MISSIONREPORT2018

Moving nuclear security forward

Radiological reportof the French environment
from 2015 to 2017

Radiological reportof the French environment
from 2015 to 2017

CONTENTS
O1. RADIOLOGICAL MONITORING OF THE ENVIRONMENT .  .  .  .  .  .  .  .  .  . 61.1. THE PURPOSE OF THE RADIOLOGICAL MONITORING OF THE ENVIRONMENT.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 61.2. RADIOLOGICAL MONITORING DEVICES USED FOR THE ENVIRONMENT. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 8Monitoring the atmosphere .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 8Monitoring the aquatic environment.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 16
Monitoring the terrestrial environment. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 20
Summary of the strategic criteria applied and the sampling and measuring devices used tomonitor the radiological properties of the different environmental components .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 22
1.3. FROM SAMPLING PLANS TO MEASURING RESULTS 24
1.4. 	DETAILS OF THE PRESENTATION AND USE OF MEASURING RESULTS
FOR THE 2015-2017 RADIOLOGICAL REPORT .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 26
Data sources and units .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 26
Decision thresholds, insignificant results, metrological uncertainties and rounding .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 27
Mean values and other statistical indicators .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 28
1.5. 	THE RNM (RÉSEAU NATIONAL DE MESURES / FRENCH METROLOGICAL NETWORK)FOR ENVIRONMENTAL RADIOACTIVITY .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 34
The reference site for environmental radioactivity measurements in France.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 34
RNM operations. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 35
Laboratory approval processes .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 39

O2. BACKGROUND RADIATION IN FRANCE. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 46
2

2.1. NATURAL BACKGROUND RADIATION .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 46
Cosmic radiation and cosmogenic radionuclides in the environment .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 46
Telluric radionuclides in the environment .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 48
2.2. BACKGROUND RADIATION FROM OLD FALLOUT. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 61
Fallout from the atmospheric testing of nuclear weapons.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 61
Fallout from the Chernobyl accident.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 64
Fallout from the Fukushima accident .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 64
2.3. RANGE OF POPULATION EXPOSURE LEVELS DUE TO BACKGROUND RADIATION IN FRANCE .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 66
Effective external doses due to cosmic and telluric radiation. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 66
Effective doses received by ingesting natural radionuclides via food or smoking .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 66
Effective dose received by inhaling radon.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 68
Effective doses due to residual radioactivity from old fallout comprising artificial radionuclides .  .  .  .  .  .  .  .  .  .  .  .  .  . 69
Report on effective doses received due to background radiation in France. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 73

O3. DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE .  .  .  .  .  .  . 76
3.1. OPERATIONAL NUCLEAR POWERPLANTS (NPP) .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 76
Discharged radioactive effluents .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 77
Monitoring plans for the immediate environment of an NPP .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 78
The impact of NPP on their immediate environment and associated public exposure .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 80
Conclusions.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 103
3.2. NUCLEAR POWERPLANTS IN THE DECOMMISSIONING PROCESS .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 106
Creys-Malville site. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 106
Brennilis site .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 112
3.3. INDUSTRIAL SITES.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 116
Malvési site .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 116
Tricastin site .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 122
Romans-sur-Isère site.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 130
La Hague site. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 135
Aube storage centre and Morvilliers storage centre .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 180
3.4. RESEARCH SITES .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 188
Marcoule site.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 188
Valduc site .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 199
Cadarache site. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 210/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

Grenoble sites .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 216
CEA DAM centre/Île-de-France region .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 224
Saclay site .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 229
Fontenay-aux-Roses site .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 238
3.5. NUCLEAR NAVAL BASES.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 244
Brest military port and Île-Longue operational base .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 244
Cherbourg military port .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 244
Toulon military port .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 244
Radiological monitoring of the environment. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 245
Site impacts on the environment .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 248

O4. FORMER MINING SITES.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 256
4.1. INTRODUCTION.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 256
General information on mining sites .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 257
4.2. 	THE POTENTIAL IMPACT OF FORMER MINING SITES ON THEIR ENVIRONMENT AND PUBLIC EXPOSURE . . . .260
4.3. MONITORING THE IMMEDIATE ENVIRONMENT AROUND FORMER MINING SITES . . . . . . . . . . . . . . . . . . . . . . . . .260
Regulations .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 261
General description of monitoring systems .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 261
4.4. A DETAILED PRESENTATION OF 4 FORMER MINING SITES SELECTED FOR THE RADIOLOGICAL REPORT .  .  .  . 261
Écarpière site. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 263
Bosc site. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 273
La Commanderie site .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 285
La Porte site. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 293

O5. OVERVIEW OF DOSE DATAAND NEWS FOR THE 2015-2017 PERIOD. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 302
5.1. SUMMARY OF DOSE EVALUATIONS . .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 302
5.2. IODINE-131 LEVELS IN THE AIR FOR JANUARY AND FEBRUARY 2017.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 305
5.3. RUTHENIUM-106 LEVELS IN THE AIR FROM LATE-SEPTEMBER TO EARLY-OCTOBER 2017.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 306
5.4. REPORT ON RADIOLOGICAL LEVELS IN THE RU ZONE IN THE LANDES REGION .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 308

O6. UNDERSTANDING RADIOACTIVITY
AND THE INHERENT POTENTIAL PUBLIC EXPOSURE.  .  .  .  .  .  .  .  . 316
6.1. RADIONUCLIDES.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 316
6.2. RADIATION.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 317
6.3. RADIOACTIVITY: THE BECQUEREL (Bq).  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 317
6.4. HALF-LIVES.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 318
6.5. TYPES OF EXPOSURE TO ENVIRONMENTAL RADIOACTIVITY .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 318
6.6. DOSES: THE SIEVERT (Sv) .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 320
6.7. RADIATION PROTECTION. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 323

O7. SOURCES OF INFORMATION ON RADIOACTIVITYMONITORING AND THE DISTRIBUTION OF DATA .  .  .  .  .  .  .  .  .  .  .  .  . 326
7.1. WEBSITES AND SOURCES OF INFORMATION AVAILABLE TO THE PUBLIC. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .326
7.2. DISTRIBUTING INFORMATION AS PER INTERNATIONAL CONVENTIONS AND TREATIES.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 329

O8. APPENDICES.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 332
8.1. CALCULATING MEAN VALUES AND CONSIDERING INSIGNIFICANT VALUES.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 332
8.2. INDICATOR BOX PLOTS .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 334
8.3. METHOD USED TO ESTIMATE DOSES .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 335
8.4. GLOSSARY .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 343
8.5. EDITORIAL COMMITTEE.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 351

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /3

Gamma spectrometry system for measuring atmospheric aerosol filters© L. Zylberman/Graphix-Images/IRSN

4/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

O1
RADIOLOGICALMONITORING
OF THE ENVIRONMENT

1.1. T HE PURPOSE OF THE RADIOLOGICAL MONITORING OF
THE ENVIRONMENT. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 6The different purposes of the radiological monitoring of theenvironment. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 71.2. R ADIOLOGICAL MONITORING DEVICESUSED FOR THE ENVIRONMENT.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 8Monitoring the atmosphere.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 8Monitoring the aquatic environment .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 16
Monitoring the terrestrial environment.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 20
Summary of the strategic criteria applied and the sampling andmeasuring devices used to monitor the radiological properties ofthe different environmental components. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 22
1.3. F ROM SAMPLING PLANS TO MEASURING RESULTS.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 24
Analysis and sampling plans .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 24
Preparing samples.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 24
Radiological analyses .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 24
1.4. D ETAILS OF THE PRESENTATION AND USE OF MEASURINGRESULTS FOR THE 2015-2017 RADIOLOGICAL REPORT .  .  .  .  .  .  .  .  .  .  .  . 26
Data sources and units .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 26
Decision thresholds, insignificant results,
metrological uncertainties and rounding .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 27
Mean values and other statistical indicators. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 28
1.5. T HE RNM (RÉSEAU NATIONAL DE MESURES /FRENCH METROLOGICAL NETWORK) FOR
ENVIRONMENTAL RADIOACTIVITY.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 34
The reference site for environmental
radioactivity measurements in France .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 34
RNM operations .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 35
Laboratory approval processes. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 39
RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /5

O1

RADIOLOGICALMONITORING
OF THE ENVIRONMENT

1.1. THE PURPOSE OF THE
RADIOLOGICAL MONITORING OF
THE ENVIRONMENT
Many operators help to monitor the radiologicalcomposition of the French environment:

As highlighted above, monitoring is shared
between many different entities with, on the one
hand, IRSN and the public authorities monitoring
radioactivity at regional and national level, and,on the other hand, nuclear facility operators
monitoring their sites. Other public authorities
and associations additionally contribute to andboost the credibility of the overall monitoring
network. They particularly check the consistencyof the measurements taken.

