)

Gross Alpha 

(pCi/l)

Gross Beta 

(pCi/l)

LF-10-LQ-024 322 < 20 201 < 140 < 192

LF-11-LQ-025 109 13 485 < 145 491

LF-12-LQ-026 102 < 6 558 < 129 440

LF-13-LQ-027 81.0 < 11 369 < 155 284

LF-14-LQ-028 101 19 1,110 < 167 1,110

LF-15-LQ-029 121 < 10 1,060 < 163 1,020

LF-16-LQ-030 114 < 7 122 < 136 < 191

LF-17-LQ-031 342 < 21.0 524 < 126 489

LF-18-LQ-032 120 < 25.0 764 < 161 703

LF-19-LQ-033 159 < 105 1,040 < 193 1,200

LF-20-LQ-034 < 130 < 110 615 182 806

LF-21-LQ-035 < 87.0 < 10.0 670 < 162 850

LF-22-LQ-036 < 77.0 < 13.0 332 < 156 531

LF-23-LQ-037 < 148 < 26.0 268 < 306 489

LF-24-LQ-038 145 < 15.0 477 < 134 489

LF-25-LQ-039 79.0 < 12.0 175 < 118 < 199

LF-26-LQ-040 < 146 < 31.0 268 < 134 < 190

LF-27-LQ-041 < 108 < 22.0 148 < 205 < 203

LF-28-LQ-042 < 89.0 < 16.0 64.0 < 277 < 221

LF-29-LQ-043 416 < 19.0 181 < 119 < 200

LF-30-LQ-044 84.0 < 6.00 551 < 342 412

LF-31-LQ-045 150 < 9.00 282 < 206 < 203

LF-32-LQ-046 < 78.0 < 21.0 < 41.0 < 125 < 189

LF-33-LQ-047 < 153 < 37.0 573 < 146 667

LF-34-LQ-048 < 111 < 21.0 423 < 157 401

LF-35-LQ-049 136 < 19.0 758 < 254 728

LF-36-LQ-050 106 22.0 471 < 353 466

LF-37-LQ-051 73.0 19.0 503 < 341 845

LF-38-LQ-052 54.0 < 5.00 249 < 152 550

LF-39-LQ-053 < 82.0 < 18.0 222 < 149 < 194

LF-40-LQ-054 91.0 35.0 505 < 143 239

LF-41-LQ-055 65.0 9.00 383 < 164 286

LF-42-LQ-056 < 72.0 < 16.0 < 54.0 < 137 384

LF-43-LQ-057 371 < 8.00 110 < 128 < 199

LF-44-LQ-058 101 < 12.0 629 < 206 365

LF-45-LQ-059 < 73.0 < 14.0 480 < 111 < 208

LF-46-LQ-060 140 15.0 354 < 486 < 416

LF-47-LQ-061 70.0 13.0 131 < 121 < 202

LF-48-LQ-062 57.0 < 5.00 354 < 181 284

LF-49-LQ-063 126 < 9.00 209 < 316 < 232

LF-50-LQ-064 85.0 < 10.0 128 < 112 < 201

LF-51-LQ-065 106 9.00 49.0 < 113 < 202
PA DEP TENORM Study Report – Section 5.0 Rev. 0

January 2015 5-8

Table 5-1. Landfill Leachate – Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/l)

Ra-228 

(pCi/l)

K-40 

(pCi/l)

Gross Alpha 

(pCi/l)

Gross Beta 

(pCi/l)

Average 112 11.9 401 94.4 389

Std. Dev. 89.5 11.4 275 43.6 311

Median 84.5 9.00 362 77.8 326

Minimum 54.0 2.50 20.5 56.0 95.0

Maximum 416 55 1,110 243 1,200

< – indicates a value less than the reported number which is the MDC.

Table 5-2. Selected Landfill Leachate – Gamma Spectroscopy and Miscellaneous Results

Sample ID Ra-226 

(pCi/l)

Ra-228 

(pCi/l)

K-40 

(pCi/l)

Gross Alpha 

(pCi/l)

Gross Beta 

(pCi/l)

LF-01-LQ-002 378 < 20.0 < 72.0 < 3.46 < 2.07

LF-02-LQ-003 136 84.0 637 < 110 295

LF-03-LQ-008 < 74.0 < 13.0 221 < 275 < 202

LF-04-LQ-009 118 < 6.00 64.0 < 253 < 395

LF-05-LQ-023 < 101 < 20.0 182 < 323 < 233

LF-06-LQ-010 85.0 < 8.00 351 < 160 259

LF-07-LQ-004 < 134 < 35.0 353 < 121 221

LF-08-LQ-017 70.0 9.00 743 < 357 280

LF-09-LQ-005 105 1,100 18,100 < 314 < 233

Average 106 139 2,299 106 176

Std. Dev. 107 361 5,930 59.8 98.5

Median 70.0 10.0 351 127 198

Minimum 85.0 3.00 36.0 1.73 1.04

Maximum 378 1,100 18,100 179 295

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 5.0 Rev. 0

January 2015 5-9

Table 5-3. Landfill Leachate Original and Aqueous Sample Analysis Results

Sample 

ID

Original Gamma Spec –

Unfiltered Sample

Re-Analysis Using EPA 903.1/904.0 Technique –

Aqueous Phase Sample Only

Ra226 

Result 

(pCi/L)

Ra226 

Error 

(pCi/L)

Ra226 

MDC 

(pCi/L)

Ra226 

Result 

(pCi/L)

Ra226 

Error 

(pCi/L)

Ra226 

MDC 

(pCi/L)

Ra228 

Result 

(pCi/L)

Ra228 

Error 

(pCi/L)

Ra228 

MDC 

(pCi/L)

LF-17-LQ031 342 92.0 131 10.3 0.294 0.063 7.821 1.02 0.956

LF-24-LQ038 145 60.0 91.0 1.91 0.107 0.032 4.274 1.063 1.329

LF-13-LQ027 81.0 33.0 51.0 1.70 0.103 0.021 2.195 0.806 1.083

LF-45-LQ059 47.0 45.0 73.0 0.472 0.085 0.09 0.896 0.662 0.998

LF-18-LQ032 120 73.0 115 6.01 0.218 0.073 5.768 0.946 0.966

LF-10-LQ024 322 85.0 121 1.22 0.089 0.057 1.413 0.77 1.125

LF-08-LQ017 54.0 26.0 41.0 0.414 0.067 0.068 1.058 0.732 1.093

LF-12-LQ026 102 40.0 62.0 0.842 0.086 0.069 2.546’s 0.771 1.004

LF-01-LQ002 378 96.0 132 0.066 0.027 0.03 0.643 0.664 1.037

LF-04-LQ009 118 34.6 53.0 0.124 0.031 0.017 0.976 0.717 1.079
PA DEP TENORM Study Report – Section 5.0 Rev. 0

January 2015 5-10

Table 5-4. Selected Landfill Effluent Leachate –

Gamma Spectroscopy and Miscellaneous Results

Source of 

Sample Sample ID Ra-226 (pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross 

Alphaa

(pCi/L)

Gross 

Betaa

(pCi/L)

Effluent LF-01-LQ-002 378 < 20 < 72.0 < 3.46 < 2.07

Effluent LF-02-LQ-003 136 84.0 637 < 110 304

Effluent LF-03-LQ-008 < 140 16 221 < 275 < 202

Effluent LF-04-LQ-009 118 < 6 64.0 < 253 < 395

Effluent LF-07-LQ-004 < 134 < 35 353 < 121 221

Effluent LF-09-LQ-005 105 1,100 18,100 < 314 < 233

Effluent LF-09-LQ-021 117 15.0 165 ND ND

Average 142 178 2,800 89.7 157

Std. Dev. 107 408 6,750 59.9 106

Median 117 16.0 221 93.5 157

Minimum 67.0 3.00 36.0 1.73 1.04

Maximum 378 1,100 18,100 157 304

aND – Sample Matrix was not suitable for analysis.

< – indicates a value less than the reported number which is the MDC.

Table 5-5. Selected Landfill Influent Leachate –

Gamma Spectroscopy and Miscellaneous Results

Source of 

Sample Sample ID Ra-226 (pCi/L)

Ra-228 

(pCi/L)

K-40 

(pCi/L)

Gross Alpha 

(pCi/L)

Gross Beta 

(pCi/L)

Influent LF-01-LQ-019 < 139 < 21 236 < 18.3 117

Influent LF-02-LQ-020 < 120 15 755 < 201 524

Influent LF-03-LQ-015 116 < 14 246 < 168 < 203

Influent LF-04-LQ-016 92.0 < 15 571 < 134 416

Influent LF-05-LQ-023 115 < 20.0 182 < 323 < 233

Influent LF-06-LQ-010 85.0 < 8.00 351 < 160 259

Influent LF-07-LQ-011 < 97 < 8.00 278 < 200 < 200

Influent LF-08-LQ-017 70 9 743 < 357 280

Influent LF-09-LQ-012 95 < 9 242 < 195 < 200

Average 83.4 7.94 400 97.6 224

Std. Dev. 23.5 3.64 227 49.9 158

Median 85.0 7.50 278 97.5 117

Minimum 48.5 4.00 182 9.15 100

Maximum 116 15.0 755 179 524

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 5.0 Rev. 0

January 2015 5-11

Table 5-6. Selected Landfill Solids, Filter Cake – Gamma Spectroscopy Results

Sample ID Ra-226 

(pCi/g)

Ra-228 

(pCi/g)

K-40 

(pCi/g)

LF-02-SL-002 8.73 4.98 4.83

LF-03-SL-004 53.0 5.03 2.72

LF-04-SL-005 11.1 1.53 2.73

Average 24.3 3.85 3.43

Std. Dev. 24.9 2.01 1.22

Median 11.1 4.98 2.73

Minimum 8.73 1.53 2.72

Maximum 53.0 5.03 4.83

Table 5-7. Selected Landfill Solids, Sediment – Gamma Spectroscopy Results

Sample ID Ra-226 

(pCi/g)

Ra-228 

(pCi/g)

K-40 

(pCi/g)

U-238 

(pCi/g)

U-235 

(pCi/g)

Th-232 

(pCi/g)

LF-01-SL-001 4.46 2.53 15.2 < 2.51 0.177 2.48

LF-02-SL-003 2.82 1.44 12.8 < 0.671 < 0.069 1.41

LF-04-SL-006 3.44 0.979 10 < 0.868 < 0.128 0.960

Average 3.57 1.65 12.67 0.675 0.092 1.62

Std. Dev. 0.828 0.796 2.60 0.505 0.075 0.781

Median 3.44 1.44 12.80 0.434 0.064 1,41

Minimum 2.82 0.979 10.00 0.336 0.035 0.96

Maximum 4.46 2.53 15.20 1.26 0.177 2.48

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 5.0 Rev. 0

January 2015 5-12

Table 5-8. Selected Landfill Radon Concentrations

Sample ID County Location Exp. End 

Date

Radon Conc. +/- 2 S.D. 

(pCi/L)

MDC 

(pCi/L)

LF-01-RA McKean 01 1/2014 0.2 ± 0.2 0.2

02 1/2014 0.4 ± 0.2 0.2

03 1/2014 0.3 ± 0.2 0.2

04 1/2014 0.4 ± 0.2 0.2

LF-02-RA Elk 01 6/2014 0.2 ± 0.2 0.2

02 6/2014 0.3 ± 0.2 0.2

03 6/2014 Missing

04 6/2014 0.4 ± 0.2 0.2

LF-03-RA Butler 01 6/2014 0.3 ± 0.2 0.2

02 6/2014 0.5 ± 0.2 0.2

03 6/2014 0.9 ± 0.2 0.2

04 6/2014 0.4 ± 0.2 0.2

LF-04-RA Butler 01 6/2014 0.3 ± 0.2 0.2

02 6/2014 0.7 ± 0.2 0.2

03 6/2014 0.5 ± 0.2 0.2

04 6/2014 0.4 ± 0.2 0.2

LF-05-RA Fayettea01 7/2014 <0.4 0.4

02 7/2014 <0.4 0.4

03 7/2014 <0.4 0.4

04 7/2014 <0.4 0.4

LF-06-RA Fayettea01 7/2014 <0.4 0.4

02 7/2014 <0.4 0.4

03 7/2014 <0.4 0.4

04 7/2014 <0.4 0.4

LF-07-RA Washingtona01 7/2014 <0.4 0.4

02 7/2014 <0.4 0.4

03 7/2014 <0.4 0.4

04 7/2014 <0.4 0.4

LF-08-RA Somerseta01 7/2014 <0.4 0.4

02 7/2014 <0.4 0.4

03 7/2014 <0.4 0.4

04 7/2014 <0.4 0.4

LF-09-RA Cambriaa01 7/2014 <0.4 0.4

02 7/2014 <0.4 0.4

03 7/2014 <0.4 0.4

04 7/2014 <0.4 0.4

The ATD laboratory does not report an error term on devices with results below their MDA.

a Represents landfills with ATDs deployed.
PA DEP TENORM Study Report 

– Section 5.0 Rev. 0

January 2015 5-13

Table 5-9. Selected Landfill Removable Alpha and Beta Surface Radioactivity Results Summary

Note: During the calculations to convert from raw counts to dpm, the calculated value was compared to half of the MDC. If the value was below 

this number, half of the MDC was inserted into the tables. Where the standard deviation is zero and the minimum, maximum, and average are the 

same, then all measurements were below half of the MDC.

Site ID

No. of 

Data 

Points

Removable Alpha (dpm/100 cm2) Removable Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

LF-01-FS-073 31 4.25 11.3 1.27 4.48 65.0 65.0 0.00 65.0

LF-03-FS-076 27 5.80 5.80 0.00 5.80 63.0 63.0 0.00 63.0

LF-05-FS-050 27 8.30 8.30 0.00 8.30 64.0 64.0 0.00 64.0

LF-08-FS-070 19 5.80 5.80 0.00 5.80 63.0 63.0 0.00 63.0

LF-02-FS-135 30 4.25 4.25 0.00 4.25 65.0 65.0 0.00 65.0

LF-04-FS-132 23 7.30 7.30 0.00 7.30 63.0 63.0 0.00 63.0

LF-06-FS-131 10 5.80 5.80 0.00 5.80 63.0 63.0 0.00 63.0

LF-09-FS-133 30 7.30 7.30 0.00 7.30 63.0 63.0 0.00 63.0

LF-07-FS-134 10 7.30 7.30 0.00 7.30 63.0 63.0 0.00 63.0
PA DEP TENORM Study Report 

– Section 5.0 Rev. 0

January 2015 5-14

Table 5-10. Selected Landfill Total Alpha and Beta Surface Radioactivity Results Summary

Site ID

No. of 

Data 

Points

Total Alpha (dpm/100 cm2) Total Beta (dpm/100 cm2)

Minimum Maximum Standard 

Deviation Average Minimum Maximum Standard Deviation Average

LF-01-FS-073 26 7.45 39.8 9.42 13.0 301 779 112 332

LF-03-FS-076 28 7.45 84.6 21.7 18.1 288 3,630 642 682

LF-05-FS-050 27 7.45 29.8 6.84 11.4 285 942 221 410

LF-08-FS-070 19 7.45 24.9 5.08 9.81 268 1,900 524 580

LF-02-FS-135 22 18.6 38.9 4.61 20.3 288 1,270 356 692

LF-04-FS-132 22 7.50 69.6 17.5 13.3 274 1,559 371 646

LF-06-FS-131 10 7.45 49.7 13.5 14.9 289 766 194 381

LF-09-FS-133 30 7.45 19.9 5.00 10.8 272 1,360 250 401

LF-07-FS-134 11 7.45 19.9 4.45 9.94 468 1,960 578 730

Note: During the calculations to convert from raw counts to dpm, the calculated value was compared to half of the MDC. If the value was below 

this number, half of the MDC was inserted into the tables. Where the standard deviation is zero and the minimum, maximum, and average are the 

same, then all measurements were below half of the MDC.
PA DEP TENORM Study Report – Section 5.0 Rev. 0

January 2015 5-15

Table 5-11. Selected Landfill Gross Gamma Radiation Scan Results Summary

Site GWS Maxa

(cpm)

GWS Mina

(cpm)

GWS 

Averagea

(cpm)

GWS Std 

Dev (cpm)

No. Data 

Points

LF-01 74,928 3,837 9,250 1,656 9,210

LF-02 16,737 3,299 9,097 2,954 13,977

LF-03 13,900 5,141 8,022 1,713 11,484

LF-04 16,545 5,272 10,742 2,807 8,691

LF-05 14,730 3,783 8,190 2,658 8,942

LF-06 10,994 5,118 7,649 902 9,129

LF-07 11,620 4,530 7,190 1,260 5,432

LF-08 18,894 3,466 6,573 1,909 10,977

LF-09 27,144 4,304 10,816 2,914 9,779

aConvert count rate data to exposure rate by dividing count rate by 800 to yield μR/hr.

Table 5-12. Results Summary of NaI Count Rate Data Converted to Exposure Rates

Site GWS Max 

(μrem/hr)

GWS Min 

(μrem/hr)

GWS 

Average 

(μrem/hr)

GWS Std 

Dev 

(μrem/hr)

No. Data 

Points

LF-01 93.7 4.80 11.6 2.07 9,210

LF-02 20.9 4.12 11.4 3.69 13,977

LF-03 17.4 6.43 10.0 2.14 11,484

LF-04 20.7 6.59 13.4 3.51 8,691

LF-05 18.4 4.73 10.2 3.32 8,942

LF-06 13.7 6.40 9.56 1.13 9,129

LF-07 14.5 5.66 8.99 1.58 5,432

LF-08 23.6 4.33 8.22 2.39 10,977

LF-09 33.9 5.38 13.5 3.64 9,779
PA DEP TENORM Study Report – Section 5.0 Rev. 0

January 2015 5-16

Table 5-13. Gamma Spectroscopy Results (pCi/g) of 

Sealed Wastewater Treatment Sludge Sample Over 24 Days

U-235

184 KeV

8.588.098.678.648.718.738.448.688.788.728.688.648.698.608.758.728.71

Ac-228

969 KeV

15.015.115.315.115.615.315.315.315.315.416.315.215.115.115.415.415.3

Ac-228

911 keV

14.914.814.914.814.815.114.914.515.014.914.814.814.715.014.814.714.8

Ra-226

186 keV

141133143142143144139143145144143142143142144144143

Bi-214

1,764 

keV

77.890.178.395.598.5

100102102105106106106108108108108109

Bi-214

1,120 

keV

70.4

81

91.7

114117119120120124125124125126126128128127

Bi-214

609 keV

63

72.586.5

105110109111111116115116116119117119120118

Pb-214

351 keV

68.878.688.8

110112114115116119120120121126122123122123

Pb-214

295 keV

68.177.387.7

108110112113114117119118119119120120120121

Pb-212

300 keV

2.112.522.211.962.381.992.212.01

#NA

1.582.452.031.821.592.021.76

Pb-212

238 keV

2.4

1.552.382.072.012.041.991.99

2

1.982.011.981.981.982.052.042.07

Time

(days)

T00T01T02T07T08T09T10T11T14T15T16T17T18T21T22T23T24

N/A – indicates the analyte was not requested and subsequently not reported by the laboratory.
PA DEP TENORM Study Report – Section 6.0 Rev. 0

January 2015 6-1

6.0 GAS DISTRIBUTION AND END USE

Uranium-238 is distributed throughout the crust of the earth, typically at concentrations of 

0.33 to 1.0 pCi/g. However, concentrations can be much higher in certain rock types or 

formations. The U-238 decay series consists of 18 decay progeny, including Rn. Radon is the 

only member of the decay series that is a gas at typical ambient conditions. All of the other

decay series members are solids. Because Rn is a gas, it is highly mobile within the soil and 

rock matrix and it easily enters into structures. There are two additional potential pathways for 

Rn entry into structures: well water and natural gas combustion, e.g., cooking and unvented 

heating. Natural gas samples were collected at underground storage sites, natural gas-fired 

power plants, gas compression and transmission facilities, and natural gas processing plants.