• lRSN (1), ASN (1), French Ministries (health,
DGAL (1), DGCCRF (1), etc.), government services
and other public operators responsible formonitoring throughout France, or which conduct
tests or monitor specific sectors (e.g. food for the
French Ministries of agriculture and consumers);© Y. Geoffray/Areva

6• operators of nuclear facilities (ANDRA (1), CEA (1),EDF (1), ILL (1), the French Navy (1) and Orano (1)).
All of these operators monitor local levels in
the immediate vicinity of their nuclear sites
as per regulatory requirements. In general,
requirements relating to environmental
monitoring for civilian nuclear facilities aredefined in ASN (French nuclear safety authority)
decision no. 2013-DC-0360 dated 16 July 2013
on controlling disturbances and the effectsof basic nuclear facilities on health and theenvironment, amended by ASN decision no.
2016-DC-0569 dated 29 September 2016. If
necessary, this programme can be detailed andadapted to match local particularities in the formof site-specific ASN decisions. The monitoring
programme applicable to former mining sites isdefined as a prefectoral decree;• associations approved for monitoring air quality(AASQA (1)), local authorities, associations (CLI (1),environmental protection associations), whichmonitor this parameter independently to publicauthorities.

Alpha spectroscopy

1. See glossary in chapter 8.4.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

RADIOLOGICAL MONITORING OF THE ENVIRONMENT / 01
The purpose of the radiological monitoring of the environment / 1.1

The different purposes of theradiological monitoring of theenvironment

Purpose no. 4

Purpose no. 1
Help to improve our knowledge of the radiologicalcomposition of the environment and variation inthis composition. This is achieved by measuring
the different radionuclides in the different
components, quantifying radioactivity levels andmonitoring geographic variation and change overtime in order to detect any increases in artificial
radioactivity, even down to several magnitudes lessthan fluctuations in natural ambient radioactivity.
Purpose no. 2
Help to evaluate radiological exposure to protect
the health of the local populations and theenvironment, particularly by evaluating doses
and improving our knowledge of the radiologicalcomposition of the different environmental
components: air, soils, waters, food, etc.
Purpose no. 3

Purpose no. 5
Improve transparency and the quality of
information provided to the public by distributing
the results of monitoring programmes, approving
laboratories and involving several entities.
While each single measurement taken separately
will not necessarily cover all five purposes, thecombined measurements taken by the different
operators will directly and indirectly contributeto ensuring the five purposes of environmental
monitoring are covered. Each contributor
organises several types of monitoring (e.g. routine
monitoring and expertises), each designed to meet
specific targets. The immediate environments ofnuclear sites are monitored in addition to effluent
monitoring by operators. The environment must
be monitored in addition to effluent monitoring,
the latter alone is insufficient.

© IRSN

Detect any abnormal increase in environmental
radioactivity as early as possible, monitor levels
and identify the cause of the variation (naturalor anthropic) and the specific source facility forspurious discharges.

Ensure compliance with all provisions applicable
to nuclear facilities by determining the typeand source of the substances in question if thepredefined thresholds are exceeded. Help tocheck that the radiological impact of the facilities
remains below regulatory limits.

Sampling aquatic plants in the Vienne region downstream from the Civaux NPPRADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /7

1.2. RADIOLOGICAL MONITORINGDEVICES USED FOR THE
ENVIRONMENT
Two complementary approaches are used for theradiological monitoring of the environment inFrance:• continuous in situ monitoring using independent
systems (remote monitoring systems) withthe real-time transmission of results. Thesesystems (figure 1A) are mainly used to trigger analert if a major accident occurs. These systems
include:−−networks of ambient gamma dose rate sensors(e.g. IRSN Téléray network, site operator
sensors),−−IRSN's Hydrotéléray network, used to monitor
the main rivers by gamma spectrometry,downstream of all nuclear facilities and before
a river crosses a national border;
8• samples taken from the various types ofenvironment near to facilities authorised todischarge radionuclides are processed andmeasured in a laboratory. Samples are takenusing two methods:−−ad hoc environmental samples. These samples
are taken for a wide range of source matrices:
water (rain, fresh surface water, ground wateror seawater), biological indicators (mosses,
algae), soils and sediments, and food (milk anddairy products, meat, fish, molluscs, shellfish,
cereals, etc.);−−continuous sampling systems. These samples
are mainly taken in view of atmospheric(aerosols, measuring specific radionuclides
in the air such as tritium and carbon-14) andsurface water (sampling via water samplingsystems) measurements.
The type of monitoring selected will depend on the
final aim, expected performance levels and any
limitations for the analyses (interfering factors,
sampling time, etc.).

The sampling and measuring systems used, andthe types of analysis carried out in France by the
many contributors to the radiological monitoringof the environment sometimes differ substantiallyfor this reason. Some systems are suitable for thetargets assigned to nuclear operators as part of
the regulatory monitoring of their facilities, whileother operators use far more advanced analysis
techniques and sampling gear, allowing themto reach much lower decision thresholds (seechapter 1.4) to meet different priorities. Thismeans that the RNM database includes resultsfrom various sources, obtained using a range ofdifferent analytical procedures.
A detailed presentation of the various samplingsystems and analysis techniques used by thedifferent laboratories in France is therefore
required to help understand the wide range ofresults included in this radiological report.

Monitoring the atmosphere
The atmosphere is monitored using two types ofsystems: firstly, continuous measuring systems
and, secondly, continuous sampling systems(air, gas, rainwater) with subsequent laboratory
analyses.
Continuous measurements of the ambient
gamma dose rate
The ambient gamma dose rate measuring networks
represent the main continuous measuring
networks for exposure to ionising radiation in
France. These systems are configured with prealarm and alarm thresholds and connected tosupervision and stand-by systems able to trigger
an alert if a major accident occurs at a nuclear
site. The situation and any developments can beinstantaneously assessed using these systems.
These sensors (see figure 1) are deployed by
IRSN throughout France and French overseas
territories, however the network is far denser in
the immediate vicinity of nuclear sites. Operators(EDF, CEA, Orano, ANDRA, the French Navy, ILL,etc.) monitor an area with a radius of between 0
and 10 km, while IRSN completes the monitoring
network within a radius of 10 - 30 km.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

RADIOLOGICAL MONITORING OF THE ENVIRONMENT / 01
Radiological monitoring devices used for the environment / 1.2

FOCUS ARTICLE
THE MAIN FACTORS WITH AN IMPACTON GAMMA DOSE RATE RESULTS

The dose rate triggered by a source of radiation
decreases rapidly as the distance from the source
increases.
On this basis, most of the gamma radiation
reaching a detector placed 1 m above the ground,with homogeneous activity levels, is emitted within a circle with a radius of approx. 10 m. The
following figure gives an example, showing the source of the gamma radiation detected 1 m above
the ground containing 137Cs: 19% of the radiation detected is sourced from the ground area with aradius of 1 m directly under the detector, 65% from an area with a radius of 4 m, and approx. 15%
from a radius of over 10 m.
These contributions can vary depending on the energy radiated by the radionuclide in the ground.
However, the key factor to remember is that any local topography, such as embankments or aconstruction, or if the detector is located in a dip, can substantially affect these contributions.
The detector may be more directly exposed to sloped, or even vertical, surfaces, in the immediate
vicinity. A wall can also act as a shield for radiation sourced behind it, or, on the contrary,radiation from a wall can dominate the radiation sourced from the ground.

© V. Malfait/IRSN

In addition, radiation is attenuated by the ground itself, which acts as a shield (see chapter 5),
and this effect will be more proportionally noticeable if the energy radiated is weak. On this basis,in the above case, the thickness of theground contributing to the radiation
reaching the detector will also dependon the energy radiated by theradionuclide in the ground. However,for most radionuclides of interest, thisdepth will be approximately 10 - 20 cm.

Téléray sensor (left)
and field gamma spectrometry
system (right)

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /9Passive environmental dosimetry
In France, the real-time monitoring systems
mentioned previously can be completedwith monitoring based on passive dosimetry(see figure 1B) using ThermoLuminescent
Dosimeters (TLD) or RadioPhotoLuminescenceglass dosimeters (RPL) set up within the groundsof nuclear sites (for operators) or throughout
France as part of the recently-installed IRSN RPL
network. The aim is to ensure compliance withregulations a posteriori (data is integrated on amonthly-to-quarterly basis and later analysed ata laboratory).

FIGURE 1 / AMBIENT GAMMA DOSE RATE CONTINUOUS MEASURING SYSTEM, PART OF THE IRSN TÉLÉRAY NETWORK(photo 1A) AND RPL DOSIMETER SET UP AT THE CADARACHE SITE (photo 1B)

1A© A. Bouisson/MEDDTL/IRSN

10

© DR

1B

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

RADIOLOGICAL MONITORING OF THE ENVIRONMENT / 01
Radiological monitoring devices used for the environment / 1.2

Atmospheric aerosols
IRSN manages the radiological monitoring ofaerosols at national level in France. Nuclear
operators and associations also contribute tomonitoring at local level. Monitoring is based on
aerosol samples collected at filters on a daily
or weekly basis, and the subsequent laboratory
analysis of the filters.
Various types of sampling methods are usedat national level (see figure 2) depending onpriorities and target performance levels. The
main difference is air intake flowrates. A flowrateof 4 - 80 m3/h (low to medium flow) is maintainedat most stations and sampling devices for higher
flowrates (100 - 700 m3/h) are fitted at aroundtwenty-odd stations (IRSN, CEA, the French Navy).
Nuclear operators measure the gross beta activity
index using daily filter samples as well as, for somesites, measuring the gross alpha radioactivity
index, as required by regulations. This index (2) isused to detect any significant air activity anomaly
and trigger complementary investigations on thisbasis.

In addition, according to regulations, the grossbeta activity index in air must not exceed a specificlimit due to normal facility discharges.
On this basis, if the value of the gross beta
activity index exceeds 2 mBq/m3 in air, a gamma
spectrometry analysis is required as per
regulations. Gamma spectrometry will be used
to determine which radionuclides are responsible
for the excess radiation and, if these radionuclides
are artificial, to identify the source and assess theinherent radiological consequences.
IRSN and some nuclear operators systematically
carry out gamma spectrometry on aerosol
filters. Performance levels mainly depend on
intake flowrate and the duration of sampling.
To give just one example, a station with a low
flowrate can be used to measure cesium-137
activity in the air of approx. 5 mBq/m3;
a station with a high flowrate can detect levels of
0.00005 mBq/m3 with reference to IRSN stations
with a flowrate of 700 m3/h. Such stations withhigh flowrates can be used to measure residual
background radiation for cesium-137 in the air,which represents approx. 0.0002 mBq/m3 (seechapter 2), and therefore to detect any increase inthis background radiation, however small.

FIGURE 2 / EXAMPLES OF ATMOSPHERIC AEROSOL SAMPLING DEVICES© DR

700 m3/h sampler shown on the left; 80 m3/h in the centre; 10 m3/h sampler on the right.

2. The gross beta (or gross alpha) activity index is used to detect any increase in the ambient radioactivity of a given environment (air, water orbiological matrix) potentially caused by a spurious discharge from a nuclear facility. The gross beta (or alpha) activity index does not correspond to
the total activity of the beta-emitting (or alpha-emitting) radionuclides contained in the sample analysed and cannot be used to determine whichradionuclides are present.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /11

Special case: radon-222 daughter isotopes withshort lives; measuring Potential Alpha Energy(PAE)

FIGURE 3 / POTENTIAL ALPHA ENERGY MEASURING
SYSTEM

Radon-222 released from rocks has migrated
across the ground to the atmosphere and thendecays to polonium-218, lead-214, bismuth-214
and polonium-214 (see chapter 2) atoms
successively. These radionuclides are present in
the atmosphere as solid particles (aerosols), andmay or may not be attached to the atmosphericaerosol. These aerosols, rather than the radon
itself, as radon is an inert gas with a short half-life(3.8 days), can, if inhaled, settle in the respiratory
tracts and release significant amounts of energy to
the cells as they successively decay. These doses
are generally considered as radon radiation.

If total equilibrium is reached, where the activityof each of the daughter isotopes is equal to thatof the radon, for 1 Bq of radon-222, the PAE isequal to 5.66 10-9J. This factor can also be used
to express the potential alpha energy by volume
as an Equilibrium Equivalent Concentration (EEC),
in Bq/m3.
Figure 3 shows one example of a PAE measuring
device. This device measures integrated PAE in theatmosphere over the periods of exposure selectedby the operator based on the purpose defined.

FIGURE 4 / BUBBLERS FOR TAKING ATMOSPHERICTRITIUM OR 14C SAMPLES

Gases: tritium (3H) and carbon-14 (14C)
Tritium and carbon-14 are the main radionuclides
discharged into the air by nuclear facilities.
Samples of atmospheric tritium are taken by
bubbling air sucked in into containers, or bubblers,
filled with water (see figure 4). Atmospheric tritiumcontent is determined by analysing the tritium inthe bubbler water. Two types of systems are used
for the continuous monitoring of facilities: systems
with two bubblers, exclusively used to measureatmospheric tritium as water vapour (tritium
HTO), and systems with four bubblers, which areused to measure tritium HTO (first 2 bubblers)and other forms of atmospheric tritium, including
gaseous HT, in the first 2 bubblers downstream ofan oxidation furnace. Such monitoring is mainly
implemented by nuclear operators based on

© DR

12

© IRSNThe Potential Alpha Energy by volume or PAEv isused to quantify the energy which can potentiallysettle in the respiratory tracts in physical terms.
This value is used to monitor workers and mining
sites. It is expressed in J/m3 (joules per cubic
metre)

weekly liquid scintillation analyses (see figure 5).
Results generally oscillate between 0.05 and1.5 Bq/m3 (background atmospheric tritium varies
between 0.005 and 0.01 Bq/m3; see chapter 2).
Samples of carbon-14 are taken by bubbling air
sucked in into sodium hydroxide in order to trap
CO2 as carbonates. In addition to the CO2 trapped in/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

RADIOLOGICAL MONITORING OF THE ENVIRONMENT / 01
Radiological monitoring devices used for the environment / 1.2

the first 2 bubblers, these systems with 4 bubblers
also trap other forms of carbon in the air (CH4, etc.)
in the 2 bubblers fitted after a catalytic heater.
Various carbon-14 analysis techniques are used.
The main technique involves measuring thedifferent forms of carbon-14 using liquid
scintillation. Data for activity by volume obtained
based on the measurements taken using theseweekly-to-monthly samples are generally between
0.02 and 0.1 Bq/m3 (background atmosphericcarbon-14 in France is approximately 0.02 - 0.06
Bq/m3; see chapter 2).

For both tritium and carbon-14, some of theentities involved in radionuclide measurements
use methods which can reach or approximate
background radiation, particularly if suitablesampling times and analysis methods areused. The decision thresholds (3) obtained byother contributors, particularly during routine
measurements, are, however, consistent with the
purpose of monitoring nuclear facilities.
Other radionuclides in the atmospheric discharges
of some facilities are also sampled and analysed,
such as atmospheric iodine (gaseous andparticulate) and krypton-85 (a noble gas mainly
discharged by the Orano La Hague plant).
The measurements for these radionuclides are also
forwarded by operators to the RNM. Atmospherictritium and carbon-14 (and krypton-85 near to
La Hague) analyses are used to assess the
exposure of local residents near to some sites.

13© IRSNFIGURE 5 / LIQUID SCINTILLATION MEASURING DEVICE

3. The decision threshold is the lowest value of a sample measurement when the metrologist can decide whether or not activity and therefore ameasurement exists. Below this value, the activity of the sample is too low to be estimated. This decision threshold depends on performance andambient radiation around the measuring devices used (see p. 27).

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FOCUS ARTICLEPASSIVE SAMPLERS:A NEW SAMPLING TECHNIQUE
FOR TRITIUM CONTAINED IN THE AIR

Current sampling systems for atmospheric tritiumused for monitoring purposes require a power
supply and regular heavy-duty maintenance tofunction properly. This is particularly the case forthe bubblers shown on page 11. For this reason,these devices are little used for routine
monitoring, despite the fact that tritium is the radionuclide the most frequently found in theeffluents discharged by the nuclear industry.

14

On this basis, IRSN developed a device which can be used in far more operating configurations, ata much lower cost. This passive trap is based on the molecular diffusivity of gases and mainlycomprises adsorbent material, which will preferentially sample water (H2O) and the tritiatedwater vapour (HTO), and a patented sampler (figure A). The sampler consists of a lid and aninternal tapered perforated structure. The two components maintain a constant sampling rate
based on the availability of ambient water vapour (H2O and HTO). The sampler comprises
adsorbent material (a molecular sieve) which acts as a pump (as in "active" systems) and collects
the tritiated water vapour. The molecular sieve is more generally known as zeolite(aluminosilicate). This sieve adsorbs gas molecules selectively, particularly tritium.
Test results and comparisons with other devices, particularly bubblers, were satisfactory, and apatent was granted to E2SInnovation for the sale of this device in France and Europe (figure B).
Cooperation agreements with various partners were concluded to develop this sampler: CEA,
CERN, EDF, the French Navy, Orano.

FIGURE A / GEOMETRY OF THE PASSIVE PASSIF SAMPLER (IRSN patent no.: WO2014037461),
LOCATION IN THE ENVIRONMENT AND MAIN CHARACTERISTICS

Ambient water
vapour and HTO
Bq m-3Liquid scintillation
Bq L-1

Adsorption
Molecular sieve(zeolite 13X)

Acquisition ofambient
hygrometryg of water m-3

Desorption
Liquid scintillation
Bq L-1

Bq m-3of ambient HTO

Regenerated
trap media●●●/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

RADIOLOGICAL MONITORING OF THE ENVIRONMENT / 01
Radiological monitoring devices used for the environment / 1.2●●●

FIGURE B / AVAILABLE VERSIONSOLD BY E2SINNOVATION
Tribase: passive sampler andrecording system for theenvironmental parameters
required to calculate the activityof atmospheric tritium.