6.1 Natural Gas in Underground Storage

Natural gas samples were collected at four underground storage sites in Pennsylvania. Duplicate 

samples were collected at each site during injection into the storage formation and during 

withdrawal from the storage formation. Sampling during injection was conducted during the 

period of May to August 2013. Sampling during withdrawal was conducted during the period of

January to early February 2014. At three of the sites the samples were obtained from the exhaust 

of the gas chromatograph, which continuously analyzes the natural gas. At the fourth site, the 

sample was collected from the injection flow dehydration unit. The results for injection 

sampling are presented in Table 6-1. The results for withdrawal sampling are presented in 

Table 6-2. The results indicate Rn concentrations are lower after underground storage. The Rn 

analytical reports are presented in Appendix H.

6.2 Natural Gas-Fired Power Plants

Two natural gas-fired power plants (PP-01 and PP-02) were surveyed for gamma radiation 

exposure rates. Natural gas samples were collected at both plants, and ambient Rn

measurements were performed at the PP-02 fence line. The natural gas Rn concentration results 

are presented in Table 6-3, and the ambient Rn concentrations measured at the plant fence line 

are presented in Table 6-4. All of the Rn analytical reports are presented in Appendix H.

The gamma radiation exposure rate survey at the PP-02 power plant was conducted using a

Ludlum Model 19 Micro-R Meter. With the exception of one area, the range of measurement 

results observed were 5-10 μR/hr, which is within the range of natural background of gamma 

radiation for Pennsylvania. The exception occurred on the external surface of a pipe elbow

where the range of measurement results observed were 15-17 μR/hr. During a subsequent 

survey event, the measurement results observed at the surface of that pipe elbow were 5-10 

μR/hr, which is within the range of natural background of gamma radiation levels.

Ambient air was sampled at the PP-02 power plant site fence line. Eight EIC passive Rn 

monitors were used. The monitors were deployed at the fence line around the power plant in 

roughly the four cardinal directions. See figures in Appendix E for exact locations. The 

monitors were placed, in duplicate, inside a single Tyvek®bag. The Tyvek®bag is permeable to 

Rn gas but impermeable to particulate matter. The monitors were hung on the fence line 

approximately 5 ft above grade. Deployment of the Rn monitors was for 64 days. The fence line 
PA DEP TENORM Study Report – Section 6.0 Rev. 0

January 2015 6-2

Rn monitor results were all at or below the MDC value for the analysis. The results are 

presented in Table 6-4. The Rn analytical reports are presented in Appendix H.

6.3 Compressor Stations

Duplicate natural gas samples were collected at intake flow lines of both facility CS-01 and 

CS-03. Duplicate samples were collected at the compressor station discharge at facility CS-04.

The CS-04 compressor station is associated with the natural gas processing plant (CP-01) 

discussed below. Because of high pressure in the intake flow lines, duplicate natural gas samples 

were collected at the continuous natural gas quality analyzer at CS-02. This sample point is a 

small line off of a main exhaust for CS-02. All compressor stations were receiving 

predominately Marcellus Shale unconventional natural gas at the time of sample collection.

Radon-measured concentrations are presented in Table 6-5. The compressor station natural gas 

Rn results are consistent with the production site Rn sample results. The Rn analytical reports 

are presented in Appendix H.

Ambient air was sampled at the CS-01 compressor station fence line for the measurement of Rn 

concentrations. Eight EIC passive Rn monitors were used. The monitors were deployed at the 

fence line around the power plant in roughly the four cardinal directions. See figures in 

Appendix E for exact locations. The monitors were placed, in duplicate, inside a single Tyvek®

bag. The Tyvek®bag is permeable to Rn gas but impermeable to particulate matter. The

monitors were hung on the fence line approximately 5 ft above grade. Deployment of the Rn 

monitors was for 62 days. The fence line Rn monitor results ranged from 0.1 to 0.8 pCi/L. The 

average concentration at each fence line location was within the range of typical ambient 

background Rn concentrations in outdoor ambient air in the U.S. The results are presented in 

Table 6-6. The Rn analytical reports are presented in Appendix H.

6.4 Natural Gas Processing Plant

Two natural gas samples were collected at the processing plant (CP-01) on two separate 

occasions: March 12, 2014 and September 11, 2014. The results are presented in Table 6-7.

The Rn analytical reports are presented in Appendix H.

Gamma radiation exposure rate surveys were performed during the two site visits. The exposure 

rate surveys were performed using a Ludlum Model 19 Micro-R Meter. The first survey was 

performed on a rainy, windy day, limiting the outdoor areas surveyed. The results include:

 Background in areas not impacted by the plant – 5-10 R/hr.

 General areas of the plant – 5-10 R/hr.

 Filter housings (exposure rate measured on the outside surface):

 Contact readings measured on contact with filter housings ranged from background to

75 R/hr, with two exceptions; one measured 350 R/hr and the other measured 

900 R/hr.

 Propane processing – radiation exposure rates measured up to 380 R/hr on contact with heat 

exchangers, reboilers, pipelines, and pumps.

 Propane storage area:

 Pipeline exposure rates measured from local background to 400 R/hr on contact.
PA DEP TENORM Study Report – Section 6.0 Rev. 0

January 2015 6-3

 Ladder to decking area measured 80 R/hr general area.

 Decking above ladder measured 50 R/hr general area.

 Propane storage tank measured 210 R/hr on contact.

 Propane tank trailer being filled – 100 R/hr on contact with the tank.

 Rail yard:

 Tank filling area – local background to 20 R/hr general area.

 Racks of filling pipes – local background to 100 R/hr on contact.

 Propane rail car tank – 30 R/hr on contact.

Radon in natural gas sample results are presented in Table 6-7. The highest concentration of Rn, 

71.1 pCi/L, was measured in natural gas entering the processing plant. The lowest concentration 

of Rn, 8.6 pCi/L, was measured in natural gas at the processing plant outflow. The Rn analytical 

reports are presented in Appendix H.

A second visit to the facility was made to survey and sample filter media. The filter housing 

with the highest exposure rate measured was selected for sampling and gamma spectroscopy 

analysis. The outside of the filter housing measured 50 R/hr. The general radiation exposure 

rate in the area of the filters was 15 R/hr. The filter housing on the facility propenizer 

equipment was opened during a filter change-out and a sample of the cardboard filter media was 

collected. The filter media sample was smeared for removable  and  surface radioactivity.

Smear samples of removable  and  surface radioactivity were taken on each of the individual 

filter cases housing the filter media within the filter bank. The gross  and  removable surface 

radioactivity results summary statistics of the 11 smear sample counts from the filter case are 

presented in Table 6-8. The average  and  surface radioactivity levels are below the RG 1.86 

 and  removable surface radioactivity criterion.

The results of the filter gamma spectrometry analysis are presented in Table 6-9. A Pb-210 

activity result of 3,580 pCi/g was identified, but no other gamma-emitting NORM radionuclide 

results were above 1 pCi/g. The gross  and  removable surface radioactivity results for the 

filter media sample are presented in Table 6-10. The results are elevated relative to the RG 1.86 

gross  and  removable surface radioactivity criterion.

6.5 Potential Exposure from Gas Scale Inside Pipes and Equipment

Materials deposited on interior surfaces of natural gas plant pipes and equipment are different 

from conventional oil industry Ra-based pipe scale. Natural gas plant scale typically consists of 

Rn decay progeny that accumulate on the interior surfaces of plant pipes and equipment without 

the long-lived Ra parent.

As a result, the only radionuclides that remain and adhere to the interior surfaces of 

machinery/pipes are the Rn decay progeny Po-210 and Pb-210. These longer-lived decay 

progeny are not readily detected on the outside of pipes. However, Pb-210 and Po-210 emit 

and  radioactive particles that may be a potential inhalation or ingestion hazard when pipes and 

machinery are opened for maintenance and/or cleaning.

Access to the internal surfaces of pipes and equipment for surveys of surface  and  activity 

was not available. However, the facility propenizer equipment opened and sampled during filter 
PA DEP TENORM Study Report – Section 6.0 Rev. 0

January 2015 6-4

change-out is representative of interior conditions and was described in Section 6.4. The results 

are presented in Table 6-9. A Pb-210 activity result of 3,580 pCi/g was identified. No other 

gamma-emitting NORM radionuclides above 1 pCi/g were identified. The results confirm the 

build-up of the longer-lived Rn decay progeny in equipment and pipes. The concentration of 

Pb-210 identified may present a potential inhalation or ingestion hazard during routine system 

maintenance.

6.6 Radon Dosimetry

Radon exposure in homes due to the use of natural gas appliances is presented in this section. 

Radon is transported with natural gas into structures (homes, apartments, and buildings) that use

natural gas for purposes such as heating and cooking.

The incremental increase of Rn-222 for a typical home was estimated using the values and 

assumptions presented in Table 6-11 and as follows:

1. Well Site Rn-222 Concentration in Natural Gas  For the Rn gas concentration, only 

production site samples from Marcellus Shale well sites were used (n=16). The median 

value was 43.6 pCi/L, and the maximum value was 148 pCi/L. Both of these values are used 

in the estimations of potential Rn exposure.

2. Natural Gas/Rn-222 Transit Time and Decay  Assumed there is no Rn decay during transit.

3. Radon-222 Influx Rate  The American Gas Association average natural gas use per day 

value of 5,465 L/day was used. The value does not consider the types of appliances used.

The amount of Rn liberated into the home per hour is calculated using the estimated natural 

gas use per day (5,465 L/day) and the Rn concentration in that natural gas (43.6 and 

148 pCi/L). The resulting values are 238,274 pCi/day for the median concentration and 

808,820 pCi/day for the maximum concentration. Dividing each value by 24 hours per day 

results in 9,928 pCi/hr and 33,700 pCi/hr, respectively. These estimates assume that none of 

the appliances are vented. Consequently, all of the Rn in the natural gas is assumed to be 

liberated into the residence.

Rn-222 Influx Rate = (5,465 L/day x 43.64 pCi/L) / 24 hrs/day = 9,928 pCi/hr

Rn-222 Influx Rate = (5,465 L/day x 148 pCi/L)/ 24 hrs/day = 33,700 pCi/hr

4. Air Exchange Rate  Using a residence volume of 385,152 L and an air exchange rate of 

0.68 air changes per hour, 261,903 L/hr of home air is exchanged with outdoor air.

5. Consistent with EPA Rn assessments, an equilibrium factor of 40 percent is assumed.

6. Indoor Rn-222 Activity Concentration  The Rn-222 influx per hour divided by the home air 

exchange rate per hour, 9,928 pCi/hr / 261,903 L/hr = 0.04 pCi/L for the median value.

The Rn-222 influx per hour divided by the home air exchange rate per hour, 33,700 pCi/hr / 

261,903 L/hr = 0.13 pCi/L for the maximum value. This is the increase in Rn-222 in the 

home resulting from natural gas use containing both a median value of 43.6 pCi/L and a 

maximum value of 148 pCi/L of Rn-222.
PA DEP TENORM Study Report – Section 6.0 Rev. 0

January 2015 6-5

The increase in Rn concentration of 0.04 and 0.13 pCi/L along with the standard values 

presented in Table 6-11 are used to estimate potential additional annual radiation dose to an 

exposed individual.

Therefore,

0.04 pCi⁄L ∗ 0.4

100 = 0.00016 WL

The cumulative exposure is then WL multiplied by the number of hours exposed divided by 

170 hrs/working month.

0.00016 WL ∗ 6,136 hrs/yr

170 hrs⁄working month

= .006 WLM/yr

This value was converted to a radiation dose by multiplying by the dose conversion factor, the 

tissue weighting factor, and the radiation weighting factor:

0.08 ∗

0.006 WLM

yr

∗

0.54 rad

WLM ∗

20 rem

rad ∗

1000 mrem

rem

= 5.2 mrem⁄yr

The result is 5.2 mrem/yr for the median dose and 17.8 mrem/yr for the maximum whole 

body effective dose.

Based on the Rn and natural gas data collected as part of this study and the conservative 

assumptions made, the incremental Rn increase in a home using natural gas appliances is 

estimated to be very small and would not be detectable by commercially available Rn testing 

devices. The radiation dose received by home residents is a small fraction of the allowable 

general public dose limit of 100 mrem/yr.
PA DEP TENORM Study Report – Section 6.0 Rev. 0

January 2015 6-6

Table 6-1. Natural Gas Underground Storage Radon Concentrations, Injection

Sample 

ID County Formation Geology

Sample 

Results, 

pCi/L

Injection Ave. 

Conc. ± 2 S.D 

(pCi/L)

MDC

(pCi/L)

US 01 Potter Oriskany Sandstone 32.6 and 

26.7 29.6 ± 8.2 0.2

US 02 Tioga Oriskany Sandstone 25.7 and 

21.2 23.5 ± 6.4 0.2

US 03 Armstrong Sandstone 20.4 and 

20.4 20.4 ± 0.0 0.2

US 04 Fayette Limestone 20.3 and 

21.2 20.8 ± 1.2 0.2

Scintillation Cells

Note: All results adjusted to ambient air by dividing by 1.054, according to Jenkins et. al., Health Physics, 

Vol. 106, No. 3, March 2014.

Table 6-2. Natural Gas Underground Storage Radon Concentrations, Withdrawal

Sample 

ID County Formation Geology

Sample 

Results, 

pCi/L

Withdrawal Ave. 

Conc. ± 2 S.D. 

(pCi/L)

MDC

(pCi/L)

US 01 Potter Oriskany Sandstone 4.9 and 5.3 5.1 ± 0.6 0.3

US 02 Tioga Oriskany Sandstone 10.9 and 9.3 10.1 ± 2.2 0.2

US 03 Armstrong Sandstone 5.6 and 5.9 5.8 ± 0.4 0.2

US 04 Fayette Limestone 10.8 and 

11.7 11.3 ± 1.2 0.4

Scintillation Cells

Note: All results adjusted to ambient air by dividing by 1.054, according to Jenkins et. al., Health Physics, 

Vol. 106, No. 3, March 2014.

Table 6-3. Natural Gas-Fired Power Plant Samples Analyzed for Radon Content

ID # County Gas Source Radon Conc. ± 2 Std. 

S.D. (pCi/L) MDC (pCi/L)

PP 01 Fayette Marcellus Shale 33.7 ± 1.8 1.5

PP 02 Berks Marcellus Shale 35.7 ± 11.0 0.2
PA DEP TENORM Study Report – Section 6.0 Rev. 0

January 2015 6-7

Table 6-4. Natural Gas-Fired Power Plants Ambient Fence Line Radon Monitors (PP 02)

Location Radon Conc. ± 2 S.D. (pCi/L) MDC (pCi/L)

West Fence 0.3 ± 0.2 0.2

0.4 ± 0.2 0.2

North Fence 0.1 ± 0.2 0.2

0.1 ± 0.2 0.2

East Fence 0.0 ± 0.2 0.2

0.2 ± 0.2 0.2

South Fence 0.2 ± 0.2 0.2

0.2 ± 0.2 0.2

Table 6-5. Compressor Station Radon Samples

Sample 

ID County Gas Source Radon Conc. ± 2 S.D. (pCi/L)

MDC 

(pCi/L)

CS-01-RG Berks Marcellus Shale 28.8 ± 1.4 0.2

CS-02-RG Fayette Mostly Marcellus Shale 39.8 ± 4.4 0.2

CS-03-RG Clinton 98% Marcellus Shale 34.0 ± 0.2 0.2

CS-04-RG Washington Marcellus Shale 58.1 ± 1.1 0.2

Table 6-6. Compressor Station Ambient Fence Line Radon Monitors (CS 01)

Location Radon Conc. ± 2 S.D. (pCi/L) MDC (pCi/L)

Northeast Fence 0.5 ± 0.2 0.2

0.8 ± 0.2 0.2

Southeast Fence 0.3 ± 0.2 0.2

0.3 ± 0.2 0.2

Northwest Fence 0.3 ± 0.2 0.2

0.1 ± 0.2 0.2

Southwest Fence 0.3 ± 0.2 0.2

0.2 ± 0.2 0.2

Table 6-7. Natural Gas Processing Plant Radon Samples

ID # County Gas Source Radon Conc. ± 2 S.D. 

(pCi/L)

MDC 

(pCi/L)

CP-01 Washington Processing Plant Inflow 1 67.7 ± 1.5 0.2

CP-01 Washington Processing Plant Inflow 2 71.1 ± 1.6 1.6

CP-01 Washington Processing Plant Outflow 

to Transmission Line 1

8.6 ± 0.4 0.3

CP-01 Washington Processing Plant Outflow 

to Transmission Line 1

9.3 ± 0.4 0.3
PA DEP TENORM Study Report – Section 6.0 Rev. 0

January 2015 6-8

Table 6-8. Compressor Station and Natural Gas 

Processing Plant Filter Case Removable Radioactivity Results

Facility ID No. of

Data Points

Removable Alpha (dpm/100 cm2)

Minimum Maximum Standard Deviation Average

CP-01-FS-136 11 4.70 29.6 8.78 15.5

Facility ID No. of Data 

Points

Removable Beta (dpm/100 cm2)

Minimum Maximum Standard Deviation Average

CP-01-FS-136 11 8.25 96.0 23.9 32.2

Table 6-9. Compressor and Natural Gas 

Processing Plant Filter Media, Gamma Spectroscopy

Nuclide Result Error MDC Units

Ac-228 0.141 0.053 0.077 pCi/g

Bi-212 0.287 0.000 0.373 pCi/g

Bi-214 0.564 0.082 0.054 pCi/g

K-40 1.30 0.216 0.225 pCi/g

Pb-210 3,580 552 14.2 pCi/g

Pb-212 0.066 0.044 0.071 pCi/g

Pb-214 0.629 0.070 0.076 pCi/g

Ra-226 0.585 0.566 0.926 pCi/g

Ra-228 0.141 0.053 0.077 pCi/g

Th-232 0.125 0.047 0.077 pCi/g

U-235 -0.105 0.000 0.382 pCi/g

U-238 -14.7 0.000 3.15 pCi/g

Table 6-10. Natural Gas Processing Plant Filter Media, Gross Alpha/Gross Beta

Sample Gross Alpha Gross Beta

Filter Media 708 ± 15.2 dpm/cm21,914 ± 11.9 dpm/cm2
PA DEP TENORM Study Report – Section 6.0 Rev. 0

January 2015 6-9

Table 6-11. Radon Dosimetry Values for a Typical Home

Parameter Value Reference

Median Sq. Feet of House 1,700 ft21

Ceiling Height 8 ft

Air Change Rate 0.68 2

Home Occupancy Factor 70% (6,136 hrs/yr) 3

Average Daily Nat. Gas Use 193 ft3/day (5,465 L/day) 4

Pipeline Distance 260 miles 5

Avg. pipeline speed (gas) 5 mph 6

Dose Conversion Factor 0.54 rad/WLM 7

Tissue Weighting Factor (Bronchial region) 0.08 7

Rad. Weighting Factor, alpha 20 rem/rad 7

Equilibrium Factor 0.4 3

Lung Cancer Risk per Unit Exposure 5.38E-4 per WLM 3

Table References:

1. U.S. Census, American Housing Survey, 2011, Table C-02-AH.

2. Nazaroff, W.W. and Nero, A.V. Radon and its Decay Products in Indoor Air. John Wiley & Sons, 

1988.

3. Pawal, D.J. and Puskin, J.S. EPA Assessment of Risks from Radon in Homes. U.S. EPA, June 2003.

4. American Gas Association, Washington, D.C.

5. National Pipeline Mapping System, User Guide, U.S. DOT, 2011.

6. Spectra Energy Transmission, Personal Communication, May 2014.

7. United Nations Scientific Committee on the Effects of Atomic Radiation (UNSCEAR), Annex E, 

2006.
PA DEP TENORM Study Report – Section 7.0 Rev. 0

January 2015 7-1

7.0 OIL AND GAS BRINE-TREATED ROADS

Brine produced from O&G wells and other sources such as brine treatment plants and brine wells 

is used as a dust suppressant and road stabilizer on unpaved secondary roads in Pennsylvania.

The O&G brine used is from conventional formations only. DEP has developed a fact sheet, 

Roadspreading of Brine for Dust Control and Road Stabilization, for use as a guide when 

utilizing brine on unpaved roads. The fact sheet was developed under the authority of the Clean 

Streams Law, the Solid Waste Management Act, and Chapters 78 and 101 of DEP’s Rules and 

Regulations (DEP 2013).

For this study, roads in the southwest, northwest, and north-central regions were surveyed and 

sampled. Most O&G operations occur in these regions. The surveys and sampling included:

 Thirty-two O&G brine-treated roads were surveyed. Thirty-one biased surface samples were 

collected from the O&G brine-treated roads. The biased locations were selected based on 

increased instrument audio response monitored by the technician during scan surveys.

 Eighteen reference background roads were surveyed, consisting of roads geographically 

close to an O&G brine-treated road that had not been identified as O&G brine-treated.

Fourteen surface samples were collected from reference background roads.

7.1 Gamma Radioactivity Survey Results

The surveys included gross gamma radiation scans performed using 2-inch x 2-inch NaI 

detectors and a Ludlum Model 2221 scaler/ratemeter instrument. Two detectors were attached to 

the hitch of a standard sport utility vehicle (SUV) approximately 3 ft apart. This detector array 

was offset to provide as much edge/shoulder coverage as possible. Each detector was mounted 

approximately 6 inches above the road surface. Every road had a complete scan on both sides.

A total of four detector passes on each road were conducted. The instrument data were recorded 

along with the location information using a pair of TrimbleTM ProXT global positioning system 

(GPS) units.

7.1.1 Gross Gamma Radiation Scan Results

Gross gamma radiation scans, recorded in cpm, were performed on 32 road surfaces treated with

O&G brine for dust suppression and road stabilization. The gamma radiation count rate data and 

GPS data were downloaded and placed on maps using the most recent aerial maps available from 

Pennsylvania Spatial Data Access (PASDA). GIS software was used to develop a graphic 

display of the gamma scan results. The resulting gamma radiation count rate intensity images 

are presented in Appendix E. The minimum, maximum, median, mean, and standard deviations 

for each data set are presented in Table 7-1. In addition to calculating the file statistics, a twosample student t-test was performed. 

The two-sample student t-test was used to compare the subject road (O&G brine-treated) results 

with a reference background road. ProUCL version 5.0 was used to perform the student t-test on 

the data. The Null Hypothesis tested is that the mean value of the treated road gamma radiation 

count rate data is statistically different from the mean value of the reference background road 

gamma radiation count rate data at the 95 percent confidence level. The results of the t-test for 
PA DEP TENORM Study Report – Section 7.0 Rev. 0

January 2015 7-2

each pair of road results are included in Table 7-1. Sixteen of 28 comparisons of O&G brinetreated and reference background roads are statistically different at the 95 percent confidence 

level. The t-test output files are included in Appendix G.

7.1.2 Gamma Radiation Exposure Rate Results Summary

Gross gamma radiation scan results in units of cpm were converted to R/hr using 800 cpm per 

R/hr, a conversion factor appropriate for Ra-226 gamma energy as detected with 2-inch by 

2-inch NaI detectors rounded to one significant figure (Table 6.4, NaI Scintillation Detector Scan 

MDCs for Common Radiological Contaminants, NUREG-1507, Minimum Detectable 

Concentrations With Typical Radiation Survey Instruments for Various Contaminants and Field 

Conditions, USNRC June 1998). Table 7-2 presents the results for each road.

7.2 Soil Sample Results

Biased surface soil samples were collected based on the audio response of the gamma scan 

survey instrument ratemeter on 31 of the 32 O&G brine-treated roads. When an area with 

elevated radioactivity was detected, surface soil samples were collected at that area.

7.2.1 Road Surface Soils Biased Sample Results

The gamma spectroscopy results are presented in Tables 7-3 through 7-5 for the U, Th, and Ac 

series radionuclides. A review of the U series radionuclides indicates excess Ra-226 activity in 

19 of 33 surface soil samples. For the purposes of this study, excess Ra-226 activity is defined 

as Ra-226 activity greater than the natural background U decay series activity in surface soil. 

The excess Ra-226 activity was determined as follows:

 The O&G brine applied to road surfaces contains Ra-226 and its progeny. It does not contain 

U, which is insoluble. Therefore, the U-238 activity identified in the gamma spectroscopy 

analysis results represents the natural background U series activity in surface soil for the 

area. The average U-238 activity of the 31 samples is 0.882 pCi/g. 

 U-235 makes up 0.7 percent by weight of natural U, which equates to 1/22 of the U-238 

activity. Therefore, 0.040 pCi/g of U-235 is present in the surface soil samples.

 Radium-226 is measured directly by detection of its 186.2 keV energy line (3.28 percent

yield). However, the presence of U-235 can cause interference with direct Ra-226 detection 

because it has a gamma line of similar energy (185.7 keV at 54 percent yield). In solid 

samples where natural U including U-238 and Ra-226 are at equal activity and U-235 is at 

1/22 the activity of U-238, overestimation of Ra-226 is quantified by multiplying the U-235 

activity by the ratio of the yields of the similar gamma radiation emissions, i.e., 54/3.28.

Therefore, the Ra-226 overestimation in the surface soil samples is equal to 0.660 pCi/g 

[0.040 pCi/g x (54/3.28) = 0.660 pCi/g].

 After correcting the reported Ra-226 activity by 0.882 pCi/g of natural background activity 

and 0.662 pCi/g of U-235 bias, 19 of 31 samples have excess Ra ranging from 0.108 to

5.42 pCi/g above natural background.
PA DEP TENORM Study Report – Section 7.0 Rev. 0

January 2015 7-3

See Section 2.3 for a complete discussion of the identification of NORM radionuclides by 

gamma spectroscopy.

The gamma spectroscopy results for the Th series radionuclides indicate the Th series is in 

secular equilibrium. The Th-232 mean and median values are essentially equal and the standard 

deviation is a fraction of the mean value, indicating the data is normally distributed. A normal 

distribution of radioactivity measurements is indicative of natural background radioactivity,

which is more homogeneous than contaminated soil. The mean Ra-228 activity of the 31 surface 

soil samples is 0.977 + 0.351 pCi/g. The range of the results is from 0.455 to 1.85 pCi/g.

7.2.2 Road Surface Soils – Reference Background Roads Soils

As a point of reference and for comparison, 18 roads in the geographic vicinity of the subject 

roads that have not been identified as O&G brine-treated were selected for surveying, and 14

biased soil samples were collected. The gamma spectroscopy results of the background samples 

are presented in Tables 7-6 through 7-8 for the U, Th, and Ac series radionuclides. A review of 

the U series radionuclides indicates excess Ra-226 activity in 14 surface soil samples. Excess 

Ra-226 activity is greater than the natural background U decay series activity in surface soil. 

The excess Ra-226 activity was determined as follows:

 The O&G brine applied to road surfaces contains Ra-226 and its progeny. It does not contain 

U, which is insoluble. Therefore, the U-238 activity identified in the gamma spectroscopy 

analysis results represents the natural background U series activity in surface soil for the 

area. The average U-238 activity of the 14 samples is 0.819 pCi/g.

 U-235 makes up 0.7 percent by weight of natural U, which equates to 1/22 of the U-238 

activity. Therefore, there is 0.037 pCi/g of U-235 present in the surface soil samples.

 Radium-226 is measured directly by detection of its 186.2 keV energy line (3.28 percent

yield). However, the presence of U-235 can cause interference with direct Ra-226 detection 

since it has a gamma line of similar energy (185.7 keV at 54 percent yield). In solid samples 

where natural U including U-238 and Ra-226 at equal activity and U-235 at 1/22 the activity 

of U-238, overestimation of Ra-226 is quantified by multiplying the U-235 activity by the 

ratio of the yields of the similar gamma emissions, i.e., 54/3.28. Therefore, the Ra-226 

overestimation in the surface soil samples is equal to 0.037 pCi/g x (54/3.28) = 0.61 pCi/g.

 After correcting the reported Ra-226 activity by 0.819 pCi/g of natural background activity 

and 0.71 pCi/g of U-235 bias, 11 of 14 samples have excess Ra ranging from 0.118 to

61.5 pCi/g above natural background.

See Section 2.3 for a complete discussion of the identification of NORM radionuclides by 

gamma spectroscopy.

The gamma spectroscopy results for the Th decay series are not normally distributed nor 

indicative of natural Th background radioactivity. Thorium-232 mean and median values are not 

equal and the standard deviation is large relative to the mean value, indicating the data are not 

normally distributed and heterogeneous. A normal distribution of radioactivity measurements is 

indicative of natural background radioactivity, which is more homogeneous than contaminated 
PA DEP TENORM Study Report – Section 7.0 Rev. 0

January 2015 7-4

soil. The mean Ra-228 activity of the 14 surface soil samples is 1.93 + 2.81 pCi/g. The range of 

the results is from 0.396 to 11.2 pCi/g.

The background reference road soil sample results are positive for excess Ra-226 at 11 of 14 

roads sampled. Three of the Ra-228 results are greater than 2.98 pCi/g, which is approximately 

three times natural background for the Th series. The excess Ra is higher than for the identified 

O&G brine-treated roads. The average excess Ra-226 for roads identified as having been O&G 

brine-treated is 1.13 pCi/g compared to an average of 8.23 pCi/g on the background reference 

roads. One possible explanation is that all of the roads have been treated with O&G brine. After

the 32 roads had been identified as O&G brine-treated, the reference background roads were 

selected by proximity to the 32 roads. Nothing precluded the selected background roads from 

having been treated with O&G brine.

7.3 Public Exposure to Oil and Gas Brine-Treated Roads

A total of 31 samples were collected from roads treated with O&G brine. An additional 14

surface soil samples were taken in reference background areas not expected to be impacted by 

O&G brine treatment. Both the treated and the reference background roads were positive for 

excess Ra. To evaluate potential exposure to the public from the O&G brine-treated roads, a

source term of 1 pCi/g of Ra-226 and 0.5 pCi/g of Ra-228 was assumed within a 6-inch layer of 

surface material (treated road surface).

The Argonne National Laboratory RESidual RADioactivity (RESRAD) Version 7.0 code for 

modeling exposure from residual radioactivity was used to evaluate potential exposure from the 

O&G brine-treated roads. RESRAD is a computer model designed to estimate radiation doses 

and risks from residual radioactive materials. RESRAD has been used widely by DOE, its 

operations and area offices, and its contractors for deriving limits for radionuclides in soil.

RESRAD has also been used by EPA, U.S. Army Corps of Engineers (USACE), NRC, industrial 

firms, universities, and foreign government agencies and institutions. The recreationist is an 

appropriate exposure scenario based on the remote location of the roads. A recreationist, such as 

a jogger or hunter, usually spends less time on the impacted area, e.g., two hours a day, three 

days a week, than a resident. However, a recreationist may have a higher inhalation rate than a 

resident. Recreational land use addresses exposure to people who spend a limited amount of 

time at or near a site while playing, fishing, hunting, hiking, or engaging in other outdoor 

activities. Environmental exposure pathways included in the recreationist scenario include 

ground external gamma, inhalation, Rn, plant consumption, meat consumption, milk 

consumption, and soil ingestion.

The estimated total dose from 1 pCi/g of Ra-226 and 0.5 pCi/g of Ra-228 above natural 

background in surface soil, to a recreationist, in the year of maximum exposure (year 1) is 

0.441 mrem/yr, which is below the 100 mrem/yr public exposure criteria based on assumed 

activity concentrations. The results of the environmental pathways for year 1, the year of 

maximum dose, are presented in Table 7-9. The actual dose received is dependent upon both the 

excess Ra radioactivity in surface soil and the time spent exposed to the soil surface.
PA DEP TENORM Study Report – Section 7.0 Rev. 0

January 2015 7-5

Table 7-1. Gamma Scan Survey Summary

Study ID

GWS 

Max 

(cpm)

GWS 

Min 

(cpm)

GWS 

Median 

(cpm)

GWS 

Mean 

(cpm)

GWS 

Std Dev 

(cpm)

No. 

Data 

Points

NaI 

BKG

(cpm)

T-Test 

Results 

(Sample to 

BKG)

BR-04-SL-011 16,512 7,892 13,022 12,655 1,588 2,906 12,511 Accept

BR-04-SL-010 Part of same road as BR-04-SL-011 

BR-05-SL-009 16,067 10,936 13,431 13,411 732 1,387 12,511 Accept

BR-06-SL-004 15,757 9,875 13,430 13,363 799 1,452 12,511 Accept

BR-07-SL-008 15,641 7,975 12,843 12,511 1,449 2,389 NA NA

BR-01-SL-001 17,778 4,106 11,456 11,759 1,564 11,536 11,135 Accept

BR-02-SL-002 13,268 9,766 11,050 11,135 615 850 NA NA

BR-08-SL-003 14,234 9,771 11,988 11,990 693 5,590 11,960 Reject

BR-09 13,565 10,313 11,998 11,960 736 222 NA NA

BR-10-SL-012 15,179 5,888 11,977 11,968 996 9,253 10,898 Accept

BR-11 12,762 9,449 10,882 10,898 591 596 NA NA

BR-13-SL-006 13,180 9,526 11,311 11,273 646 961 NA NA

BR-12-SL-005 12,050 6,114 9,121 9,136 895 4,644 11,273 Accept

BR-15-SL-014 14,509 7,695 10,816 10,873 1,128 1,359 NA NA

BR-14-SL-013 14,053 2,032 10,861 10,759 1,053 5,395 10,873 Reject

BR-16-SL-015 12,360 9,470 10,587 10,614 461 592 NA NA

BR-17-SL-016 13,870 9,100 11,586 11,555 761 4,388 10,614 Accept

BR-18-SL-017 9,949 6,066 7,479 7,524 616 727 NA NA

BR-19-SL-018 16,990 6,821 9,395 9,510 921 5,231 7,524 Accept

BR-20-SL-019 13,511 5,404 8,747 8,825 1,317 3,944 NA NA

BR-21-SL-020 12,463 6,232 8,560 8,611 899 877 8,825 Accept

BR-22-SL-021 13,126 5,947 9,019 9,317 1,646 704 NA NA

BR-23-SL-022 13,740 5,491 9,335 9,376 1,352 3,605 9,317 Reject

BR-24-SL-023 13,217 5,349 8,498 8,590 1,182 3,375 9,317 Reject

BR-25-SL-024 13,248 5,069 7,436 7,781 1,487 1,984 8,226 Reject

BR-26-SL-025 11,208 5,882 8,254 8,226 893 343 NA NA

BR-27-SL-026 11,333 5,708 8,281 8,267 955 579 NA NA

BR-28-SL-027 12,475 4,597 7,678 7,785 1,234 3,376 8,267 Reject

BR-29-SL-028 14,465 5,309 9,041 9,490 1,924 2,556 7,925 Accept

BR-30-SL-029 10,360 5,687 7,965 7,925 703 759 NA NA

BR-31-SL-030 14,415 6,200 9,744 9,801 1,172 7,245 10,093 Reject

BR-32-SL-031 14,117 6,527 10,057 10,093 1,118 1,958 NA NA

BR-33-SL-032 10,975 6,030 8,442 8,406 658 2,603 10,093 Reject

BR-34-SL-033 11,448 5,340 8,276 8,211 790 3,347 10,093 Reject

BR-35-SL-034 12,056 5,972 9,036 9,076 925 2,186 10,093 Reject
PA DEP TENORM Study Report – Section 7.0 Rev. 0

January 2015 7-6

Table 7-1. Gamma Scan Survey Summary

Study ID

GWS 

Max 

(cpm)

GWS 

Min 

(cpm)

GWS 

Median 

(cpm)

GWS 

Mean 

(cpm)

GWS 

Std Dev 

(cpm)

No. 