Characteristics of the molecular sieve
Quantity of molecular sieves
Maximum sampling capacity
Diameter, height
Operating time
Operating temperature
Relative humidity

180 g
30% by weight
94 and 111 mmfrom 24 hours to
30 days– 10 °C to 35 °C
30-100%© IRSN

Figure C shows the operating envelope for this passive
sampler, and highlights that sampling periods can range
from less than 1 day to over a month,with a decision threshold of 1 Bq/L (0.01 Bq/m3) for astandard liquid scintillation sample analysis. However, thisdevice can only be used to collect tritium in atmosphericwater vapour. Note: this form of tritium is the one directlytransferred to flora and fauna in the environment and is themain contributor to human exposure.
IRSN started using this device, which is easy to deploy andrelatively low-cost, for monitoring. No specific premises or power supply are required. When
combined with routine monitoring, this passive sampler is ideal for radiological mapping as partof reinforced local monitoring policies.

FIGURE C / OPERATING ENVELOPE OF THE PASSIVE TRITIUM SAMPLER

La Hague discharges
NPP discharges

Immediateenvironment
around the Valduc site
(2 - 300 TBq/year)
Immediateenvironment aroundthe NPP (1 - 7 TBq/year)
Natural backgroundradiation• For operational conditions withregular monitoring (DT: 1 -5 Bq/L)• Depends on relative humidity andbubbler performanceler )b b gas
u
B nd
Oa
H
( T

se r
en
d
n
Co (HTO)

1 hour

r ap
et
v
i
)
ss
Pa (HTO
1 day

1 weekSampling period

1 monthRADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /15

Rainwater
Atmospheric radionuclides are leached from theatmosphere by rain, and subsequently precipitatedon the ground. On this basis, rainwater is sampled
and analysed to complement atmosphericmonitoring. Collectors (see figure 6) continuously
collect water during rainy episodes and samples
are taken either weekly or monthly.
FIGURE 6 / RAINWATER COLLECTOR

16

Monitoring the aquatic environment
Water and total suspended solids
As the receiving environment for liquid discharges
from nuclear facilities and any potential input
from runoff, water acts as a direct vector ofcontamination for the aquatic environment. Water(fresh water, seawater) is monitored using various
sampling and analysis systems. The extent of themonitoring required will vary depending on theconditions at each site, particularly hydrogeologicalcharacteristics, background radiation and thepotential presence of radionuclides emitted in thepast. IRSN's Hydrotéléray network (see figure 7)
is set up on the 7 main rivers downstream fromall unclear facilities, and is designed to trigger
an alarm if the level of activity measured in theenvironment is likely to be the outcome of a largescale accidental discharge. Gamma spectrometry
measurements are taken at each station, andintegrated over two hours, giving an approximate
water flowrate of 5 m3/h. The measurements
taken give decision thresholds of approx. 0.5 to 1
Bq/L for 137Cs, 60Co and 131I. Data are automaticallyanalysed, stored and retransmitted to the IRSN
site control centre in Vésinet.

© P. Demail

FIGURE 7 / HYDROTÉLÉRAY STATION© DR

Rainwater is generally analysed to determine
tritium activity. Such analyses are frequently
carried out at the same time as determining grossalpha and total beta activity indexes (see footnote
on p. 11), or even as gamma spectrometry, as partof monitoring policies at nuclear sites.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

RADIOLOGICAL MONITORING OF THE ENVIRONMENT / 01
Radiological monitoring devices used for the environment / 1.2

Water is also monitored using water samplingsystems, which take semi-automatic water
samples (see figure 8). These systems can takecontinuous or sequential samples. Sampling andanalysis frequencies vary depending on the sites(daily to monthly). A settling tray is sometimes
added to this system to collect the suspended
solids in the water.

FIGURE 9 / AD HOC WATER SAMPLING
USING A HORIZONTAL KEMMERER SAMPLER

© DR

© DR

FIGURE 8 / WATER SAMPLING SYSTEM

Finally, many ad hoc (instantaneous) surface
water samples are taken throughout France
by all contributors, mainly using manual
equipment (see figure 9). These ad hoc samples
complement the semi-automatic samples.
To give one example, EDF must systematicallytake a river water sample during each dischargeof liquid effluents ("mid-discharge" sample),particularly to analyse tritium.
According to regulations, ground water mustalso be monitored by operators in the form of
ad hoc samples. The main aim is to check thatno effluents are directly discharged into theground water and to track any variation in former
radiological contamination, for example. Groundwater is pumped out using specially designed
structures: piezometers. Samples may be taken
on a monthly to annual basis.

The water samples taken are generally analysed
to determine tritium, gross alpha and gross beta
activity. These measurements are complemented
by determining uranium isotope levels or
quantifying content for specific radionuclides(gamma spectrometry, alpha spectrometry, etc.)
at some nuclear sites. Analytical procedures
can also be extremely extensive for watermeasurements. To give just one example, decisionthresholds for tritium vary between 2.5 and
10 Bq/L for most operators (background tritiumin fresh water with no discharges varies fromless than 1 to 3 Bq/L). Thresholds of less than
1 Bq/L can be reached as part as some appraisal
programmes using other sampling and analysis
techniques. By conducting tritium analyses onriver water samples taken downstream of nuclear
facilities, the potential exposure of local residents
to doses by ingestion can be quantified. Decisionthresholds for water measurements obtainedby gamma spectrometry vary between 0.0001
and 0.5 Bq/L in France according to the different
laboratories and set targets.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /17

Sediments

Aquatic fauna and floraRadionuclides with low solubility and a long
half-life can integrate sediments on a long-termbasis. For this reason, ad hoc sediment samples
are taken upstream and downstream of nuclear
facilities (see figure 10). Most samples taken
for monitoring programmes include surface
sediments and are intended to quantify any
radionuclides due to recent discharges.

Sampling runs are also completed alongsideof the monitoring of the aquatic environment
for products eaten by humans (fish, shellfish,
molluscs) and bio-markers (aquatic plants) inorder to assess the effects of these effluents fromthe facilities.

These samples are taken at frequencies between
monthly and five yearly. The sediment samples
taken are generally subjected to gamma
spectrometry and gross alpha and gross beta
activity analyses. Complementary analyses (alpha
spectrometry, tritium, 14C, 90Sr) are also carriedout depending on the specific spectrum of theeffluents discharged at each site. The analysis
methods used must ensure that the analyticalresults achieved meet the set targets (regulatory
monitoring, radio-ecological studies, etc.).

18

FIGURE 10 / AD HOC SEDIMENT SAMPLING
USING A BERTHOIS CONE

Radionuclides can accumulate in aquatic plants
and reach high concentration factors. Such factors
rapidly respond to variations in radionuclide
activity in the water and are considered as "frontline" markers. Fish samples are selected based onwhat they eat and mobility trends. Sedentary andgrass-eating species are preferred when possible.
In general, the minimum requirements ofregulations imply annual fish samples. However,some operators carry out radio-ecological studies
in addition to meeting regulatory requirements interms of monitoring. Ad hoc and recurrent (annual,
ten-year) sampling for these studies mainly focus
on key environmental matrices (algae, bryophytes
and aquatic phanerogams, fish, molluscs).
IRSN and other contributors to monitoring (ACRO,etc.) also run monthly, quarterly, six-monthly
and annual sampling campaigns for aquatic
sediments, fauna and flora at a series of fresh
water and seawater stations, specifically as partof their monitoring programmes for nuclear
facilities and in France in general. The results ofthe periodic radio-ecological studies focusing on
one or several regions (radiological observations)are combined with such regular monitoring.

© DR

Samples are generally taken upstream anddownstream of nuclear facilities (see figure 11)
in the continental aquatic environment. Samples
are taken in the immediate vicinity and further
away from facilities at sea. Sea stations arelocated in positions based on potential sourcesof discharges and likely dispersal routes at sea(currents, tides, etc.).

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

RADIOLOGICAL MONITORING OF THE ENVIRONMENT / 01
Radiological monitoring devices used for the environment / 1.2

Gamma spectrometry is systematically carriedout on these matrices to check for any radioactive
products (58Co, 60Co, 54Mn, 110mAg, etc.) and fission
products (131I, 129I, 137Cs, 106Ru, etc.). The spectrum of
the radionuclides analysed will depend on the liquid
effluents discharged from the facility monitored
and any other nearby facilities upstream or in thevicinity. Some monitoring contributors also focus
their strategy on analysing radionuclides with adominant effect on dosimetric impact (generally
14
C and 3H).

Additional measurements (90Sr, Pu, Am, U, 99Tc) aresometimes taken near to specific sites affected bythese radionuclides, either due to current liquid
discharges, or due to former radiological levels.
IRSN also monitors residual radioactivity fromfallout from atmospheric testing.

FIGURE 11 / SAMPLING AQUATIC PLANTS (creeping water primrose) IN THE VIENNE REGION DOWNSTREAM FROM THE
CIVAUX NPP

© DR

19

© DR

FIGURE 12 / FOOD SAMPLING

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Monitoring the terrestrial environment
Terrestrial plants and soils
Mosses, lichens, tree leaves and grass areused as bio-markers, indicating the presenceof radionuclides suspended in the air, due
to their ability to capture aerosols and dust
raised from the ground and suspended.
These bio-markers provide information on
short-term and long-term variation in radionuclide
activity in the environment, which food analyses
could not necessarily contribute.
Soils can integrate radionuclide deposits with asufficiently long half-life (a few years), which will
progressively migrate to deeper locations. It isfrequently difficult to estimate the contributionof a facility to soil activity due to the presence ofradionuclides from nuclear weapon atmospherictest fallout and the Chernobyl accident (particularly
137
Cs and 90Sr).