Data 

Points

NaI 

BKG

(cpm)

T-Test 

Results 

(Sample to 

BKG)

BR-36-SL-035 10,981 5,693 8,566 8,502 748 975 NA NA

BR-37-SL-036 11,617 5,591 8,069 8,059 699 10,257 8,502 Reject

BR-38-SL-037 10,668 6,105 8,006 7,979 662 406 NA NA

BR-39-SL-038 10,535 6,124 7,942 7,920 649 1,124 7,979 Reject

BR-40-SL-039 11,617 5,684 7,883 7,866 653 3,712 7,979 NA

BR-41 10,227 5,868 8,001 7,974 679 510 NA NA

BR-42-SL-040 10,859 5,774 7,951 7,950 722 1,560 7,974 NA

BR-43-SL-041 12,789 5,048 7,978 7,954 1,036 3,399 7,974 NA

BR-44-SL-042 15,498 5,710 9,911 9,995 1,759 5,223 6,260 Accept

BR-45-SL-043 15,390 6,376 11,268 11,015 1,531 1,399 6,260 Accept

BR-46-SL-044 8,437 5,017 6,195 6,260 578 917 NA NA

BR-47-SL-045 10,560 5,177 7,252 7,258 822 3,434 6,260 Accept

BR-48-SL-046 12,338 5,208 7,868 7,991 1,239 3,152 6,260 Accept

BR-49-SL-047 14,314 5,523 8,906 9,124 1,418 2,928 6,260 Accept

BR-50-SL-048 12,933 6,066 9,315 9,292 1,067 2,293 6,260 Accept

Notes:

1. Each group of O&G brine-treated and associated background road(s) are shaded the same.

2. Bold – represents the background population for each shaded or unshaded group, respectively.

3. NA – indicates reference background road.

4. Accept (the Null Hypothesis) indicates there is a statistical difference in the data at the 95 percent 

confidence level. Reject (the Null Hypothesis) indicates the resulting surveys are statistically the 

same at the 95 percent confidence level.
PA DEP TENORM Study Report – Section 7.0 Rev. 0

January 2015 7-7

Table 7-2. Summary of NaI Gamma Count Rate Data Converted to Exposure Rate

Site GWS Max 

(μR/hr)

GWS Min 

(μR/hr)

GWS 

Median 

(μR/hr)

GWS 

Mean 

(μR/hr)

GWS Std.

Dev.

(μR/hr)

No. Data 

Points

BR-04-

SL-011 20.6 9.90 16.3 15.8 2.00 2,906

BR-04-

SL-010 Part of same road as BR-04-SL-011 – file statistics are same.

BR-05-

SL-009 20.1 13.7 16.8 16.8 0.90 1,387

BR-06-

SL-004 19.7 12.3 16.8 16.7 1.00 1,452

BR-07-

SL-008 19.6 10.0 16.1 15.6 1.80 2,389

BR-01-

SL-001 22.2 5.10 14.3 14.7 2.00 11,536

BR-02-

SL-002 16.6 12.2 13.8 13.9 0.800 850

BR-08-

SL-003 17.8 12.2 15.0 15.0 0.900 5,590

BR-09 17.0 12.9 15.0 15.0 0.90 222

BR-10-

SL-012 19.0 7.40 15.0 15.0 1.20 9,253

BR-11 16.0 11.8 13.6 13.6 0.70 596

BR-13-

SL-006 16.5 11.9 14.1 14.1 0.80 961

BR-12-

SL-005 15.1 7.60 11.4 11.4 1.10 4,644

BR-15-

SL-014 18.1 9.60 13.5 13.6 1.40 1,359

BR-14-

SL-013 17.6 2.50 13.6 13.4 1.30 5,395

BR-16-

SL-015 15.5 11.8 13.2 13.3 0.600 592

BR-17-

SL-016 17.3 11.4 14.5 14.4 1.00 4,388

BR-18-

SL-017 12.4 7.60 9.30 9.40 0.800 727

BR-19-

SL-018 21.2 8.50 11.7 11.9 1.20 5,231

BR-20-

SL-019 16.9 6.80 10.9 11.0 1.60 3,944

BR-21-

SL-020 15.6 7.80 10.7 10.8 1.10 877

BR-22-

SL-021 16.4 7.40 11.3 11.6 2.10 704
PA DEP TENORM Study Report – Section 7.0 Rev. 0

January 2015 7-8

Table 7-2. Summary of NaI Gamma Count Rate Data Converted to Exposure Rate

Site GWS Max 

(μR/hr)

GWS Min 

(μR/hr)

GWS 

Median 

(μR/hr)

GWS 

Mean 

(μR/hr)

GWS Std.

Dev.

(μR/hr)

No. Data 

Points

BR-23-

SL-022 17.2 6.90 11.7 11.7 1.70 3,605

BR-24-

SL-023 16.5 6.70 10.6 10.7 1.50 3,375

BR-25-

SL-024 16.6 6.30 9.30 9.70 1.90 1,984

BR-26-

SL-025 14.0 7.40 10.3 10.3 1.10 343

BR-27-

SL-026 14.2 7.10 10.4 10.3 1.20 579

BR-28-

SL-027 15.6 5.70 9.60 9.70 1.50 3,376

BR-29-

SL-028 18.1 6.60 11.3 11.9 2.40 2,556

BR-30-

SL-029 13.0 7.10 10.0 9.9 0.90 759

BR-31-

SL-030 18.0 7.80 12.2 12.3 1.50 7,245

BR-32-

SL-031 17.6 8.20 12.6 12.6 1.40 1,958

BR-33-

SL-032 13.7 7.50 10.6 10.5 0.800 2,603

BR-34-

SL-033 14.3 6.70 10.3 10.3 1.00 3,347

BR-35-

SL-034 15.1 7.50 11.3 11.3 1.20 2,186

BR-36-

SL-035 13.7 7.10 10.7 10.6 0.900 975

BR-37-

SL-036 14.5 7.00 10.1 10.1 0.900 10,257

BR-38-

SL-037 13.3 7.60 10.0 10.0 0.800 406

BR-39-

SL-038 13.2 7.70 9.90 9.90 0.800 1,124

BR-40-

SL-039 14.5 7.10 9.90 9.80 0.800 3,712

BR-41 12.8 7.30 10.0 10.0 0.800 510

BR-42-

SL-040 13.6 7.20 9.90 9.90 0.900 1,560

BR-43-

SL-041 16 6.30 10.0 9.90 1.30 3,399
PA DEP TENORM Study Report – Section 7.0 Rev. 0

January 2015 7-9

Table 7-2. Summary of NaI Gamma Count Rate Data Converted to Exposure Rate

Site GWS Max 

(μR/hr)

GWS Min 

(μR/hr)

GWS 

Median 

(μR/hr)

GWS 

Mean 

(μR/hr)

GWS Std.

Dev.

(μR/hr)

No. Data 

Points

BR-44-

SL-042 19.4 7.14 12.4 12.5 2.20 5,223

BR-45-

SL-043 19.2 7.97 14.1 13.8 1.91 1,399

BR-46-

SL-044 10.5 6.27 7.74 7.82 0.722 917

BR-47-

SL-045 13.2 6.47 9.06 9.07 1.03 3,434

BR-48-

SL-046 15.4 6.51 9.84 9.99 1.55 3,152

BR-49-

SL-047 17.9 6.90 11.1 11.4 1.77 2,928

BR-50-

SL-048 16.2 7.58 11.6 11.6 1.33 2,293
PA DEP TENORM Study Report – Section 7.0 Rev. 0

January 2015 7-10

Table 7-3. Road-Biased Soil – Uranium Series Gamma Spectroscopy Results

Sample ID U-238 

(pCi/g)

Ra-226 

(pCi/g)

Pb-214 

(pCi/g)

Bi-214 

(pCi/g)

BR-01-SL-001 0.905 2.57 1.36 1.30

BR-04-SL-010 1.08 2.03 0.959 0.872

BR-04-SL-011 < 2.75 1.51 0.991 0.985

BR-05-SL-009 0.792 2.12 1.03 0.932

BR-06-SL-004 < 1.54 2.05 0.891 0.858

BR-12-SL-005 < 1.96 1.81 1.02 1.03

BR-14-SL-013 < 1.45 2.98 1.90 1.82

BR-15-SL-014 1.63 2.55 1.31 1.22

BR-17-SL-016 < 0.901 2.22 1.17 1.07

BR-19-SL-018 < 1.19 1.44 0.598 0.587

BR-21-SL-020 1.27 4.57 2.86 2.69

BR-23-SL-022 1.81 4.38 2.32 2.18

BR-24-SL-023 < 1.03 4.22 2.85 2.67

BR-25-SL-024 1.19 6.96 4.89 4.48

BR-28-SL-027 1.50 3.07 2.02 1.74

BR-29-SL-028 1.52 2.50 1.20 1.15

BR-31-SL-030 < 0.599 1.93 0.840 0.822

BR-33-SL-032 0.624 1.53 0.820 0.751

BR-34-SL-033 0.605 1.22 0.648 0.564

BR-35-SL-034 0.949 1.65 0.867 0.811

BR-37-SL-036 0.790 1.75 0.842 0.771

BR-39-SL-038 < 0.912 1.14 0.638 0.625

BR-40-SL-039 0.930 < 0.057 0.458 0.507

BR-42-SL-040 0.562 1.35 0.626 0.561

BR-43-SL-041 < 0.563 1.18 0.635 0.613

BR-44-SL-042 0.931 1.95 0.909 0.830

BR-45-SL-043 < 0.72 < 0.070 0.590 0.763

BR-47-SL-045 1.39 0.970 0.481 0.443

BR-48-SL-046 < 1.02 1.45 0.716 0.725

BR-49-SL-047 0.696 1.30 0.595 0.547

BR-50-SL-048 0.865 1.99 1.02 0.949

Average 0.882 2.14 1.23 1.16

Std. Dev. 0.410 1.38 0.932 0.852

Median 0.792 1.93 0.909 0.858

Minimum 0.282 0.029 0.458 0.443

Maximum 1.81 6.96 4.89 4.48

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 7.0 Rev. 0

January 2015 7-11

Table 7-4. Road-Biased Soil  Thorium Series Gamma Spectroscopy Results

Sample ID Th-232 

(pCi/g)

Ra-228 

(pCi/g)

Ac-228 

(pCi/g)

Pb-212 

(pCi/g)

Bi-212 

(pCi/g)

BR-01-SL-001 1.08 1.09 1.13 1.40 0.626

BR-04-SL-010 1.31 1.33 1.37 1.62 0.809

BR-04-SL-011 1.49 1.51 1.56 1.56 0.912

BR-05-SL-009 1.43 1.43 1.50 1.73 0.857

BR-06-SL-004 1.16 1.18 1.22 1.22 0.720

BR-12-SL-005 1.14 1.16 1.19 0.987 0.605

BR-14-SL-013 1.15 1.17 1.21 1.57 0.708

BR-15-SL-014 1.16 1.18 1.22 1.51 0.651

BR-17-SL-016 1.29 1.45 1.35 1.59 0.763

BR-19-SL-018 0.746 0.760 0.781 0.926 0.565

BR-21-SL-020 0.882 0.901 0.923 1.16 0.463

BR-23-SL-022 1.26 1.29 1.32 1.60 0.737

BR-24-SL-023 1.48 1.51 1.55 1.79 0.748

BR-25-SL-024 1.81 1.85 1.89 2.07 0.760

BR-28-SL-027 0.711 0.727 0.744 0.675 0.426

BR-29-SL-028 1.04 1.06 1.08 1.37 0.762

BR-31-SL-030 0.771 0.789 0.807 0.971 0.492

BR-33-SL-032 0.701 0.717 0.734 0.846 0.412

BR-34-SL-033 0.581 0.595 0.609 0.764 0.405

BR-35-SL-034 0.798 0.817 0.835 0.909 0.484

BR-37-SL-036 0.768 0.787 0.804 0.917 0.471

BR-39-SL-038 0.670 0.687 0.701 0.704 0.370

BR-40-SL-039 0.616 0.632 0.645 0.213 0.386

BR-42-SL-040 0.664 0.681 0.695 0.782 0.386

BR-43-SL-041 0.684 0.702 0.717 0.875 0.423

BR-44-SL-042 1.11 1.12 1.16 1.38 0.714

BR-45-SL-043 0.863 0.872 0.904 0.210 0.586

BR-47-SL-045 0.45 0.455 0.471 0.559 0.277

BR-48-SL-046 0.773 0.780 0.809 0.864 0.479

BR-49-SL-047 0.577 0.582 0.604 0.685 0.376

BR-50-SL-048 0.515 0.520 0.539 0.688 0.259

Average 0.972 0.979 1.00 1.10 0.569

Std. Dev. 0.334 0.349 0.355 0.465 0.179

Median 0.873 0.872 0.904 0.971 0.565

Minimum 0.450 0.455 0.471 0.210 0.259

Maximum 1.81 1.85 1.89 2.07 0.912
PA DEP TENORM Study Report – Section 7.0 Rev. 0

January 2015 7-12

Table 7-5. Road-Biased Soil  Actinium Series and 

Miscellaneous Gamma Spectroscopy Results

Sample ID U-235 

(pCi/g)

K-40 

(pCi/g)

BR-01-SL-001 < 0.075 10.6

BR-04-SL-010 < 0.107 21.4

BR-04-SL-011 < 0.212 29.4

BR-05-SL-009 0.117 24.8

BR-06-SL-004 < 0.152 21.7

BR-12-SL-005 < 0.157 7.01

BR-14-SL-013 < 0.183 13.2

BR-15-SL-014 < 0.150 12.5

BR-17-SL-016 < 0.083 17.6

BR-19-SL-018 < 0.114 10.9

BR-21-SL-020 < 0.127 5.61

BR-23-SL-022 < 0.110 13.0

BR-24-SL-023 < 0.103 16.9

BR-25-SL-024 < 0.093 16.3

BR-28-SL-027 0.074 11.4

BR-29-SL-028 < 0.209 20.1

BR-31-SL-030 0.094 8.84

BR-33-SL-032 < 0.045 7.35

BR-34-SL-033 < 0.051 11.3

BR-35-SL-034 0.071 7.21

BR-37-SL-036 < 0.048 8.92

BR-39-SL-038 < 0.007 6.85

BR-40-SL-039 < 0.044 7.22

BR-42-SL-040 < 0.042 7.49

BR-43-SL-041 0.100 8.39

BR-44-SL-042 < 0.055 19.1

BR-45-SL-043 < 0.051 15.0

BR-47-SL-045 < 0.035 6.10

BR-48-SL-046 < 0.071 12.3

BR-49-SL-047 0.102 7.96

BR-50-SL-048 < 0.091 5.40

Average 0.056 12.6

Std. Dev. 0.029 6.19

Median 0.052 11.3

Minimum 0.018 5.40

Maximum < 0.091 29.4

< – indicates a value less than the reported 

number which is the MDC.
PA DEP TENORM Study Report – Section 7.0 Rev. 0

January 2015 7-13

Table 7-6. Reference Background Road  Uranium Series Gamma Spectroscopy Results

Sample ID U-238 

(pCi/g)

Ra-226 

(pCi/g)

Pb-214 

(pCi/g)

Bi-214 

(pCi/g)

BR-02-SL-002 < 1.64 3.07 1.69 1.69

BR-07-SL-008 < 1.58 2.38 1.05 0.965

BR-13-SL-006 < 1.08 6.09 3.81 3.59

BR-16-SL-015 < 1.55 2.24 1.09 0.967

BR-18-SL-017 < 0.753 0.828 0.479 0.445

BR-20-SL-019 < 3.14 63.0 51.0 48.4

BR-22-SL-021 < 1.99 16.1 14.2 12.7

BR-26-SL-025 < 0.919 4.25 3.01 2.85

BR-27-SL-026 0.643 4.10 2.83 2.70

BR-30-SL-029 1.61 2.86 1.55 1.45

BR-32-SL-031 < 0.854 1.69 1.11 0.940

BR-36-SL-035 0.825 1.41 0.640 0.609

BR-38-SL-037 12.7 1.55 0.784 0.711

BR-46-SL-044 8.04 1.13 0.523 0.468

Average 2.184 7.91 5.98 5.61

Std. Dev. 3.606 16.3 13.4 12.7

Median 0.805 2.62 1.33 1.21

Minimum 0.377 0.828 0.479 0.445

Maximum 12.7 63.0 51.0 48.4

< – indicates a value less than the reported number which is the MDC.
PA DEP TENORM Study Report – Section 7.0 Rev. 0

January 2015 7-14

Table 7-7. Reference Background Road  Thorium Series Gamma Spectroscopy Results

Sample ID Th-232 

(pCi/g)

Ra-228 

(pCi/g)

Ac-228 

(pCi/g)

Pb-212 

(pCi/g)

Bi-212 

(pCi/g)

BR-02-SL-002 1.38 1.41 1.45 1.70 0.826

BR-07-SL-008 1.28 1.30 1.34 1.66 0.874

BR-13-SL-006 3.26 3.32 3.43 2.03 0.885

BR-16-SL-015 1.28 1.30 1.34 1.58 0.778

BR-18-SL-017 0.392 0.399 0.410 0.509 0.244

BR-20-SL-019 11.0 11.2 11.5 10.5 1.53

BR-22-SL-021 2.93 2.99 3.06 3.47 0.765

BR-26-SL-025 1.05 1.08 1.10 1.12 0.414

BR-27-SL-026 0.838 0.857 0.877 0.982 0.331

BR-30-SL-029 0.543 0.556 0.568 0.778 0.307

BR-32-SL-031 0.709 0.725 0.742 1.07 0.433

BR-36-SL-035 0.637 0.653 0.667 0.788 0.376

BR-38-SL-037 0.752 0.772 0.788 0.890 0.441

BR-46-SL-044 0.392 0.396 0.410 0.513 0.249

Average 1.889 1.93 1.98 1.97 0.604

Std. Dev. 2.764 2.81 2.89 2.57 0.359

Median 0.944 0.969 0.989 1.10 0.437

Minimum 0.752 0.396 0.410 0.509 0.244

Maximum 11.0 11.2 11.5 10.5 1.53
PA DEP TENORM Study Report – Section 7.0 Rev. 0

January 2015 7-15

Table 7-8. Reference Background Road  Actinium Series and 

Miscellaneous Gamma Spectroscopy Results

Sample ID U-235 

(pCi/g)

K-40 

(pCi/g)

BR-02-SL-002 < 0.223 13.6

BR-07-SL-008 < 0.149 23.1

BR-13-SL-006 < 0.165 18.1

BR-16-SL-015 < 0.161 12.0

BR-18-SL-017 < 0.131 6.14

BR-20-SL-019 < 0.322 9.32

BR-22-SL-021 < 0.197 20.7

BR-26-SL-025 < 0.085 6.07

BR-27-SL-026 < 0.069 4.87

BR-30-SL-029 < 0.058 6.68

BR-32-SL-031 < 0.050 13.0

BR-36-SL-035 < 0.050 7.18

BR-38-SL-037 < 0.044 8.73

BR-46-SL-044 0.077 4.44

Average 0.066 11.0

Std. Dev. 0.040 6.03

Median 0.071 9.03

Minimum 0.022 4.44

Maximum 0.161 23.1

< – indicates a value less than the reported number 

which is the MDC.

Table 7-9. Dose Assessment Results for Oil and Gas Brine-Treated Roads

Nuclide Ground 

(mrem)

Inhalation 

(mrem)

Radon 

(mrem)

Plant 

(mrem)

Meat 

(mrem)

Milk 

(mrem)

Soil 

(mrem)

Ra-226 5.458E-02 1.253E-05 1.221E-05 0.000E+00 8.301E-02 0.000E+00 3.089E-04

Pb-210 3.402E-05 3.213E-05 0.000E+00 0.000E+00 2.201E-01 0.000E+00 1.552E-03

Ra-228 1.772E-02 4.096E-05 6.173E-05 0.000E+00 4.118E-02 0.000E+00 1.601E-04

Th-228 2.024E-02 2.060E-04 3.381E-04 0.000E+00 1.093E-03 0.000E+00 7.426E-05

Total 9.256E-02 2.916E-04 4.120E-04 0.000E+00 3.453E-01 0.000E+00 2.095E-03
PA DEP TENORM Study Report – Section 8.0 Rev. 0

January 2015 8-1

8.0 QUALITY ASSURANCE AND QUALITY CONTROL

The quality assurance (QA) and QC objectives and criteria for this study were established in the 

study-specific Quality Assurance Project Plan (QAPP) which, along with the FSP, is available on 

the DEP website.

The purpose of the QAPP is to provide procedures and metrics for evaluating and ensuring that 

all data are technically sound and legally defensible. This is accomplished by establishing 

sample collection and preservation procedures, data collection procedures, analytical 

requirements and data evaluation processes, which result in accurate, precise, representative and 

complete data.

All sampling and analyses performed for this study were conducted in accordance with the 

QAPP standards.

8.1 Data Quality Levels (DQLs)

The requirements for this study were based on DQL I for field screening methods and DQL III

for Non-Contract Laboratory Program (non-CLP) laboratory methods.

8.2 Quality Control Parameters

The established QC parameters for evaluating data in this study were precision [duplicates, 

matrix spikes (MS), matrix spike duplicates (MSD)], accuracy (spiked samples, laboratory 

control samples), and completeness (percentage of valid data).

Precision and accuracy obtained during this study met QC parameters unless otherwise noted.

Completeness is determined by calculating the percentage of valid data. Approximately eight

percent of the gross / analyses were invalidated due to excessive concentrations of total 

dissolved solids (TDS). The TDS remaining after the water was evaporated were in excess of 

the allowable mass. Attempts to dilute the samples to allow valid analyses to be performed were 

unsuccessful.

8.3 Field Screening

Field surveys were performed by Perma-Fix personnel trained in the use of the survey 

instrumentation required. DQL I criteria were used to collect the following types of data:

 Gamma radiation exposure rate measurements

 Gross gamma radiation measurements

 Total  and  surface radioactivity

 Removable  and  surface radioactivity

 Background gamma radiation exposure rate and gross gamma radioactivity measurements 

(outside the influence of sampling areas)

 Liquid and solid samples for off-site analysis
PA DEP TENORM Study Report – Section 8.0 Rev. 0

January 2015 8-2

8.4 Sample Identification

Field samples were assigned a unique number to identify information such as the sampling 

technician, the sequential number corresponding to the sample type, and the order in which it 

was collected in accordance with the FSP.

8.5 Sample Custody

A field chain-of-custody form or sample submission form was used to record the custody of all 

samples collected. This chain-of-custody form documented the transfer of the custody from the 

sampling personnel to another person, to the laboratory, or another party, such as a courier 

delivery service.

Field samples were packaged and shipped to the laboratory on the day of collection in 

accordance with chain-of-custody protocols. All samples were transported to the laboratory by 

the quick courier service or hand delivered to the laboratory. The original chain-of-custody form 

was sent with the samples. The remaining copy was stored in the field team files.

Further details pertaining to chain-of-custody may be found in the FSP.

8.6 Analytical Procedures

Analytical methods and procedures were established before the study began based on 

preliminary assumptions and are listed in Table 8-1. Additional analytical methods were 

subsequently added and/or modified when preliminary assumptions were found to be different 

due to the amount of TDS in the samples. Additional analytical method selection was based on 

the following:

 Original specified methodologies for radiochemistry failed due to elevated dissolved solids 

and Barium (Ba) concentrations.

 Alternate EPA methods, which were used as necessary.

All procedures for environmental sample handling, storage, and documentation while in the 

laboratory’s custody and deliverable requirements upon delivery of the data to the user are 

documented in the laboratory’s quality assurance manual (QAM).

8.7 Instrument Calibrations

All field and laboratory equipment were calibrated to NIST traceable standards before use to 

ensure proper operating accuracy. Laboratory instrument calibration procedures are presented in 

the laboratory QAMs. Field calibrations were performed in accordance with specified

procedures. Prior to the use of field equipment, daily operational QC checks were completed.

All daily QC instrumentation checks are presented in Appendix B.

8.8 Data Evaluation and Validation

The following subsections describe the field and laboratory data validation processes used for the 

study.
PA DEP TENORM Study Report – Section 8.0 Rev. 0

January 2015 8-3

8.8.1 Validation of Field Data

During the field operations, field measurements were validated at the time of collection by the 

field sampler through the use of standard operating procedures (SOPs) and field QC checks.

Field-obtained data, as well as ongoing QA/QC checks of environmental samples collected, were 

validated by trained Perma-Fix and DEP field technicians. All field data were reviewed at the 

time of sample collection.

8.8.2 Validation of Laboratory Data

Prior to reporting laboratory data, the analyst validated the sample results based on the QC 

criteria specified in the analytical methods. The data validation process included verification of 

the following steps:

 Ensure the standard regression coefficient is within the acceptable range.

 Ensure standard reference materials were analyzed at the proper frequencies and acceptable 

results were obtained.

 Ensure the reagent blanks were analyzed at the proper frequency.

 Ensure precision requirements of the plan were met.

 Ensure accuracy requirements of the plan were met.

 Ensure completeness requirements of the plan were met.

 Ensure samples were analyzed within the proper sample holding times.

 Verify all calculations were correct.

 Ensure proper units were reported.

 Ensure the proper methodologies were used.

In addition to the review of analytical results and project-specific precision, accuracy, and 

completeness requirements, the laboratory department manager or senior chemist performed

internal audits of report forms and other data sheets as well as regular reviews of instrument logs, 

performance test results, and analysts’ performance. Where review of analytical results or 

internal QA/QC checks indicated discrepancies, immediate corrective actions were taken and all 

data results collected since the previous approved QC audits were reviewed for validity. Specific 

laboratory procedures for validation of the analytical data generated are described in the 

laboratory QAMs.

8.9 Data Reporting  Analytical Laboratory

After the data were validated internally by the laboratory, the results were entered into the 

laboratory’s data management system. The laboratory data management system contains the 

final data results. When data entries were completed, the laboratory director (or his/her 

designee) issued a final data report. The director then issued the final data report to the data user.

The data reports prepared for this project contain all pertinent information for the data user in 

determining the applicability and validity of the data. A specified and uniform data reporting 

format was implemented to facilitate this effort. For this project, DQL III data packages were

reported as a DQL IV (CLP-like) deliverable to facilitate data validation and are presented in 
PA DEP TENORM Study Report – Section 8.0 Rev. 0

January 2015 8-4

Appendix K. The following criteria and information were supplied, as a minimum, for data 

reports generated for this project:

 A descriptive case narrative describing the internal data validation.

 Completed and legible chains-of-custody for all analyses contained within each submitted 

data package.

 A laboratory sample record documenting which analyses were performed for the samples 

contained in the data package is presented in Table 8-1.

 All of the laboratory sample identifications and the correlating field sample identifications.

 All applicable analytical results, counting errors, and MDCs reported in the correct number 

of significant figures and reporting units.

 Included in the individual sample reporting results are the complete sample identifications, 

the sample dilutions (if necessary), and the individual sample analysis dates.

8.9.1 DQL III Reporting

The following summary forms and raw data deliverable requirements apply for DQL III.

The following forms are required for all analyses using gamma spectroscopy; isotopic U and Th; 

and gross , gross  and Ra methods, and were provided by the DEP Laboratory in various 

forms:

 Narrative and sample identification cross reference

 Copies of chain-of-custody documentation

 Laboratory chronicle

 Method summaries and references

 MS/MSD summary or any laboratory duplicate

 Method blank summary and results

 Instrument performance check summary

 Initial calibration summary for all constituents of interest

8.10 Quality Control Procedures

QC procedures and checks ensure the accuracy of the data.

For any laboratory QC result that was outside of the acceptance criteria, the samples were 

reanalyzed and/or the results were qualified in the final report.

8.10.1 Field QC Checks

Duplicate samples were collected and analyzed to assess the quality of field sampling techniques.

These samples were treated as separate and discrete samples and analyzed by the selected offsite

laboratory. The results are provided in Section 8.16.
PA DEP TENORM Study Report – Section 8.0 Rev. 0

January 2015 8-5

8.10.2 Internal Laboratory QC Checks

The laboratory followed the internal QC checks specified in the QAPP for each analysis type 

employed. In addition, these QC checks have met the requirements specified in the respective 

EPA analytical methods.

8.10.2.1 Initial and Continuing Calibration

Each instrument and measurement system was calibrated prior to use to verify the instrument 

met performance criteria throughout the course of the analytical cycle. Continuing calibration

checks were performed at a minimum frequency in accordance with the DEP Laboratory QAM.

For instruments used for radiological analysis, performance checks are conducted each day

samples are analyzed. For instruments used for non-radiological analysis, performance checks 

are conducted for each batch of 20 samples or less.

8.10.2.2 Reagent Blanks

A reagent blank was analyzed with each set of samples received for analysis. No responses 

above the reportable detection limit were observed in any of the blanks, indicating no possible 

laboratory contamination. The exact frequency and method of use is presented in the laboratory 

QAM.

8.10.2.3 Matrix Spike and Duplicate (Matrix Spike Duplicate) Analysis

One in 20 samples were analyzed as MSs and MSDs or one per day, whichever was greater.

MS/MSD QC is not required for gamma spectroscopy analysis because no sample preparation is 

involved. The MS/MSD QC measures the effects of the sample matrix on method performance.

The percent recovery for spiked samples was calculated using the equations documented in 

Section 11.0 of the QAPP and compared to the accuracy criteria specified in the QAM for the 

associated analytical method. The relative percent difference (RPD) of replicate spikes or 

replicate analytical results was calculated using the equations documented in Section 11.0 of the

QAPP and compared to the precision criteria for the associated analytical method.

8.10.2.4 Calibration Standards

Calibration standards were analyzed as required in the reference methods throughout the course 

of the analysis. The exact frequencies and methods of use are presented in the laboratory QAM.

8.11 Laboratory Performance Audits

Laboratory performance audits are conducted by the DEP Laboratory QA officer three times per 

year. Each laboratory analyst is provided a performance evaluation or proficiency test sample 

containing analytes for the parameters which he/she usually performs. These proficiency test

sample results are used to identify issues in sample preparation, analysis techniques, or 

methodologies. Any issues are identified, investigated, documented on the proper form, resolved 

with a corrective action plan to eliminate the issues and prevent reoccurrence, and then shared 

with the accreditation bodies.
PA DEP TENORM Study Report – Section 8.0 Rev. 0

January 2015 8-6

The DEP Laboratory internal audits include verification of each analyst’s record keeping, proper 

use and understanding of procedures, and performance documentation. Deficiencies/findings are 

discussed with the analyst, documented, and resolved through the implementation of a corrective 

action.

8.12 Laboratory System Audits

Laboratory system audits are conducted by an external third-party assessor once every two years.

These audits are used to ensure that all aspects of the DEP Laboratory’s QAM are operative and 

within compliance. This involves a thorough review of all laboratory methods performed and 

documentation to confirm that all analytical procedures are performed according to the DEP 

Laboratory’s QAM. An external third-party assessment was not conducted during the time

period that samples from the TENORM study were received, processed, analyzed, and reported.

8.13 Assessment Procedures for Data Acceptability

The following subsections describe the data validation procedures that were used to evaluate the 

precision, accuracy, and completeness of the data generated.

8.13.1 Precision

Precision is the evaluation of agreement among individual measurements of the same property 

under prescribed similar conditions. Precision is assessed by calculating the RPD of replicate 

spike samples or replicate sample analyses according to the following equation:

Relative Percent Difference: RPD =

R1−R2

(R1+R2)⁄2

× 100

Where: R1 = result 1

R2 = result 2

8.13.2 Accuracy

Accuracy is the evaluation of closeness of an individual measurement to the true value.

Accuracy is measured by calculating the percent recovery (%R) of known levels of spike 

compounds as follows:

Percent Recovery:

%R =

[spike sample] − [unspiked sample]

[spike added]

× 100

8.13.3 Completeness

Completeness is the quantification of the amount of valid data obtained from a measurement 

system, expressed as a percentage of the number of valid measurements that could have been 

accomplished. More than one completeness check can be evaluated. It is calculated as follows:
PA DEP TENORM Study Report – Section 8.0 Rev. 0

January 2015 8-7

Completeness (%) =

number of valid samples reported

total number of samples analyzed × 100

8.13.4 Quality Control Charts

Valid QC charts can be prepared after the initial 20 analytical determinations to graphically 

evaluate precision and accuracy criteria. The charts are prepared by calculating the mean value 

of the determinations and setting control limits at + 3 standard deviations from that mean. The 

following equations are used:

Mean:

X̅ =

1

N

∑xi

N

i=1

Where: N = number of samples

Xi = sample value

Standard Deviation:

σ = √

∑ (xi − X̅)

N 2

i=1

N − 1

The control limits must be within acceptance limits or ranges presented in the DEP Laboratory’s 

SOPs. If the values are found to be outside these limits or ranges, the measurement system is 

examined to determine if possible problems exist. Most of the values were found inside the 

limits; however, those values which exceeded the control limits were reported with an 

appropriate data qualifier.

8.14 Preventative Maintenance

Performance of preventative maintenance was completed on equipment to ensure operability. 

Instrument manuals are kept on file and used for reference whenever equipment required repair

or maintenance.

8.14.1 Field Equipment

Field sampling personnel were responsible for preventative maintenance of all field instruments.

The field sampling personnel ensured field instrumentation was protected from extreme weather 

conditions as well as physical hazards.

8.14.2 Laboratory Instruments

Preventative maintenance schedules and/or procedures for laboratory equipment are presented in 

the DEP Laboratory QAM. No major preventative maintenance was performed on the DEP 

Laboratory equipment during the time period that samples from the TENORM study were 

received, processed, analyzed and reported.
PA DEP TENORM Study Report – Section 8.0 Rev. 0

January 2015 8-8

8.15 QA Reports to Management

Audit reports have been provided by the DEP Laboratory director (or his/her designee) as a 

means of tracking program performance. An annual method internal audit was performed 

covering the period of January 1, 2013, to present. In addition, the state of New Jersey

Department of Environmental Protection (NJDEP) performed an audit of the DEP Laboratory

management system, QA program, and analytical testing procedures performed by the DEP 

Laboratory. The NJDEP submitted a February 11, 2013, report to the DEP Laboratory that 

concluded no findings for the Radiation Measurement Section.

Field QA reports were not necessary due to the size and length of individual sample collection 

activities. Any problems noted during sampling were immediately communicated to the project 

certified health physicist.

8.16 Third-Party Quality Control

QC samples were collected as follows:

 Solid Samples – five percent (field replicate/split) QC samples, i.e., one every 20 samples 

collected to verify results of onsite laboratory per total samples in a calendar year.

 Aqueous Samples – five percent (field replicate/split) QC samples, i.e., one every 20 samples 

collected to verify results of onsite laboratory per total samples in a calendar year.

The samples were sent offsite to an independent, third-party, accredited laboratory for gamma 

spectroscopy analysis and compared to the DEP Laboratory gamma spectroscopy analysis of the 

split sample using NRC Inspection Manual Procedure 84750:

 Divide each offsite laboratory result by its associated uncertainty to obtain the resolution. 

For purposes of this procedure, the uncertainty is defined as the relative standard deviation, 

one sigma, of the offsite laboratory results as calculated from counting statistics, i.e., the 95 

percent confidence level reported error divided by 1.96.

 Divide each DEP Laboratory result by the corresponding offsite laboratory result to obtain 

the ratio (DEP Laboratory/offsite laboratory).

 The DEP Laboratory’s measurement is in agreement if the value of the ratio falls within the 

limits shown in the following table for the corresponding resolution:

Criteria for Accepting the DEP Laboratory’s Measurements

Resolution Ratio

<4 Statistics are too poor for comparison

4-7 0.5-2.0

8-15 0.6-1.66

16-50 0.75-1.33

Resolution Ratio

51-200 0.80-1.25

>200 0.85-1.18
PA DEP TENORM Study Report – Section 8.0 Rev. 0

January 2015 8-9

The results of the comparison for solid samples are presented in Tables 8-2 through 8-5 for four 

of the radionuclides identified using gamma spectroscopy. If either the DEP Laboratory or the 

third-party laboratory (GEL) result was < MDC value reported, the comparison was not made.