Grass samples (on a monthly or quarterly
basis), and topsoil samples (yearly sampling)
are taken at most nuclear sites. The analyses
performed on these samples will vary dependingon the radionuclides in the effluents discharged
from the facilities. Gamma spectrometry ispractically systematic. Gamma spectrometryis then occasionally complemented by 3H, 14C,
90
Sr, plutonium, americium uranium analyses.
Institutional monitoring (IRSN, DGCCRF)
networks also contribute to regular monitoring
programmes. Additional analyses on terrestrial
vegetation (tree leaves, mosses) and soils are also
carried out as part of specific, ad hoc or recurrent
radio-ecological studies.

© DR

20

Analysing water from Toulon bay/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

RADIOLOGICAL MONITORING OF THE ENVIRONMENT / 01
Radiological monitoring devices used for the environment / 1.2

Food: dairy products, meat, fruit and vegetables
Radionuclides (aerosols or gases) can settle
directly onto the leaves of terrestrial plants. Such
radionuclides reach the highest activity levels
recorded. Only part of the activity deposited
onto the leaves is transferred from the leaves tothe other parts of the plant (fruit, seeds, roots
or tubers). The percentage transferred varies
depending on the radionuclide.
Radionuclides mainly transfer to livestock when
the animals ingest contaminated food. The degreeof transfer to meat and dairy products (milk,eggs) will vary depending on the product and theradionuclide. However, the activity transferred will
systematically be less than, frequently significantly
less than, the activity in the plant.
Food analyses are therefore carried out as part ofmost monitoring programmes (run by operators,
institutions and associations), in order to confirm
monitoring data for the effluents discharged andhelp to estimate the doses absorbed by the public.
The main food samples taken by nuclear operators
include milk (see figure 13) and cereals. Food
samples (cereals, mushrooms, fruit, vegetables,
meat, honey, eggs, cider, wine, olive oil, etc.),
sampling intervals and types of analysis all vary
substantially depending on site locations andoperators.

IRSN regularly monitors food radioactivity
at departmental (French administrative
départements) level. A network of plant crop
(cereals, vegetables, fruit, mushrooms, etc.) andlivestock (milk, meat, game, fish) samplers was
deployed throughout France with contributions by
the local services of DGAL, DGCCRF and France
Agrimer. Finally, the radiological status of areas
which are not affected by discharges from nuclear
facilities is also determined using very low levelmeasurements taken during specific studies orradiological observations.
The measurements taken can be comparedwith those taken for terrestrial plants (gamma
spectrometry is performed on all samples,
occasionally for operators and more systematicallyfor institutions, for 3H, 14C, 90Sr, plutonium,
americium and uranium measurements). As isthe case for all samples taken for the purposesof the radiological monitoring of the environment,
the measuring performance levels adopted mustbe suitable for the set targets (regular facility
monitoring, radio-ecological studies, etc.) and canlead to variation in decision thresholds by a factor
of between 10 and 100 depending on the type ofanalysis used.

© P. Bourguignon/ANDRAFIGURE 13 / SAMPLING COW'S MILKRADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /21

Summary of the strategic criteria applied and the sampling and measuring devices
used to monitor the radiological properties of the different environmental
components
The following tables summarise the various methods used to monitor the atmosphere and aquatic andterrestrial environments, as well as the strategic criteria applied to the samples taken and in situ analyses.

TABLE 1 / THE ATMOSPHERE

The atmosphere
Air

Atmospheric aerosols

Strategic criteria applied to measurements
and sampling in this component

Continuous measurement sensors(ambient gamma dose rate)
The receiving environment for atmosphericdischarges.

Passive environmental dosimeters

The radioactive gases and particles in the air
are passed on to humans via external andinternal (if inhaled) exposure.

Continuous sampling systems for aerosols(with subsequent laboratory measurements)

Rainwater

Continuous measuring and/or samplingsystems for aerosols

Bubblers (3H, 14C), noble gas monitors (85Kr),
activated carbon cartridges (iodines)

Gas

22

Measuring and/or sampling systems

Wet aerosol deposition(which potentially includes radioactivity) as thecolumn of air passed through by the dropletsof rainwater is leached.

Rainwater collectors

TABLE 2 / TERRESTRIAL COMPONENT, INCLUDING FOOD

Terrestrial component and food

Strategic criteria applied to measurements
and sampling in this component

Mosses, lichens, tree leaves and grass are used
Terrestrial plants (grass, leaves, as bio-markers for atmospheric contamination,
mosses, etc.)
due to their ability to capture aerosols and dust
raised from the ground and suspended.

Measuring and/or sampling systems

Ad hoc (manual) sampling

Soils

Soils can integrate radionuclide deposits with asufficiently long half-life (a few years), which will
progressively migrate to deeper locations.
Soils can also contaminate vegetables, fruit andgrasses via their roots.

• Ad hoc sampling (manual)• On-site gamma spectrometry

Plants(cereals, vegetables,
fruit, wine, etc.)

Plants are contaminated when radionuclides
settle on aboveground parts or are absorbed bytheir roots.
Fauna eating contaminated plants can also be
contaminated.

Ad hoc (manual sampling or collection
by growers) samplingLivestock(milk, meat, eggs, etc.)

Radioactive feed will lead to the transfer ofradionuclides to products of animal origin,including milk, a significant vector forradionuclides (caesium, strontium, iodine, etc.).

Ad hoc (manual sampling or directcollection by growers or
slaughterhouses) sampling/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

RADIOLOGICAL MONITORING OF THE ENVIRONMENT / 01
Radiological monitoring devices used for the environment / 1.2

TABLE 3 / AQUATIC COMPONENTStrategic criteria applied to measurements andsampling in this component

Measuring and/or samplingsystems

Water

As the receiving environment for liquid discharges
from nuclear facilities and any potential input fromrunoff, water acts as a direct vector of contamination
for the aquatic environment.

• Continuous measuring andsampling systems(IRSN Hydrotéléray network)• Water sampling systems• Ad hoc sampling

Total Suspended Solids(TSS)

TSS are the main support base for radionuclides. TSS
are mobile and help to ensure the presence ofradionuclides on river banks, beaches and land after
flooding.

• Settling trays combined withwater sampling systems• Water samples are filtered in alaboratory

Sediments

Sediments can effectively integrate radionuclides anddesorb radionuclides from the aquatic environment.

Ad hoc (manual or mechanical)
sampling

Aquatic plants(algae, mosses,
phanerogams)

Aquatic plants can very effectively and rapidly fix someradionuclides.
Radionuclide activity by mass can be compared at
different locations thanks to the wide geographic
distribution of aquatic plants.
Some plants, such as marine algae, react rapidly tovariations in the radionuclide composition of water.

Ad hoc (manual) sampling

Molluscs

Both filter-feeding and grazing marine molluscs are
effective long-term bio-markers thanks to theirnutritional habits.

Ad hoc (manual sampling or directcollection by growers) sampling

Shellfish
Fish

Fish effectively integrate radionuclides thanks to theirposition at the end of the food chain.
Fish are also extremely popular with humans.
Thanks to the geographic distribution of the species
sampled, the activities by mass measured at different
sampling locations in France can be compared.

Ad hoc (fishing or direct collection
by professionals) sampling© DR

Aquatic component

IRSN's gamma spectrometry room at Orsay can be used to measure very low activity levels

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /23

1.3. FROM SAMPLING PLANS TO
MEASURING RESULTS
All of the analysis and sampling techniques
described below are used by RNM contributors as
per the relevant provisions of NF or ISO standards,
particularly NF EN ISO/IEC 17025.

Analysis and sampling plans
Regulatory monitoring of the environment ofbasic nuclear facilities is adapted to each type of
facility (nuclear powerplant, plant, laboratory).
Predefined plans dictate the analyses carried out
on each sample based on the effluent discharged(type of effluent, radionuclides and level of activity
discharged) and past events (previous incidents
and discharges). Analysis and sampling plans
are included in chapter 3, for each site, after a
description of the effluents discharged.

24

Preparing samples
Upon receipt at the laboratory, the samples areprocessed and packaged as necessary for theplanned radiological analyses. The initial phaseof radioactivity analysis on a sample taken fromthe environment involves preparing the sample.
This phase ranges from simply placing the sample
in a standardised container to more sophisticatedprocesses such as drying, calcination or freeze
drying to concentrate the sample (see figure 14).
In general, the different techniques used totreat the samples aim to concentrate as much
radioactivity as possible in the smallest possible
volume in order to detect radionuclides at low, orvery low, levels. In some cases, the sample starts
the concentration process from sampling thanks
to the specific systems used (e.g. aerosol samples,
TSS samples, etc.).
In most cases, only part of the sample is used
for analysis. The sample is homogenised prior
to testing to ensure that the partial sample
does not lead to biased or non-representative
measurements. Most parties involved in monitoringalso archive some of the samples analysed (filters,
soils and dried sediments, samples of dried or
calcinated fauna and flora), in view of potential
analyses in the future using complementary or
more advanced equipment.