There were 28 comparisons of split solid samples made; 14 passed and 14 failed. The pass/fail 

rate of 50 percent is likely due to the difficulty with splitting solid samples in regards to the total 

radioactivity concentration. The performance has been determined to be acceptable based on the 

following criteria: split sampling of solid samples, especially at low-activity concentrations, 

rarely results in equal activity for both resulting samples. Radioactive particulate contamination 

within solids is usually not homogenous, making split sampling improbable to split activity 

evenly between the two aliquots.

 Mixing or blending of the solid sample prior to splitting into equal aliquots does not ensure 

the radioactivity is evenly divided.

 Duplicate analysis of the same solid sample is more appropriate as a third-party QC

comparison, eliminating the large variability of split samples, but was not possible for this 

study.

 Liquid samples are much easier to mix prior to splitting and are a more appropriate measure 

of the agreement between the two laboratories.

The results of the comparison for liquid samples are presented in Tables 8-6 through 8-9 for four

of the radionuclides identified using gamma spectroscopy. If either the DEP Laboratory or the 

independent laboratory (GEL) result was < MDC value reported, the comparison was not made.

Of the 33 comparisons made on split liquid sample gamma spectroscopy analysis results, 28 met 

acceptance criteria. The agreement between the DEP Laboratory and the independent laboratory 

(GEL) gamma spectroscopy results is acceptable.

The following actions and/or conclusions were made based on the split solid sample analytical 

results:

1. Split sampling of radioactive solid samples does not result in equal radioactivity in the two 

resulting samples. Solid samples were mixed in the field prior to filling two sample 

containers (splitting the sample). Low-activity solid sample media does not readily split into 

equal radioactivity concentration.

2. All of the split solid samples failing the comparison acceptance criteria were reviewed by 

asking the question: “Would the result of one of the two splits result in a different 

conclusion?” For example, would the result of one split pass a compliance test that may be 

applicable to the media and the result of the other split fail? Only one sample, with results of 

363 versus 6.02 pCi/g, would result in a different action based on the result.

3. Duplicate analysis of the same sample (no splitting) is a much better comparison of 

laboratory performance and is recommended for any future sample and analysis study.
PA DEP TENORM Study Report – Section 8.0 Rev. 0

January 2015 8-10

Table 8-1. Summary of Analytical Procedures

Sample Type

Media/

Sample 

Type

Analytical Parameters Analytical(a)

Methods Frequency(b)

Cuttings as produced on a 

drilling rig including cuttings 

stored temporarily on site in 

lined pits or containers

Solid phase from flowback and 

produced water

Solids accumulated in vessels 

or on equipment

Scale from drilling rigs and 

associated equipment

Soil/salt samples from 

beneficial reuse areas

(Off-site Lab)

Soil/soillikeGamma spectroscopy to 

identify TENORM 

radionuclides

Alpha spectroscopy to 

identify isotopic U

(233/234, 235, and 238) 

and isotopic Th (228, 

230, and 232) 

USEPA 901.1 

Health and Safety 

Laboratory

(HASL) 300

Once per site

WWTP sludge

WWTP discharge sediments

(Off-site Lab)

Soil/soillikeGamma spectroscopy to 

identify TENORM 

radionuclides

Alpha spectroscopy to 

identify isotopic U

(U-233/234, 235, and 

238) and isotopic Th

(Th-228, 230, and 232)

USEPA 901.1

HASL 300

Three times per 

facility

Flowback and produced waters

Accumulated liquids from 

production equipment

(Off-site Lab)

Aqueous 

(Grab)

Gross  and 

Gamma spectroscopy to 

identify TENORM 

radionuclides

USEPA 900.0

USEPA 901.1 

Once per site

Influent Marcellus Shale 

industry water (as is and 

filtered)

WWTP effluent discharge 

water (as is and filtered)

(Off-site Lab)

Aqueous 

(Grab)

Gross  and 

Gamma spectroscopy to 

identify TENORM 

radionuclides

USEPA 900.0

USEPA 901.1 

Quarterly x3

Landfill Leachate Aqueous 

(Grab)

Gross  and 

Gamma spectroscopy 

analysis

Radium (Ra-226 and 

Ra-228)

USEPA 900.0

USEPA 901.1 

EPA 903.1 and

EPA 904.0 

equivalent

Once per landfill
PA DEP TENORM Study Report – Section 8.0 Rev. 0

January 2015 8-11

Table 8-1. Summary of Analytical Procedures

Sample Type

Media/

Sample 

Type

Analytical Parameters Analytical(a)

Methods Frequency(b)

Gas sampling as necessary

(Off-site Lab)

Ambient Radon

Gaseous 

(Grab)

Charcoal 

canister

Radon

Radon

As determined by 

DEP

(a) Analytical methods are as follows:

 Up to 10 percent of the samples, based on the gross  and  and gamma spectroscopy results, are also 

analyzed by  spectroscopy for U (U-238, U-235, and U-234), Th-232, Ra (Ra-226 and Ra-228), and for 

any unsupported decay chain radionuclides.

 Analytical method as specified or an equivalent method where appropriate.

(b) QC samples were collected as follows:

 Solid Samples – five percent (field replicate/split) QC samples, i.e., one every 20 samples collected to 

verify results of onsite laboratory per total samples in a calendar year.

 Aqueous Samples – five percent (field replicate/split) QC samples, i.e., one every 20 samples collected to 

verify results of on-site laboratory per total samples in a calendar year.

Table 8-2. Bi-214 Split Solid Sample Comparison Results

Sample ID Bi-214 Result 

(pCi/g)

Bi-214 Err 

(pCi/g)

Bi-214 MDC 

(pCi/g)

Bi-214 

Resolution / 

Ratio

Bi-214 

Criteria / 

Pass-Fail

5942116 0.001 0.000 0.016 7

5942116GEL 0.556 0.158 0.12 0.002

5942130 26.5 4.160 0.217 5 0.5-2.0

5942130GEL 12.1 4.77 0.857 2.190 Fail

5942134 0.638 0.106 0.057 5 0.5-2.0

5942134GEL 4.19 1.58 0.461 0.152 Fail

5942145 0.000 0.269 1.050 12 0.6-1.66

5942145GEL 1.14 0.185 0.109 0.000 Fail

5942155 3.77 0.317 0.056 21 0.75-1.33

5942155GEL 2.63 0.25 0.0787 1.433 Fail

5942180 0.780 0.073 0.048 14 0.6-1.66

5942180GEL 0.969 0.133 0.0741 0.805 Pass

5942189 370 25.300 1.108 377 0.85-1.18

5942189GEL 589 3.06 0.973 0.628 Fail

5942188 24.0 1.970 0.156 58 0.80-1.25

5942188GEL 21.6 0.726 0.241 1.111 Pass
PA DEP TENORM Study Report – Section 8.0 Rev. 0

January 2015 8-12

Table 8-3. Pb-212 Split Solid Sample Comparison Results

Sample ID Pb-212 Result 

(pCi/g)

Pb-212 Err 

(pCi/g)

Pb-212 MDC 

(pCi/g)

Pb-212

Resolution / 

Ratio

Pb-212 

Criteria / 

Pass-Fail

5942116 -0.008 0.000 0.014

5942116GEL 0.533 0.0928 0.0987

5942130 6.31 0.377 0.484 7 0.5-2.0

5942130GEL 11.4 3.02 0.545 0.554 Pass

5942134 1.19 0.137 0.089 3

5942134GEL 1.54 1.05 0.318 0.773

5942145 0.909 0.129 0.062 27 0.75-1.33

5942145GEL 1.57 0.115 0.0848 0.579 Fail

5942155 1.47 0.104 0.036 23 0.75-1.33

5942155GEL 1.51 0.131 0.0657 0.974 Pass

5942180 0.832 0.072 0.059 21 0.75-1.33

5942180GEL 0.898 0.083 0.0586 0.927 Pass

5942189 154 20.700 0.998 256 0.85-1.18

5942189GEL 146 1.12 0.743 1.055 Pass

5942188 8.40 0.589 0.178 19 0.85-1.18

5942188GEL 2.29 0.238 0.179 3.668 Fail

Table 8-4. Pb-214 Split Soil Sample Comparison Results

Sample ID Pb-214 Result 

(pCi/g)

Pb-214 Err 

(pCi/g)

Pb-214 MDC 

(pCi/g)

Pb-214 

Resolution / 

Ratio

Pb-214 

Criteria / 

Pass-Fail

5942116 0.289 0.033 0.034 10 0.6-1.66

5942116GEL 0.689 0.132 0.12 0.419 Fail

5942130 26.4 1.930 0.217 8 0.6-1.66

5942130GEL 17.1 4.43 0.812 1.544 Pass

5942134 6.05 0.527 0.061 5 0.5-2.0

5942134GEL 3.89 1.39 0.418 1.555 Pass

5942145 1.21 0.213 0.066 19 0.75-1.33

5942145GEL 1.34 0.14 0.104 0.903 Pass

5942155 4.18 0.283 0.054 23 0.75-1.33

5942155GEL 3.18 0.271 0.0858 1.314 Pass

5942180 0.822 0.072 0.059 16 0.6-1.66

5942180GEL 1.25 0.155 0.0816 0.658 Pass

5942189 373 62.500 1.030 4 0.5-2.0

5942189GEL 6.02 3.13 4.47 61.960 Fail

5942188 26.3 1.730 0.152 66 0.80-1.25

5942188GEL 24.4 0.724 0.24 1.078 Pass
PA DEP TENORM Study Report – Section 8.0 Rev. 0

January 2015 8-13

Table 8-5. Ra-226 Split Soil Sample Comparison Results

Sample ID Ra-226 

Result (pCi/g)

Ra-226 Error 

(pCi/g)

Ra-226 MDC 

(pCi/g)

Ra-226

Resolution / 

Ratio

Ra-226 

Criteria / 

Pass-Fail

5942116 -0.060 0.000 0.183

5942116GEL 0.556 0.158 0.12

5942130 31.7 2.660 2.490 5 0.5-2.0

5942130GEL 12.1 4.77 0.857 2.620 Fail

5942134 7.73 0.957 0.756 5 0.5-2.0

5942134GEL 4.19 1.58 0.461 1.845 Pass

5942145 1.99 0.418 0.595 12 0.6-1.66

5942145GEL 1.14 0.185 0.109 1.746 Fail

5942155 6.14 0.609 0.650 21 0.75-1.33

5942155GEL 2.63 0.25 0.0787 2.335 Fail

5942180 1.500 0.382 0.579 14 0.6-1.66

5942180GEL 0.969 0.133 0.0741 1.548 Pass

5942189 421 38.5 8.796 377 0.85-1.18

5942189GEL 589 3.06 0.973 0.715 Fail

5942188 35.1 2.670 1.750 58 0.80-1.25

5942188GEL 21.6 0.726 0.241 1.625 Fail

Table 8-6. Bi-214 Split Liquid Sample Comparison Results

Sample ID Bi-214 Result 

(pCi/L)

Bi-214 Error 

(pCi/L)

Bi-214 MDC 

(pCi/L)

Bi-214

Resolution / 

Ratio

Bi-214 

Criteria / 

Pass-Fail

5942389 41.0 7.00 7.00 6 0.5-2.0

5942389GEL 32.8 11.50 10.60 1.250 Pass

5942390 57.0 6.00 5.00 6 0.5-2.0

5942390GEL 29.3 9.13 9.10 1.945 Pass

5942391 181 24.00 22.00 15 0.6-1.66

5942391GEL 187 24.60 20.40 0.968 Pass

5942392 229 19.00 8.00 20 0.75-1.33

5942392GEL 251 25.00 13.60 0.912 Pass

5942228 458 35.00 8.00 30 0.75-1.33

5942228GEL 669 43.50 22.40 0.685 Fail

5942275 4,660 377.00 37.00 94 0.80-1.25

5942275GEL 4,450 92.90 38.80 1.047 Pass

5942276 4,320 38.00 11.00 105 0.80-1.25

5942276GEL 4,860 90.80 34.70 0.889 Pass

5942277 2,020 245.00 14.00 75 0.80-1.25

5942277GEL 2,370 62.20 26.00 0.852 Pass

5942278 2,150 33.00 22.00 71 0.80-1.25

5942278GEL 2,230 61.20 26.00 0.964 Pass

5942291 15,300 1,340.00 44.00 195 0.80-1.25

5942291GEL 16,400 165.00 62.20 0.933 Pass
PA DEP TENORM Study Report – Section 8.0 Rev. 0

January 2015 8-14

Table 8-7. Pb-214 Split Liquid Sample Comparison Results

Sample ID Pb-214 Result 

(pCi/L)

Pb-214 Error 

(pCi/L)

Pb-214 MDC 

(pCi/L)

Pb-214

Resolution / 

Ratio

Pb-214 

Criteria / 

Pass-Fail

5942389 45.0 8.00 9.00 8 0.6-1.66

5942389GEL 52.1 13.10 10.40 0.864 Pass

5942390 64.0 5.00 5.00 3

5942390GEL 18.2 10.80 18.20 3.516

5942391 178 23.00 23.00 17 0.75-1.33

5942391GEL 201 23.10 17.90 0.886 Pass

5942392 255 18.00 8.00 4 0.5-2.0

5942392GEL 43.4 23.90 43.40 5.876 Fail

5942228 510 33.00 9.00 33 0.8-1.25

5942228GEL 790 47.20 28.10 0.646 Fail

5942275 4,710 655.00 30.00 97 0.8-1.25

5942275GEL 4,770 96.20 200.00 0.987 Pass

5942276 4,320 373.00 20.00 106 0.80-1.25

5942276GEL 5,350 99.30 46.70 0.807 Pass

5942277 2,180 243.00 16.00 81 0.80-1.25

5942277GEL 2,570 61.90 135.00 0.848 Pass

5942278 2,160 249.00 28.00 72 0.80-1.25

5942278GEL 2,500 67.80 32.70 0.864 Pass

5942291 15,300 1,340.00 56.00 205 0.85-1.18

5942291GEL 18,100 173.00 84.40 0.845 Fail

Table 8-8. Ra-226 Split Liquid Sample Comparison Results

Sample ID

Ra-226 

Result 

(pCi/L)

Ra-226 Error 

(pCi/L)

Ra-226 MDC 

(pCi/L)

Ra-226

Resolution / 

Ratio

Ra-226 

Criteria / 

Pass-Fail

5942389 104 60.00 95.00 2

5942389GEL 119 127.00 119.00 0.874

5942390 117 40.00 63.00 2

5942390GEL 135 117.00 135.00 0.867

5942391 445 190.00 300.00 3

5942391GEL 218 137.00 218.00 2.041

5942392 453 70.00 98.00 2

5942392GEL 221 190.00 221.00 2.050

5942228 2,000 158.00 118.00 7 0.5-2.0

5942228GEL 1,200 324.00 312.00 1.667 Pass

5942275 8,360 1,490.00 533.00 20 0.75-1.33

5942275GEL 5,690 559.00 564.00 1.469 Pass

5942276 7,950 835.00 257.00 24 0.75-1.33

5942276GEL 6,740 560.00 511.00 1.180 Pass

5942277 3,910 698.00 220.00 18 0.75-1.33

5942277GEL 3,120 338.00 336.00 1.253 Pass

5942278 4,300 801.00 362.00 15 0.6-1.66

5942278GEL 3,100 410.00 374.00 1.387 Pass

5942291 25,500 3,270.00 713.00 59 0.8-1.18

5942291GEL 22,000 731.00 924.00 1.159 Pass
PA DEP TENORM Study Report – Section 8.0 Rev. 0

January 2015 8-15

Table 8-9. Ra-228 Split Liquid Sample Comparison Results

Sample ID

Ra-228 

Result 

(pCi/L)

Ra-228 Error 

(pCi/L)

Ra-228 MDC 

(pCi/L)

Ra-228

Resolution / 

Ratio

Ra-228 

Criteria / 

Pass-Fail

5942389 94.0 15.00 14.00 8 0.6-1.66

5942389GEL 88.4 21.80 19.80 1.063 Pass

5942390 112 12.00 12.00 3

5942390GEL 41.4 28.70 19.40 2.705

5942391 392 46.00 32.00 17 0.75-1.33

5942391GEL 434 49.00 36.20 0.903 Pass

5942392 467 36.00 13.00 21 0.75-1.33

5942392GEL 506 47.30 26.00 0.923 Pass

5942228 442 31.00 18.00

5942228GEL 318 54.90 40.00

5942275 571 79.00 67.00 10 0.6-1.66

5942275GEL 439 86.30 81.70 1.301 Pass

5942276 523 39.00 21.00 11 0.6-1.66

5942276GEL 561 98.90 64.20 0.932 Pass

5942277 230 25.00 22.00 9 0.6-1.66

5942277GEL 262 57.20 49.20 0.878 Pass

5942278 250 30.00 42.00 9 0.6-1.66

5942278GEL 231 52.30 55.40 1.082 Pass

5942291 1,740 164.00 56.00 26 0.75-1.33

5942291GEL 1,980 151.00 124.00 0.879 Pass
PA DEP TENORM Study Report – Section 9.0 Rev. 0

January 2015 9-1

9.0 OBSERVATIONS AND RECOMMENDATIONS

Radiological sampling and surveys were conducted at well sites, WWTPs, landfills, gas 

distribution facilities and facilities that use natural gas, and O&G brine-treated roads. Various 

samples of solids, liquids, natural gas, and ambient air were collected and analyzed for 

radiological constituents and in some cases additional parameters. The data and various 

assessments are presented in Sections 3.0, 4.0, 5.0, 6.0, and 7.0. The following observations 

were made based upon the data compiled from the samples collected and surveys conducted as 

part of this study.

9.1 Observations

9.1.1 Well Sites (Section 3.0)

 There is little potential for internal radiation exposure to workers and members of the public 

from and  surface radioactivity from natural gas well site development drilling 

operations.

Ten of the 491  measurements and 69 of the 491  measurements of total surface 

radioactivity exceeded the RG 1.86 criteria. Only 1 of 493 removable surface activity 

measurements and 1 of 493  surface radioactivity measurements exceeded RG 1.86 criteria, 

indicating the total / surface radioactivity measured is fixed to the surface and not readily 

available for inhalation or ingestion. (Section 3.5.2)

 There is little potential for exceeding public dose limits from external gamma radiation 

during the drilling phase of natural gas wells.

The gamma dose rates during the drilling phase ranged from background (measured at 

5 μR/hr) to a maximum of 38.5 μR/hr, and the highest average exposure rate at any of the 

well sites was 18.1 μR/hr. (Section 3.5.1)

 There is little potential for additional Rn exposure to workers and members of the public 

during the flowback phase of unconventional natural gas wells.

The Rn in ambient air measurement results during the flowback phase are within the range of 

typical ambient background Rn concentrations (0.2 to 0.7 pCi/L in outdoor ambient air in the 

U.S.). (Section 3.5.3)

 There is little potential for radiological exposure to workers and members of the public from

the handling, hauling, and temporary storage of vertical drill cuttings on natural gas well 

sites.

Vertical drill cuttings contain U, average of 1.47 + 0.881 pCi/g, and Th, average 

1.64 + 0.403, slightly above typical background in surface soil. Both the U natural decay 

series and the Th natural decay series are identified in equilibrium. (Table 3-6)
PA DEP TENORM Study Report – Section 9.0 Rev. 0

January 2015 9-2

 There is little potential for radiological exposure to workers and members of the public from 

handling, hauling, and temporary storage of horizontal drill cuttings on natural gas well 

sites.

Horizontal drill cuttings contain U, average 8.40 + 6.70 pCi/g, and Th, average 1.42 + 0.331.

The Th is slightly above typical background in surface soil. The U activity is higher than 

typical surface soil background U activity and statistically higher than vertical drill cuttings

U activity. Both the U natural decay series and the Th natural decay series are identified in 

equilibrium. (Table 3-8)

 There is little potential for radiological exposure to workers and members of the public from 

hydraulic fracturing proppant sand.

Nominal U and Th activity was identified in hydraulic fracturing proppant sand samples. 

The U and Th activity was less than typical background for surface soil. (Section 3.2.4)

 There is little potential for radiological exposure to workers and members of the public from 

drilling mud.

Nominal U and Th activity was identified in liquid and solid drilling mud samples. The U 

and Th activity was less than typical background for surface soil. (Section 3.2.3)

 There is little potential for radiological exposure to workers and members of the public from 

handling and temporary storage of hydraulic fracturing fluid on natural gas well sites.

However, there is a potential for radiological environmental impacts from spills of hydraulic 

fracturing fluid on natural gas well sites and from spills that could occur from the 

transportation and delivery of this fluid.

Radium-226 was detected within the hydraulic fracturing fluid ranging from 64.0 –

21,000 pCi/L. Radium-228 was also detected ranging from 4.5 – 1,640 pCi/L. The hydraulic 

fracturing fluid was made up of a combination of fresh water, produced water, and reuse 

flowback fluid. (Section 3.3.2)

 There is little potential for radiological exposure to workers and members of the public from 

handling and temporary storage of flowback fluid on natural gas well sites.

However, there is a potential for radiological environmental impacts from spills of flowback 

fluid on natural gas well sites and from spills that could occur from the transportation and 

delivery of this fluid.

Radium-226 concentrations were detected within flowback fluid samples ranging from 551 –

25,500 pCi/L. Radium-228 was also detected ranging from 248 – 1,740 pCi/L.

(Section 3.3.3)

 There is little potential for radiological exposure to workers and members of the public from 

handling and temporary storage of produced water on natural gas well sites.
PA DEP TENORM Study Report – Section 9.0 Rev. 0

January 2015 9-3

However, there is a potential for radiological environmental impacts from spills of produced 

water from unconventional natural gas well sites and from spills that could occur from the 

transportation and delivery of this fluid.

Radium-226 concentrations were detected in produced water samples ranging from 40.5 –

26,600 pCi/L. Radium-228 concentrations were also detected ranging from 26.0 –

1,900 pCi/L. The Ra-226 activity in unconventional well site produced water is 

approximately 20 times greater than that observed in conventional well site produced water. 

The ratio of Ra-226 to Ra-228 in unconventional well site produced water is approximately 

eight times greater than that found in conventional well site produced water. (Sections 3.3.4 

and 3.6.3)

 There were no statistically significant differences observed between filtered and unfiltered 

liquid sample analytical results.

Because the liquid samples were preserved by addition of acid prior to filtering, the 

radioactive particulates may have entered solution and were therefore not removed by 

filtering. (Section 3.6.2)

 The Rn concentrations in natural gas sampled at Pennsylvania well sites during this study 

are consistent with the Rn concentrations in natural gas reported by the U.S. Geological 

Survey (USGS) for Pennsylvania, which range from 1 to 79 pCi/L with an overall median of

37 pCi/L.

The Rn in natural gas measured ranged from 3.0 to 147.5 pCi/L, with a median Rn 

concentration of 40.8 pCi/L. (Section 3.4.2)

 There is little potential for additional Rn exposure to workers and members of the public on 

or near natural gas well sites.

The Rn concentrations in ambient air sampled at well sites during this study are consistent 

with the typical ambient background Rn concentrations of 0.2 to 0.7 pCi/L. (Section 3.4.1)

9.1.2 Wastewater Treatment Plants (Section 4.0)

9.1.2.1 Publicly Owned Treatment Works

 There is little potential for internal radiation exposure to workers and members of the public 

from and  surface radioactivity at POTWs.

Nine of the 566  measurements and 68 of the 566  measurements of total surface 

radioactivity exceeded the RG 1.86 criteria. One of the 286 removable  measurements and 

none of the 286 removable  measurements exceeded the RG 1.86 criteria. Fixed or 

removable  and  surface radioactivity may present a potential inhalation or ingestion 

hazard if disturbed in the future. (Section 4.1.6.2)
PA DEP TENORM Study Report – Section 9.0 Rev. 0

January 2015 9-4

 There is little potential for exceeding public dose limits from external gamma radiation for 

workers and members of the public at POTWs.

The highest average gamma radiation exposure rate was 36.3 R/hr, and the maximum 

gamma radiation exposure rate measured was 257 R/hr. Assuming the time period of 

exposure is a full occupational year of 2,000 hours, the maximum average POTW annual 

external gamma radiation exposure was estimated as 62.6 mrem/yr, which is less than the 

maximum public dose limit of 100 mrem/yr. (Sections 4.1.2.1 and 4.1.6.1)

 There is little potential for radiological exposure to workers and members of the public from 

handling and temporary storage of filter cake at POTW-I’s.

However, there is a potential for radiological environmental impacts from spills and the 

long-term disposal of POTW-I filter cake.

The filter cake analytical results for POTW-I plants show Ra-226 and Ra-228 are present 

above typical background concentrations in soil. The average Ra-226 result was 20.1 pCi/g 

with a large variance in the distribution. The maximum result was 55.6 pCi/g. The average 

Ra-228 result was 8.32 pCi/g, and the maximum result was 32.0 pCi/g Ra-228. 

(Section 4.1.2.1)

 There is little potential for radiological exposure to workers and members of the public from 

handling and temporary storage of filter cake at POTW-N’s.

There is little potential for radiological environmental impacts from spills and the long-term 

disposal of POTW-N filter cake.

The radioactivity levels at POTW-N plants presented in Table 4-6 were above typical 

background concentrations in soil with Ra-226 average and maximum results of 8.89 pCi/g 

and 35.4 pCi/g. The average and maximum Ra-228 results were 2.13 pCi/g and 7.26 pCi/g. 

(Section 4.1.2.1)

 There is little potential for radiological exposure to workers and members of the public from 

sediment-impacted soil at POTW-I’s.

However, there is a radiological environmental impact to soil from the sediments from 

POTW-I’s.

The analytical results for POTW-I sediment-impacted soil samples indicate Ra-226 and 

Ra-228 are present at concentrations above typical background in soil. The average Ra-226 

result was 9.00 pCi/g, and the maximum result was 18.2 pCi/g. The average Ra-228 result 

was 3.52 pCi/g, and the maximum result was 6.25 pCi/g. (Section 4.1.2.2)

 There is little potential for additional Rn exposure to workers and the members of the public

inside POTW-I’s.
PA DEP TENORM Study Report – Section 9.0 Rev. 0

January 2015 9-5

Indoor Rn results from POTW-I results ranges from 0.2 to 8.7 pCi/L. One result exceeds the 

EPA action level of 4.0 pCi/L. The Rn measured in indoor air averaged 1.7 pCi/L. The 

average is above the average indoor level of 1.3 pCi/L in the U.S. as reported by EPA. 

(Section 4.1.4)

9.1.2.2 Centralized Wastewater Treatment Plants

 There is potential for internal radiation exposure to workers and members of the public from 

and  surface radioactivity at CWTs that treat O&G wastewater. Fixed  and  surface 

radioactivity may present a potential inhalation and ingestion hazard if disturbed during 

routine system maintenance.

One hundred eighty-six of the 777  measurements and 461 of the 777  measurements of 

total surface radioactivity exceeded the RG 1.86 criteria. Seven of the 805 removable 

measurements and 6 of the 805 removable  measurements exceeded the RG 1.86 criteria. 

The average of the  total surface radioactivity measurements exceeded the RG 1.86 criteria 

in 10 of the 11 CWT facilities surveyed. The average of the total  surface radioactivity 

measurements exceeded the RG 1.86 criteria in four of the 11 CWT facilities surveyed. The 

corresponding removable radioactivity measurements are mostly less than the RG 1.86 

criteria, indicating the total radioactive contamination measured is fixed to the surface and 

not immediately available for inhalation or ingestion. (Section 4.2.6.2)

 There is little potential for exceeding public dose limits from external gamma radiation for 

workers and members of the public at CWTs that treat O&G wastewater.

Assuming the time period of exposure is a full occupational year of 2,000 hours, and the 

average maximum exposure rate of 19.1 R/hr, the maximum average CWT annual external 

gamma radiation exposure was estimated as 38 mrem/yr. The maximum gamma radiation 

exposure rate measured was 502 R/hr on contact with the outside of a wastewater tank. 

(Section 4.2.6.1)

 There is little potential for radiological exposure to workers and members of the public from 

handling and temporary storage of filter cake at CWTs that treat O&G wastewater.

However, there is a potential for radiological environmental impacts from spills and the 

long-term disposal of CWT filter cake from CWTs that treat O&G wastewater.

The analytical results indicate all the CWT filter cake samples contain elevated Ra-226 and 

Ra-228 above typical background levels for soil. The maximum results were 307 pCi/g of 

Ra-226 and 177 pCi/g of Ra-228. Five of 27 filter cake samples exceeded the DOT Ra

threshold for labeling as radioactive material. (Section 4.2.2.1)

 There is little potential for radiological exposure to workers and members of the public from 

sediment-impacted surface soil at CWTs that treat O&G wastewater.

However, there is a radiological environmental impact to soil from the sediments from CWTs

that treat O&G wastewater.
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Sediment-impacted soil was collected at the accessible effluent discharge points at the 

CWTs. Radium above typical soil background levels to a maximum of 508 pCi/g of total Ra 

was identified in the sediment-impacted soil samples. (Section 4.2.7)

 There is little potential for radiological exposure to workers and members of the public from 

impacted soil at CWTs that treat O&G wastewater.

However, there is a radiological environmental impact to surface soil at CWTs that treat 

O&G wastewater.

Gamma radiation walkover surveys identified areas with radioactivity above local 

background. At three of these locations, a biased soil sample was collected to determine the 

amount of activity at or near the surface. Radium above soil typical background levels to a 

maximum of 117 pCi/g Ra-226 and 83.1 pCi/g Ra-228 was identified in biased soil samples. 

(Section 4.2.2.3)

 There is little potential for additional Rn exposure to workers and the members of the public

inside CWTs that treat O&G wastewater.

Indoor air was sampled and analyzed for Rn concentration at various CWT indoor locations 

such as break rooms, laboratories, offices, etc. The results ranged from 0.9 to 5.0 pCi/L. 

One result exceeded the EPA action level. The Rn measured in indoor air averaged 

2.0 pCi/L. The average is above the average indoor level of 1.3 pCi/L in the U.S. as reported 

by EPA. (Sections 4.2.4 and 4.2.6.3)

9.1.2.3 Zero Liquid Discharge Plants

 There is potential for internal and  surface radioactivity exposure to workers and 

members of the public at ZLDs that treat O&G wastewater. Fixed  and  surface 

radioactivity may present a potential inhalation and ingestion hazard if disturbed during 

future routine system maintenance.

One hundred fifty-nine of the 566  measurements and 175 of the 566  measurements of 

total surface radioactivity exceeded the RG 1.86 criteria. Fourteen of the 589 removable 

measurements and 2 of the 589 removable  measurements exceeded the RG 1.86 criteria.

The highest average total  and  surface radioactivity levels were 239 dpm/100 cm2and 

4,740 dpm/100 cm2. The maximum total  and  surface radioactivity levels were 

1,410 dpm/100 cm2and 49,700 dpm/100 cm2. The corresponding removable surface 

radioactivity measurements are mostly less than the RG 1.86 criteria, only 14 of 589 

measurements exceeded the applicable criteria, indicating the total surface radioactivity 

measured is fixed to the surface and not immediately available for inhalation or ingestion. 

Fixed  and  surface radioactivity may present a potential inhalation or ingestion hazard if 

disturbed during routine system maintenance. (Section 4.3.6.2)

 There is little potential for exceeding public dose limits from external gamma radiation for 

workers and members of the public at ZLDs that treat O&G wastewater.
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The maximum average gamma radiation exposure rate measured at any of the ZLD plants 

was 43.1 R/hr. The lowest background gamma radiation exposure rate measured at any of 

the sites was 5 R/hr. Assuming the time period of exposure is a full occupational year of 

2,000 hours, the maximum average ZLD annual external gamma radiation exposure was 

estimated as 76 mrem/yr. The maximum gamma radiation exposure rate measured was 

445 R/hr. (Sections 4.3.1.4 and 4.3.6.1)

 There is little potential for radiological exposure to workers and members of the public from 

handling and temporary storage of filter cake at ZLDs that treat O&G wastewater.

However, there is a potential for radiological environmental impacts from spills and the 

long-term disposal of filter cake from ZLDs that treat O&G wastewater.

Radium-226 and Ra-228 were measured in ZLD filter cake samples at concentrations above 

typical background levels for surface soils. Radium-226 concentrations ranged from 3.08 to 

480 pCi/g and Ra-228 concentrations ranged from 0.58 to 67.3 pCi/g. (Section 4.3.2.1)

 There is little potential for radiological exposure to workers and members of the public from 

influent and effluent water at ZLDs that treat O&G wastewater.

However, there is a potential for radiological environmental impacts from spills of influent 

and effluent water at ZLDs that treat O&G wastewater.

Radium (Ra-226 and Ra-228) was routinely detected in all liquid influent and effluent 

sample types with an approximate 50 percent difference between influent and effluent, but 

little difference between filtered and unfiltered results. Results ranged from 29.0 to 

20,900 pCi/L. (Section 4.3.5)

 There is little potential for additional Rn exposure to workers and the members of the public

at ZLDs that treat O&G wastewater.

Indoor air was sampled and analyzed for Rn concentration at various indoor locations such as 

break rooms, laboratories, offices, etc. The results ranged from 0.5 to 4.9 pCi/L. Two results 

exceeded the EPA action level. The Rn measured in indoor air averaged 2.3 pCi/L. The 

average is above the average indoor level of 1.3 pCi/L in the U.S. as reported by EPA. 

(Sections 4.3.4 and 4.3.6.3)

 There is little potential for exceeding public dose limits from external gamma radiation for 

truck drivers from hauling O&G wastewater or sludge/filter cake from facilities that treated 

O&G wastewater.

It was assumed a truck driver hauled full containers with either wastewater or sludge/filter 

cake for four hours per day and made return trips with empty containers for four hours per 

day. The driver was assumed to work 40 hours per week for 10 weeks per year hauling O&G 

wastewater or sludge. The total estimated dose to the wastewater truck driver was 

0.35 mrem/yr. The total estimated dose to the sludge truck driver was 52 mrem/yr. 

(Section 4.3.6.4)
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9.1.3 Landfills (Section 5.0)

 There is little potential for radiological exposure to workers and members of the public from 

leachate at landfills.

 There is little difference in the radium detected in the leachate from the nine landfills 

selected based on the volume of O&G industry waste accepted and from the 42 other 

landfills.

Samples of leachate were collected from the nine landfills selected based on the volume of 

O&G industry waste received and from the 42 other landfills not selected based on the 

volume of O&G industry waste received and analyzed using gamma spectroscopy for Ra-226 

and Ra-228. Radium was detected above the MDC value in 34 of 51 samples. Radium-226 

results ranged from 26.5 to 416 pCi/L with an average of 112 pCi/L in the 42 unselected 

landfills and 106 pCi/L in the nine selected landfills. Radium-228 results ranged from 2.50 

to 84.0 pCi/L with an average of 12.6 pCi/L in the 42 unselected landfills and 16.5 pCi/L in 

the nine selected landfills. (Section 5.1)

 There is limited potential for radiological environmental impacts from spills or discharges of 

effluent or influent leachate at landfills that accept O&G waste for disposal.

Nine influent and seven effluent leachate samples were collected at the nine selected 

landfills. Radium was detected in all of the leachate samples. Radium-226 results ranged 

from 26.5 to 378 pCi/L with an average of 127 pCi/L for effluent samples and 64.7 pCi/L for 

influent samples. Radium-228 results ranged from 3.00 to 84.0 pCi/L with an average of 

19.9 pCi/L for effluent samples and 6.17 pCi/L for influent samples. The influent and 

effluent samples from the same facility do not represent the same leachate at different times 

in treatment. (Section 5.2.1)

 There is little potential for radiological exposure to workers and members of the public from

handling and temporary storage of filter cake at landfills that accept O&G waste for 

disposal.

However, there is a potential for radiological environmental impacts from spills and the 

long-term disposal of landfill filter cake from landfills that accept O&G waste for disposal.

Filter cake from three of the nine selected landfills was sampled and analyzed using gamma 

spectroscopy. Radium was detected in all of the filter cake samples. Radium-226 results 

ranged from 8.73 to 53.0 pCi/g, with an average of 24.3 pCi/g. Radium-228 results ranged 

from 1.50 to 4.93 pCi/g, with an average of 3.77 pCi/g. (Section 5.2.2)

 There is little potential for radiological exposure to workers and members of the public from 

sediment-impacted soil at landfills that accepted O&G waste for disposal.

However, there may be a radiological environmental impact to soil from the sediments from 

landfill leachate treatment facilities that treat leachate from landfills that accept O&G waste 

for disposal.
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The three landfills that had filter cake sampled also discharged effluent water to the 

environment. At each of the three effluent outfalls, a sediment-impacted soil sample was 

collected. Radium was detected in all of the samples. Radium-226 results ranged from 2.82 

to 4.46 pCi/g with an average of 3.57 pCi/g. Radium-228 results ranged from 0.979 to 

2.53 pCi/g with an average of 1.65 pCi/g. (Section 5.2.3)

 There is little potential for additional Rn exposure to workers and the members of the public

at or from landfills that accept O&G waste for disposal.