Laboratory facilities are required in order toconcentrate the sample or extract the radionuclides
to be measured, to ensure the highest possible
quality levels for all or part of the phases involvedin characterising the radionuclides in a sample.

Radiological analyses
Determining the activity of a radionuclide (seechapter 4) in a sample involves estimating theamount of radiation emitted by measuring theradiation absorbed by a detector. The main
detection methods used are based on the factthat radiation will excite (transmit energy toatoms) and ionise (separate electrons from atoms)
the materials which absorb it. These temporary
effects of radiation are recorded by the detector
and amplified to allow for measurement. The
number of pulses per second absorbed by thedetector can then be compared with the radiation
emitted by the sample, and therefore its activity,
by considering the performance of the measuring
device. Several measuring techniques and devices
can be used, mainly depending on the large
differences in the distances potentially travelledby the different types of radiation (see chapter 4):• gamma spectrometry can be used to identify
the radionuclides and measure activity for most
gamma emitting radionuclides, in fresh, dried,or incinerated samples (137Cs, 134Cs, 60Co, 125Sb,
110m
Ag, 131I, 129I, 40K, 210Pb, etc.);• due to the very short distance travelled by thealpha radiation and the fact that the radiation
is absorbed by the sample itself (reducing
the amount of radiation leaving the sample,
which can then be measured), radiochemicaltreatment is required before the alpha emitting
radionuclides (plutonium, uranium, polonium,etc.) can be measured and counted, mainly byalpha spectrometry. The aim is to remove theradioactive atoms in question from the sample
by eliminating all or part of the surrounding
sample;/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

RADIOLOGICAL MONITORING OF THE ENVIRONMENT / 01
From sampling plans to measuring results / 1.3• radiochemistry is also required prior tomeasuring some beta emitters such as
strontium-90;

Tracers are used, or control sources with specificreferences in terms of activity, density and type,to ensure the quality of the measurements taken.

• finally, for radionuclides emitting beta particles
with very low energy levels, such as tritium or
carbon-14, the sample is placed in a solution andmixed directly with the liquid scintillator used todetect them.

© IRSNFIGURE 14 / THE MAIN PHASES OF A RADIOACTIVITY ANALYSIS ON ENVIRONMENTAL SAMPLES(from sampling to archiving)

2. Oven dry

3. Freeze dry

4. Crush andhomogenise

5. Calcinate

7.3. Detect gamma
radiation

8. Archive

25© IRSN

1. Take a grass sample

6. Radiochemistry

7.1. Detect alpharadiation

7.2. Detect beta
radiation

After samples have been taken in the field (1), they must be
rapidly packaged to avoid any modification to their properties
and then transported to the laboratory for various types oftreatments. The characteristics of the sample are recorded
upon arrival at the laboratory to ensure traceability throughout
processing.
The initial phase of radioactivity measurements for a sample
involves physically preparing the sample. This phase ranges
from simply placing the sample in a standardised container tomore sophisticated processes such as oven drying (2), freeze
drying (3), crushing (4) and calcination (5) to concentrate theradioactivity of the sample.

More intensive processes (6) are sometimes required in order
to concentrate the sample or extract the radionuclides to bemeasured. These processes generally concentrate or separate
the selected radionuclides.
After this phase, the samples are measured using various
types of counters depending on the selected radionuclides(7) (proportional alpha-beta counters, alpha counters withphotomultipliers, liquid scintillation counters, gamma
detectors, etc.). Samples are then archived (8).

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /1.4. DETAILS OF THE
PRESENTATION AND USE OF
MEASURING RESULTS FOR THE
2015-2017 RADIOLOGICALREPORT
Data sources and units

26

All of the data shown in this report in graphic ortable format were taken from monitoring resultsin the RNM database on 31 December 2017 andcover the period running from January 2015 to
December 2017. However, earlier data can beused to improve our understanding of variation
over time based on recurrent input. The data used
are also obtained from IRSN results for specificstudies, such as radiological observations orradio-ecological monitoring on behalf of nuclear
operators (EDF or Orano). Finally, the chapter onformer mining sites describes and comments on
the Potential Alpha Energy (PAE) measurement
results acquired by Orano at and near to thesesites. These data were considered to be sufficiently
pertinent and reliable to be included in this report,with the agreement of ASN and MSNR, despite thelack of current approval.

Table 4 shows the different types of measuring
results shown and used in this report, with units.
With carbon-14, if the activity added around afacility, at local level, is too low to be differentiatedfrom background radiation using activity
measurements by mass in Bq/kg fresh, specificactivity measurements in Bq/kg of carbon can beused to quantify the extra activity representing
a few percent of the background radiation (seechapter 2). The activity by mass corresponding to
the mean carbon content of the food tested canbe calculated using these specific added activities.
The conversion method used is described inchapter 8 of the appendices.
Three types of tritium analysis results forbiological matrices (food or biological indicators)
are used in this radiological report: total tritium
measurements as Bq/kg fresh, Organically-Bound
Tritium (OBT) measurements as Bq/kg fresh of
OBT or Bq/L of combustion water, and free tritium
activity (HTO) as Bq/kg fresh of free tritium or Bq/Lof drying water (see focus article in this chapter
pp. 29-31). The conversion ratios between the
different values and units are provided in chapter
8 of the appendices.

TABLE 4 / THE DIFFERENT TYPES OF MEASURING RESULTS SHOWN AND USED, WITH UNITS

Dose rates

Sv/h (sub-multiples: µSv/h and nSv/h)

Air activity

Bq/m3 (sub-multiples: mBq/m3 and µBq/m3)

Potential Alpha Energy

J/m3 (sub-multiple: nJ/m3)

Water (rain, rivers, seawater, etc.) activity

Bq/L (sub-multiple: mBq/L)

Soil activity

Bq/kg (sub-multiple: mBq/kg)

Activity levels for biological markers

Bq/kg (sub-multiple: mBq/kg)

Food activity

Bq/kg fresh (sub-multiple: mBq/kg fresh)
Bq/kg of carbon for carbon-14
Bq/L of combustion water for organically-bound tritium (OBT)
Bq/L of drying water for free tritium (HTO)/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

RADIOLOGICAL MONITORING OF THE ENVIRONMENT / 01
Details of the presentation and use of measuring results for the 2015-2017 radiological report / 1.4

Decision thresholds, insignificant
results, metrological uncertainties
and rounding
Even if the sample to be measured is notradioactive, radiological measuring devices canprovide measuring results for external radiation,
particularly the natural radiation (see chapter 2)
to which the detector is exposed, and backgroundnoise from the device itself. This metrologicalbackground radiation fluctuates. If the activityof the sample is very low, it is also difficult todifferentiate between the radiation added by
the sample and fluctuations in metrologicalbackground radiation. In some cases, themetrologist will decide that the measuring result
for the activity of the sample is insignificant(the activity measured cannot be definitively
attributed to the sample). In this case,the metrologist will declare that the activity ofthe sample is "below the decision threshold": ≤ DT.
On this basis, the decision threshold is thelowest value of a sample measurement when themetrologist can decide whether or not activity
exists. Note: the value of this decision threshold
only depends on the measuring device (ormetrological background radiation), rather than
the activity of the sample.
The activities of some radionuclides in theenvironment are very low, therefore the series ofmeasurement results frequently includes results
which are below the decision threshold. These
results are also qualified as "insignificant" results.
In this case, a "significant" result or "significant
measurement" refers to activity above the decisionthreshold.
Insignificant results are shown on the charts asvertical bars running from the x-axis to the DT.
"< DT" appears in the legend. Significant results
are shown as colour symbols as per the legend
provided (figure 15).
"Nm" in the table refers to a "not measured"parameter or radionuclide.
27

FIGURE 15 / EXAMPLE DIAGRAM USED TO DIFFERENTIATE BETWEEN LOWER AND UPPER MEASUREMENTS AT DECISIONTHRESHOLDS

Activity
10
8
6
4
2
0
Decision thresholds for non-significant measurements
Significant measurements (activity measurements)

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Activity cannot be precisely measured, mainly due
to fluctuating metrological background radiation.
A metrologist will systematically indicate themetrological uncertainty for analysis results. The
metrological uncertainty is, however, very low
compared with the uncertain representativenessof the sample with respect to the environmental
component sampled, which is additionallymuch more complex to determine. Just how
representative is a litre of water sampled at a
precise location of a river, or more precisely,of the river water over a day or a week? How
representative is the activity of a lettuce sampled
at a given location of average activity for lettuces inthe entire field? For this reason, and to avoid giving
the misleading impression that results are precise,the uncertainties indicated by the metrologist are
not shown on the charts and tables published inthis report.

A mean value is used as the statistical indicator forthis report, calculated using significant analysis
results (> DT) and insignificant analysis results(< DT) subject to the DT if specific conditions are
met. The reasons for selecting this indicator, themethod used and the different potential scenarios
are described in chapter 8 of the appendices.
Box plots are used in chapter 2 to show the rangeof activity levels recorded in the environment forthe different background radiation radionuclides.
The information shown in these box plots and its
specific meaning are described in chapter 8 of theappendices.