Ambient air was sampled at the fence line of each of the nine selected landfills and analyzed 

for Rn concentration. The Rn in ambient air at the fence line of the landfills ranged from 

0.2 to 0.9 pCi/L consistent with U.S. background levels of 0.2 to 0.7 pCi/L in outdoor 

ambient air. (Section 5.2.4)

 There is little potential for internal and  surface radioactivity exposure to workers and 

members of the public at landfills that accept O&G waste for disposal.

None of the 195  measurements and 17 of the 195  measurements of total surface 

radioactivity exceeded the RG 1.86 criteria. All average total  and  surface radioactivity 

levels were below the RG 1.86 criteria. The maximum total  and  concentrations were 

84.6 dpm/100 cm2and 3,630 dpm/100 cm2. The average removable  and  levels at each 

landfill were below the RG 1.86 criteria. The maximum removable  and  levels were also 

below the RG 1.86 criteria. None of the 205 removable  or  surface radioactivity 

measurements exceeded the RG 1.86 criteria. (Section 5.4.1.1)

 There is little potential for exceeding public dose limits from external gamma radiation for 

workers and members of the public at landfills that accept O&G waste for disposal.

The highest average exposure rate was 13.5 R/hr, and the maximum gamma exposure rate 

measured was 93.7 R/hr. The minimum, limiting local background measured was 5 R/hr.

Assuming the duration of exposure is a full occupational year of 2,000 hours, the external 

gamma radiation exposure at the landfill was estimated as 17 mrem/yr, which is much less 

than the 100 mrem/yr dose equivalent limit for a member of the public. (Sections 5.3 and 

5.4.1)

9.1.4 Gas Distribution and End Use (Section 6.0)

9.1.4.1 Natural Gas in Underground Storage

 Radon concentrations in natural gas are lower after underground storage.

Natural gas samples were collected at four underground storage sites in Pennsylvania.

Duplicate samples were collected at each site during injection into the storage formation, and 

also during withdrawal from the storage formation. (Section 6.1)
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9.1.4.2 Natural Gas-Fired Power Plants

 Radon concentrations in the natural gas sampled entering power plants are consistent with 

the Rn in natural gas concentrations in samples collected at well sites.

The two natural gas sample results from natural gas-fired power plants were 33.7 ± 1.8 pCi/L 

and 35.7 ± 11.0 pCi/L. (Section 6.2 and Table 6.3)

 There is little potential for exceeding public dose limits from external gamma radiation for 

workers and members of the public at natural gas-fired power plants.

The gamma radiation exposure rate survey results at the PP-02 power plant were within the 

range of natural background of gamma radiation for PA. The exception occurred on the 

external surface of a pipe elbow where the range of measurement results observed was 15 to 

17 μR/hr. (Section 6.2)

 There is little potential for additional Rn exposure to workers and the members of the public

at or from natural gas-fired power plants.

Ambient air was sampled at the PP-02 power plant site fence line. The fence line Rn monitor 

results were all at or below the MDC value for the analysis. (Section 6.2)

9.1.4.3 Compressor Stations

 Radon concentrations in the natural gas sampled at compressor stations are consistent with 

the Rn in natural gas concentrations in samples collected at well sites.

All compressor stations were receiving predominately Marcellus Shale unconventional 

natural gas at the time of sample collection. The range of compressor station natural gas Rn 

results is 28.8 ± 1.4 to 58.1 ± 1.1 pCi/L, which is consistent with the production site Rn 

sample results. (Section 6.3 and Table 6.5)

 There is little potential for additional Rn exposure to workers and the members of the public

at or from natural gas compressor stations.

Ambient air was sampled at the CS-01 compressor station fence line for the measurement of 

Rn concentrations. The fence line Rn monitors results ranged from 0.1 to 0.8 pCi/L. The 

average concentration at each fence line location was within the range of typical ambient 

background Rn concentrations in outdoor ambient air in the U.S. (Section 6.3) 

9.1.4.4 Natural Gas Processing Plant

 Radon concentrations in natural gas entering the natural gas processing plant are consistent 

with levels measured at well sites.

Radon in natural gas sampled entering the plant measured 67.7 pCi/L. The Rn in natural gas 

sampled at the processing plant outflow measured 9.3 pCi/L. (Section 6.4 and Table 6.7)
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 There is potential for exceeding public dose limits from external gamma radiation for 

workers at the natural gas processing plant.

Contact readings measured with filter housings ranged from background to 75 R/hr, with 

two exceptions; one measured 350 R/hr and the other measured 900 R/hr. Radiation 

exposure rates with values ranging from 20 to 400 R/hr were measured on additional 

system components. (Section 6.4)

 There is potential for internal and  surface radioactivity exposure to workers at the 

natural gas processing plant when a filter housing is opened.

The filter housing on the facility propenizer equipment was opened during a filter change-out 

and a sample of the cardboard filter media was collected. The filter media sample was 

smeared for removable  and  surface radioactivity. The average  and  surface 

radioactivity levels are below the RG 1.86  and  removable surface radioactivity criterion.

The results of samples collected from the facility propenizer equipment filter had a Pb-210 

activity result of 3,580 pCi/g, but no other gamma-emitting NORM radionuclide results were 

above 1 pCi/g. The gross  and  removable surface radioactivity results for the filter media 

sample are elevated relative to the RG 1.86 gross  and  removable surface radioactivity 

criterion. (Section 6.5)

9.1.4.5 Radon Dosimetry

 There is little potential for additional Rn exposure to members of the public in homes using 

natural gas from Marcellus Shale wells.

 The potential radiation dose received by home residents is a small fraction of the allowable 

general public dose limit of 100 mrem/yr.

Radon is transported with natural gas into structures (homes, apartments, and buildings) that 

use natural gas for purposes such as heating and cooking. The incremental increase of 

potential dose from Rn-222 to occupants of a typical home from use of natural gas was 

conservatively estimated as 5.2 mrem/yr for the median dose and 17.8 mrem/yr for the 

maximum dose. Based on the Rn and natural gas data collected as part of this study and the 

conservative assumptions made, the incremental Rn increase in a home using natural gas 

appliances is estimated to be very small, and would not be detectable by commercially 

available Rn testing devices. The average and maximum calculated Rn concentration in 

homes were 0.04 and 0.13 pCi/L, consistent with the EPA estimated indoor average of 

0.13 pCi/L. (Section 6.6)

9.1.5 Oil and Gas Brine-Treated Roads (Section 7.0)

 Radium activity measured in O&G brine-treated road samples is greater than typical surface 

soil concentrations.

Biased surface soil samples were collected based on the audio response of the gamma scan 

survey instrument ratemeter on 31 of the 32 O&G brine-treated roads. When an area with 
PA DEP TENORM Study Report – Section 9.0 Rev. 0

January 2015 9-12

elevated radioactivity was detected, surface soil samples were collected at that area. After 

correcting the reported Ra-226 activity by 0.992 pCi/g of natural background activity and 

0.741 pCi/g of U-235 bias, 18 of 31 samples have excess Ra ranging from 0.020 to

5.23 pCi/g above natural background. (Sections 7.0 and 7.2.1)

 Radium activity measured in reference background road samples is greater than typical

surface soil concentrations. The reference background roads were selected by geographical 

location to O&G brine-treated roads selected for the study.

As a point of reference and for comparison, 18 roads in the geographic vicinity of the subject 

roads that have not been identified as O&G brine-treated were selected for surveying, and 14 

biased soil samples were collected. After correcting the reported Ra-226 activity by 

0.819 pCi/g of natural background activity and 0.71 pCi/g of U-235 bias, 11 of 14 samples 

have excess Ra ranging from 0.021 to 61.5 pCi/g above natural background. Three of the 

Ra-228 results are greater than 2.98 pCi/g, which is approximately three times natural 

background for the Th series. (Section 7.2.2)

 The excess Ra measured in reference background samples is higher than for the identified 

O&G brine-treated roads.

The average excess Ra-226 for roads identified as having been brine-treated is 1.13 pCi/g 

compared to an average of 8.23 pCi/g on the background reference roads. One possible 

explanation is that all of the roads have been treated with brine. After the 32 roads had been 

identified as brine-treated, the reference background roads were selected by proximity to the 

32 roads. (Section 7.2.2)

 There is little potential for members of the public exceeding the public dose limit from 

exposure to Ra in O&G brine-treated roads.

To evaluate potential exposure to the public from the brine-treated roads, a source term of 

1 pCi/g of Ra-226 and 0.5 pCi/g of Ra-228 was assumed within a 6-inch layer of surface 

material (treated road surface). The estimated total dose from 1 pCi/g of Ra-226 and 

0.5 pCi/g of Ra-228 above natural background in surface soil, to a recreationist, in the year of 

maximum exposure (year 1) is 0.441 mrem/yr, which is below the 100 mrem/yr public 

exposure criteria based on assumed activity concentrations. The actual dose received is 

dependent upon both the excess Ra radioactivity in surface soil and the time spent exposed to 

the soil surface. (Section 7.3)

9.2 Recommendations for Future Actions

9.2.1 Well Sites

 Conduct research and investigation of vertical and horizontal drill cuttings for beneficial use, 

onsite disposal, and future landfill disposal protocols.

 Add sampling and analyses for Ra-226, Ra-228, and additional man-made radionuclides such 

as tracers used in the O&G industry to Pennsylvania spill response protocol for spills of 
PA DEP TENORM Study Report – Section 9.0 Rev. 0

January 2015 9-13

flowback fluid, hydraulic fracturing fluid, or produced water. Field survey instrumentation 

should also be available for surveys of areas impacted by the spill.

9.2.2 Wastewater Treatment Plants

 Perform routine survey and assessment of areas impacted with surface radioactivity to 

determine personnel protective equipment (PPE) use and monitoring during future activity 

that may cause surface  and  radioactivity to become airborne.

 Conduct additional radiological sampling and analyses and radiological surveys at all 

WWTPs accepting wastewater from O&G operations to determine if there are areas of 

contamination that require remediation; if it is necessary to establish radiological effluent 

discharge limitations; and if the development and implementation of a spill policy is 

necessary.

9.2.3 Landfills

• Evaluate and, if necessary, modify the landfill disposal protocol for sludges/filter cakes and 

other solid waste-containing TENORM.

 Conduct additional radiological sampling and analyses and radiological surveys at all 

facilities that treat leachate from landfills that accept waste from O&G operations to 

determine if there are areas of contamination that require remediation; if it is necessary to 

establish radiological effluent discharge limitations; and if the development and 

implementation of a spill policy is necessary.

 Add total Ra (Ra-226 and Ra-228) to the annual suite of contaminants of concern in leachate 

sample analyses.

9.2.4 Gas Distribution and End Use

 Survey and sample internal surfaces of natural gas plant piping and filter housings for 

radiological contamination. This effort should include evaluation of worker exposure and 

buildup of radioactivity in systems from natural gas processing and transmission. Evaluate 

monitoring and recommendation of PPE and other controls to be used during pipe clean-out 

and other activities when internal surfaces are exposed.

9.2.5 Oil and Gas Brine-Treated Roads

 Perform further study of O&G brine-treated roads. This study should evaluate produced 

water radionuclide concentrations prior to treatment, resultant surface activity and 

radionuclide concentration of road surfaces and future Ra migration.
PA DEP TENORM Study Report – Section 10.0 Rev. 0

January 2015 10-1

10.0 REFERENCES

Section 1.0:

1. PSU Marcellus Center for Outreach and Research (MCOR) 2014. www.marcellus.psu.edu, 

August.

2. U.S. EPA 2014. > Climate Change > Natural Gas Star Program > Basic Info, 

www.epa.gov/methane/gasstar/basi-information/index.html, August.

3. U.S. EPA 2003. “EPA Assessment of Risks from Radon in Homes,” June.

Section 2.0:

1. ANSI/HPS 2009. N13.53-2009, Control and Release of Technologically Enhanced NORM 

(TENORM).

2. DOE 1990. DOE Procedure Gamma 4.5.2.3, EML Procedures Manual, 27th Edition, Vol. I, 

DOE Report HASL-300-ED. 27-VOL. 1.

3. DOT, 49 CFR 173.436, Radioactive Material.

4. EPA 2012. U.S. EPA/OAR/IED (6609J), EPA 402-K-12-002, A Citizen’s Guide to Radon, 

May. Also: http://www.epa.gov/radon/pubs/citguide.html

5. EPA 2000. Directive No. 9200.4-35, Remediation Goals for Radioactively Contaminated 

CERCLA Sites.

6. EPA 1980. EPA 900.0, “Prescribed Procedures for Measurement of Radioactivity in 

Drinking Water,” U.S. EPA-6000/4-80-032, August.

7. EPA, Drinking Water Standard, 40 CFR 141.66.

8. Jenkins, P.H., Burkhart, J.F., and Camley, R.E. 2014. “Errors in Measurement of Radon-222 

in Methane and Carbon Dioxide using Scintillation Cells Calibrated for Radon-222 in Air.” 

Health Physics, Vol. 106, No. 3, March.

9. NRC, 10 CFR 20 Appendix B, Table 1, Col 3.

10. NRC, 10 CFR 20 Appendix B, Table 2, Liquid Effluent.

11. NRC, 10 CFR 20.1201, Occupational Dose Limits for Adults.

12. NRC, 10 CFR 20.1301, Radiation Dose Limits for Members of the Public.

13. NRC, 10 CFR 20.1402-20.1403, Radiological Criteria for Unrestricted Use.

14. NRC 1974a. Regulatory Guide 1.86, Termination of Operating Licenses for Nuclear 

Reactors (1974)—Criteria for Natural Thorium Including Ra-228.

15. NRC 1974b. Regulatory Guide 1.86, Termination of Operating Licenses for Nuclear 

Reactors (1974)—Criteria for Ra-226.

16. OSHA, 29 CFR 1910.1096.

17. United Nations Scientific Committee on the Effects of Atomic Radiation (UNSCEAR) 2000. 

Sources and Effects of Ionizing Radiation.
PA DEP TENORM Study Report – Section 10.0 Rev. 0

January 2015 10-2

Section 3.0:

1. Jenkins et al., 2014. Health Physics, Vol. 106, No. 3, March.

2. NRC 1998a. Table 6.4, NaI Scintillation Detector Scan MDCs for Common Radiological 

Contaminants, NUREG-1507, Minimum Detectable Concentrations With Typical Radiation 

Survey Instruments for Various Contaminants and Field Conditions, June.

3. NRC 1998b. Table 6.3, NaI Scintillation Detector Count Rate Versus Exposure Rate 

(cpm/μR/hr), NUREG-1507, Minimum Detectable Concentrations With Typical Radiation 

Survey Instruments for Various Contaminants and Field Conditions, June. 

4. NRC 1974. Regulatory Guide 1.86, Termination of Operating Licenses for Nuclear Reactors 

(1974)—Criteria.

Section 4.0:

1. EPA 2012. U.S. EPA/OAR/IED (6609J), EPA 402-K-12-002, A Citizen’s Guide to Radon, 

May. Also: http://www.epa.gov/radon/pubs/citguide.html

2. NRC 1998a. Table 6.4, NaI Scintillation Detector Scan MDCs for Common Radiological 

Contaminants, NUREG-1507, Minimum Detectable Concentrations With Typical Radiation 

Survey Instruments for Various Contaminants and Field Conditions, June.

3. NRC 1974. Regulatory Guide 1.86, Termination of Operating Licenses for Nuclear Reactors 

(1974)—Criteria.

Section 5.0:

1. NRC 1998a. Table 6.4, NaI Scintillation Detector Scan MDCs for Common Radiological 

Contaminants, NUREG-1507, Minimum Detectable Concentrations With Typical Radiation 

Survey Instruments for Various Contaminants and Field Conditions, June.

2. NRC 1974. Regulatory Guide 1.86, Termination of Operating Licenses for Nuclear Reactors 

(1974)—Criteria.

Section 6.0:

1. American Gas Association, Washington, D.C.

2. DOT 2011. National Pipeline Mapping System, User Guide.

3. EPA 2003. Pawal, D.J. and Puskin, J.S. EPA Assessment of Risks from Radon in Homes, 

June.

4. Jenkins et al., 2014. Health Physics, Vol. 106, No. 3, March.

5. Nazaroff, W.W. and Nero, A.V., 1988. Radon and its Decay Products in Indoor Air. John 

Wiley & Sons.

6. NRC 1974. Regulatory Guide 1.86, Termination of Operating Licenses for Nuclear Reactors 

(1974)—Criteria.

7. Rowan, E.L. and Kraemer, T. F. U.S. Geological Survey. Radon-222 Content of Natural 

Gas Samples from Upper and Middle Devonian Sandstone and Shale Reservoirs in 

Pennsylvania: Preliminary Data, Open-file Report Series 2012-1159.

8. Spectra Energy Transmission 2014, Personal Communication, May.
PA DEP TENORM Study Report – Section 10.0 Rev. 0

January 2015 10-3

9. UNSCEAR 2006. Annex E.

10. U.S. Census, American Housing Survey, 2011, Table C-02-AH.

Section 7.0:

1. Pennsylvania Department of Environmental Protection (DEP) 2013. Fact sheet, 

Roadspreading of Brine for Dust Control and Road Stabilization, developed under the 

authority of the Clean Streams Law, the Solid Waste Management Act, and Chapters 78 and 

101 of DEP’s Rules and Regulations.

2. NRC 1998a. Table 6.4, NaI Scintillation Detector Scan MDCs for Common Radiological 

Contaminants, NUREG-1507, Minimum Detectable Concentrations With Typical Radiation 

Survey Instruments for Various Contaminants and Field Conditions, June.

Section 8.0:

1. DEP 2013. Sample and Analysis Plan Part I, Field Sampling Plan (FSP), April.

2. DEP 2013. Sample and Analysis Plan Part II, Quality Assurance Project Plan (QAPP), April.

3. DEP. Laboratory QAM.

4. NRC 1994. NRC Inspection Manual Procedure 84750, March.

Section 9.0:

1. EPA 2012. U.S. EPA/OAR/IED (6609J), EPA 402-K-12-002, A Citizen’s Guide to Radon, 

May. Also: http://www.epa.gov/radon/pubs/citguide.html

2. NRC 1974. Regulatory Guide 1.86, Termination of Operating Licenses for Nuclear Reactors 

(1974)—Criteria.