Results expressed as mean values are rounded totwo significant figures to reflect the uncertainty
for the data. If the third significant figure is
between 0 and 5, the second figure is rounded
down. If the third significant figure is between
5 and 9, the second figure is rounded up. For
example, if the result is equal to 23.12548 Bq/L,
a value of 23.1 Bq/L will be indicated.

© IRSN

28

Mean values and other statisticalindicators

Crushing and adjustment of the geometry of a dried grasssample/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

RADIOLOGICAL MONITORING OF THE ENVIRONMENT / 01
Details of the presentation and use of measuring results for the 2015-2017 radiological report / 1.4

FOCUS ARTICLEANALYSING ORGANICALLY-BOUND TRITIUM(OBT) IN SOLID AND LIQUID ENVIRONMENTAL
MATRICES (EXCLUDING WATER)

The following radionuclides co-exist in theorganic matter in environmental matrices:• free water tritium in the sample (dewatering
tritium, DT), in the form of HTO molecules;• Organically-Bound Tritium (OBT), replacinghydrogen atoms bound to atoms of organic matter.

The 1st stage of analysing OBT is to separate the tritium from the free water of the OBT in thematrix in question. Freeze drying is generally used for this purpose.
The OBT fraction can be separated into two parts: (i) exchangeable organically-bound tritium(E-OBT), where the tritium atoms are bound to nitrogen, oxygen or sulphur atoms with labile
bonds and (ii) the non-exchangeable organically-bound tritium (NE-OBT) where the tritium
atoms are bound to carbon atoms with covalent bonds. Only the OBT analysis is confirmed foranalytical purposes based on current knowledge.
OBT activity can be measured by:
1. tritium measurement in water obtained by liquid scintillation analysis;
2. calculation after measuring helium 3 (the daughter of tritium) using mass spectrometry
1. Tritium measurement in water obtained by liquid scintillation analysis

29

Dehydrated samples are subjected to combustion to remove the hydrogen from the organic matteras H2O.
Various combustion systems exist:• automated combustion with a flow of oxygen (Oxidiser type combustion);• combustion in a contained system with pressurised oxygen (Parr pump type combustion);• combustion with a flow of oxygen in a tube furnace (Pyroxidiser type combustion)
The tritiated water vapour obtained from the combustion gases is collected after the combustion
phase, in the form of water, using a cold trap. This water is then analysed by liquid scintillation (LS).
Oxidisers and tube furnaces are the most frequently used systems in French laboratories.
2. Calculation after measuring helium 3 (the daughter of tritium) using mass spectrometry
The dehydrated samples are placed in isolation containers (glass tanks, metal pots) with the lowest
possible helium leakage rate once closed.
The containers are then placed on a vacuum degassing line (P < 10-5 Torr).
This degassing process must eliminate all dissolved gases in the sample, particularly helium. It
effectively "resets" the helium before closing the container.
After degassing, the containers are closed, sealed and stored prior to measuring.

●●●

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /●●●Isolating the samples allows the tritium to decay to helium-3. The isolation period (t) is
determined based on the mass of the sample, the expected tritium activity and target uncertainty
and generally lasts for a few weeks to a few months.
After the storage period, the containers are placed on a feeder line for a mass spectrometer
specifically designed to measure noble gases (static operation).
As the number of helium-3 atoms produced in the sample during the isolation period can be
determined by mass spectrometry, the number of tritium atoms initially present and therefore thetritium activity of the sample at the start of storage can be calculated.
Figure A shows the different OBT analysis techniques.

FIGURE A / THE DIFFERENT OBT ANALYSIS TECHNIQUES(pe = mass of the dehydrated sample)

Fresh sample

30

Dehydration water

Dehydration (freeze drying)

Analysis of Organically-Bound
Tritium (OBT)

Dehydrated sample

Combustion in an
automated device

Degassing in a
vacuumLeaktight closure

Combustion in atubular furnace(Oxidiser)

Storage pending
decay to 3He
Combustion water

Combustion watergas
Distillation

Liquid scintillation
measurement

Liquid scintillation
measurement

OBT Bq kg dry-1

OBT Bq L-1 of combustionwater

Mass spectrometry
measurement

OBT Bq kg dry-1●●●/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

RADIOLOGICAL MONITORING OF THE ENVIRONMENT / 01
Details of the presentation and use of measuring results for the 2015-2017 radiological report / 1.4●●●

The selected analysis technique will depend on many factors, such as the type of matrix, the massof the available dehydrated sample, the purpose of the measurement in terms of response timeand analytical performances (decision threshold, uncertainty).
For example, for a matrix containing 80% water and 6.2% hydrogen (plant matrix), table A lists
the results generally achieved by laboratories for the different techniques.

TABLE A / LIMITATIONS AND RESULTS FOR THE DIFFERENT PREPARATION METHODS

Automatic combustion
system (oxidiser)3
He mass
spectrometry

Tube furnace

Mass of a fresh sample

2.5 g

100 g

500 g

Mass of a dehydrated
sample

0.5 g

20 g

100 g

Mass of the combustion
water counted

0.25 g*

10 g-

Detection performance

30 - 40% tritium window
1-2 mL water/
10 mL scintillator

20 - 25 % tritium window
10 mL water/
10 mL scintillator-

Duration of counting

120 min

120 min-

Isolation period (decay to
3
He)

-

-

5 months

50 Bq/kg of dry matter

5 Bq/L of
combustion water
2.5 Bq/kg of dry matter

0.025 Bq/kg ofdry matter
0.05 Bq/L of
combustion water

Decision threshold*T his mass is not measured experimentally in automatic mode.

Results will be obtained (see figure A) either in Bq/kg dry, or Bq/L of combustion water
depending on the selected operating procedure. The percentage by mass of hydrogen measured in
the dehydrated sample can be used to convert the result into the other unit.
Recommendations
Isotopic exchanges with water vapour in ambient air should be limited during the different phasesof OBT analysis (preparation, storage, aliquoting, conservation, handling, treatments) due to thephysical and chemical properties of hydrogen isotopes. In particular, all sample handling phases
must be carried out in a suitable location and as rapidly as possible.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /31

FOCUS ARTICLEANALYSING CARBON-14 IN
ENVIRONMENTAL MATRICESCONTAINING CARBON

Carbon-14 can be found in the air, mainly as
carbon dioxide (CO2).
The properties and transfer of carbon-14 are an
indissociable part of the carbon cycle. Carbon-14
is incorporated into organic matter in plants
during photosynthesis, and subsequently into thefauna eating the plants. Just like stable carbon, carbon-14 is a component of organic matter.
Carbon-14 activity in environmental matrices can be determined using:
1. Liquid Scintillation (LS);
2. Accelerator Mass Spectrometry (AMS).
The sample must be dehydrated prior to analysis for all measuring techniques. Freeze drying is
generally used for this purpose. The carbon (including carbon-14) contained in the carbon
dioxide sample must then be converted by combustion or oxidation.
Various combustion systems exist, e.g.
• combustion in a contained system with pressurised oxygen (Parr pump type combustion);• automated combustion with a flow of oxygen (Oxidiser type combustion);• combustion with a flow of oxygen in a tube furnace (Pyroxidiser type combustion)
32

With liquid scintillation analysis, the carbon dioxide obtained is:• either trapped in a specific CO2 absorber, such as Carbosorb®E, before liquid scintillator isadded;• or chemically converted into an organic form which can be mixed with the liquid scintillator(benzene synthesis method).
After the CO2 has been routed to and trapped in cold traps, benzene is synthesised in thefollowing phases:
1. carbide production (750 °C): 2 CO2 + 10 Li → Li2C2 + 4 Li2O;
2. hydrolysis of lithium carbide: Li2C2 + H2O → C2H2 + Li2O;
3. trimerisation of acetylene into benzene (Cr catalyst): 3 C2H2 → C6H6.
Butyl PBD (2-(4’-t-butylphenyl)-5-(4-biphenylyl)-1,3,4-oxadiazole) and bis-MSB (1.4-bis-(2methylstyryl)-benzene) scintillators are added to the synthetic benzene for measurement
purposes.
If AMS is used, after the carbon dioxide is combusted and collected, a graphite source is obtainedby catalytically reducing CO2 using H2, with iron powder as a catalyst. This reaction occurs at
600°C with excess H2 (H2/CO2 = 2.5). The resulting carbon-iron powder is compressed into apellet for measurement purposes.
The selected analysis technique will depend on many factors, such as the type of matrix, the massof the available dehydrated sample or the purpose of the measurement in terms of analytical
performances, and response times (see table A on the next page). Parr pump analysis techniques
are suitable for matrices containing at least 10% carbon, which is enough to trap a sufficientamount of CO2 for the rest of the analysis. On this basis, only AMS is feasible for sediments (dueto the very low percentage by mass of carbon).

●●●/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

RADIOLOGICAL MONITORING OF THE ENVIRONMENT / 01
Details of the presentation and use of measuring results for the 2015-2017 radiological report / 1.4●●●

Figure A shows the different carbon-14 analysis techniques.
FIGURE A / THE DIFFERENT 14C ANALYSIS TECHNIQUES(pe = mass of the dehydrated sample)

Dehydration (freeze drying)Fresh sample

14

Dehydrated sample

C analysis

Combustion
Automated device(Oxidiser)

Parr pumpParr pumpSpecific combustion

CO2 obtained
CO2 trapped in a
specific absorbent
material

CO2 trapped in a
specific absorbent
material

Benzene synthesis

Catalytic reduction using H2
Artemis AMS

33
Mass spectrometry
measurement

Liquid scintillation measurement

14

C Bq kg-1 exc.

14

C Bq kg-1 exc.

14

C Bq kg-1 of C

14

C Bq kg-1 of C

Results will be obtained (see figure A) either in Bq/kg of dry sample, or Bq/kg of carbon (seechapter 2) depending on the selected operating procedure. The percentage by mass of carbon
measured in the dehydrated sample can be used to convert the result into the other unit.
The performance of the different available tools for 14C analysis, in terms of detection limits, is notcritical as the activity levels measured are systematically significant. In fact, background radiation(excluding the direct impact of effluents discharged) is currently approximately 227 Bq/kg C.
Results will mainly be compared based on the associated uncertainty (table A).
TABLE A / ANALYTICAL PERFORMANCE LEVELS FOR THE DIFFERENT PREPARATION METHODS

Automatic combustion
system (oxidiser)

Benzenesynthesis

AMS

Associated uncertainty as a %(with a coverage factor k = 2) for
activity of 227 Bq/kg C

20

6

2.5

Duration of the analysis (days)

1

5

4

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /1.5. THE RNM (RÉSEAUNATIONAL DE MESURES /FRENCH METROLOGICALNETWORK) FOR
ENVIRONMENTAL
RADIOACTIVITY• by any public or private organisation, or
any association contributing to radiologicalmonitoring in France.

The reference site for environmental
radioactivity measurements in France

www.mesure-radioactivite.fr can be used to track
variation in the radiological composition of a
specific environmental component over time and tocompare the measurements provided by different
contributors. Measurements can be comparedthanks to the use of strict and homogeneous
measuring methods and data harmonisation
criteria such as measurement units.

The French metrological network for environmental
radioactivity centralises all approved monitoringdata for environmental radioactivity in France.
An approval procedure is applied to ensure data
quality and harmonisation.
One of the strengths of this approach is the manysources of available information: measurements
are provided by Government services and publicsites, nuclear operators and other public & privateorganisations or associations.
34

Since 2010, www.mesure-radioactivite.fr
has published the 300,000 measurements taken in
France each year (representing a total of slightly
over 2 million data items in 2017) for the different
environmental components (air, water, soil, faunaand flora) and food products to ensure 100%transparent access for all.
The www.mesure-radioactivite.fr initiative is
unique in Europe and allows just anybody tounderstand how the radioactivity in their area ismonitored.
Centralisation
The environment is currently extensively
monitored by a large number of contributors,
focusing on various aspects, as part of the French
nuclear segment. The environmental radioactivity
data forwarded to the RNM include the results of
the analyses conducted:• by nuclear operators monitoring the radiologicalcomposition of the immediate environment of
their facility as per regulatory requirements;• by public authorities, Government services andpublic sites in charge of health safety checks forfood and water;

The French metrological network collects andcentralises these data from various sources via aunique database.
Harmonisation

All measurements to be added to the RNM
database must be carried out by laboratories
approved by the ASN (Autorité de sûreté nucléaire
- French Nuclear Safety Authority). This approval
is issued based on the opinion of a multi-party
approval committee.
Reliability
Laboratories must meet two combined conditions
to guarantee the reliability of measurements:• comply with International standard ISO/IEC
17025, establishing the general requirements
in terms of the skills needed for testing and/or
calibration, including sampling;• obtain results able to satisfy the comparativeinter-laboratory tests organised by IRSN. With
these expertise tests, the results obtained by
the laboratories based on identical samples arecompared with a control value.
Presentation
The www.mesure-radioactivite.fr site allows justanybody to understand how the radioactivity intheir area is monitored.
The site was fully revamped in 2016 in order tobetter meet the expectations of the general publicby providing a "guided" user mode, as well as the"advanced" user mode intended for well-informed
users.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

RADIOLOGICAL MONITORING OF THE ENVIRONMENT / 01
The RNM (Réseau National de Mesures) for environmental radioactivity / 1.5

The site has also been available in English since
early 2018 to allow non-French-speaking users toaccess content.

RNM operations
The French network was set up under the aegis
of ASN (French nuclear safety authority). IRSN
(French national institute of radiation protection
and nuclear safety) manages the network.
Other system contributors include representativesof the main Ministries involved, health agencies,
public institutes, the nuclear industry, qualified
individuals and consumer and environmental
protection associations.

Transmitting measuring results to the RNM
Most French contributors to the radiologicalmonitoring of the environment upload theirmeasurements to the RNM.
All contributors send their data formatted
according to a jointly-defined informationexchange protocol via the internet using a securetransfer system. To date, 66 contributors upload
environmental radioactivity measurements to the
French network.
These measurements have been entered into thecentral database of the RNM since its launch in
January 2009. 25,000 measurements are uploaded
each month on average.

RNM committees

Using and presenting RNM data

The French network is led by a management
committee, which is chaired by ASN, and entrustedwith defining strategic guidelines for the network.
An approval committee also issues an opinion on
applications submitted by laboratories for ASN
approval. The different RNM contributors are
represented within these two bodies.

The data centralised in the RNM information
system are presented to the public andexperts in the form of a map-based web
p o r ta l
( w w w. m e s u re - ra d i o a c t i v i te . f r ) .
A radiological report on the status of theenvironment is released every 3 years using thisdata and input analysis. This report is the second
radiological report to be released. The first report
was published in 2015 and covered the June 2011December 2014 period.

The Management committee meets twice annually.
Management committee meeting reports can beaccessed under the "Publications" section. The
Management committee will issue its opinions on
strategic guidelines for the RNM. The committee is
supported by working group input when necessary.
The working groups are set up as required to study
RNM upgrades.
The approval committee is responsible for
ensuring that the measuring laboratories hold thenecessary organisational and technical expertiseto provide quality measurements to the network.
The committee can suggest that ASN propose orrefuse, withdraw or suspend approval. ASN willthen decide whether or not to issue or refuse
approval. This decision will be published in ASN's
Official bulletin.
IRSN (French national institute of radiation
protection and nuclear safety) manages thenational metrological network (RNM), as well as
overseeing its development, technical operations
and general organisation.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /35

FIGURE 16 / RNM ORGANISATION

Chairs the management committee and the approvalcommittee.
Runs the secretariat of the approval committee.

Runs the secretariat of the management committee.
Organises comparative inter-laboratory tests.
Manages and upgrades the Information system andwebsite.

Legend:Represented on the
management committee

Represented on the approval committee

GOVERNMENT SERVICESHEALTH(DGS)
ENVIRONMENT(DGPR)
CONSUMPTION(DGCCRF - SCL)AGRICULTURE(DGAL)

36

DEFENCE(EMM - SPRA)ANSES
FRENCH PUBLIC HEALTH
ARS
IRSN
ASN
(DIVISIONS)DEPARTMENTAL LABORATORIESOPERATORS(FRENCH NAVY)&/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

RNM contributor

RADIOLOGICAL MONITORING OF THE ENVIRONMENT / 01
The RNM (Réseau National de Mesures) for environmental radioactivity / 1.5

RNM FOCUS ARTICLE
AN ALL-NEW WEBSITE,NOW TRANSLATED INTO ENGLISH

The RNM website was totally revamped
towards the end of 2016. The main aim
was to make it more approachable forthe general public. The "guided user
mode" version provides basic
information on the number and type ofmeasurements: e.g. the measurements
taken near to the location of the RNM
user (geolocation function).

The RNM is continuing to open its activities up
to a wider public: after modernising the website
in 2016 to ensure easier access for the "generalpublic", non-French-speaking experts should
appreciate the English translation.

FIGURE A / THE GUIDED USER MODE FOR THE NEW
VERSION OF THE WEBSITE

A second level is available fornon-specialist users, simply providing
access to around a dozen or so of thehundreds of available types of measuring
results. These results are preselected toprovide both a representative overview
and in-depth analysis, hence the term
"Landmark".

RNM "Landmark" results
Maximum values and the extent ofbackground radiation (values measured
in the surrounding environment) areindicated for these "Landmarks" as well
as specific items of information(via a "did you know?" section).

37

FIGURE B / "LANDMARKS" FOR THE NORTH COTENTIN
SITES

The selected Landmarks are considered
to be representative of radioactivity
measurements throughout France(e.g. the ambient gamma dose rate or
caesium 137 measurement in aerosols)
or of one or several specific nuclear
facilities (e.g. iodine-129 measurements
in milk, which mainly affects the
La Hague facility, or tritium
measurements in dairy products
reflecting tritium discharged from the
Marcoule and Valduc facilties).
A "thermometer" is displayed for each selected Landmark measurement and reflects backgroundradiation in France●●●

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /●●●(radioactivity excluding the impact of nuclear facilities)
and the maximum value measured in France with an
explanation describing the context and providing users
with the details they need to understand why this value wasmeasured.

FIGURE C / CONTEXT-BASEDEXPLANATIONS FOR THE CESIUM-137
CONTROL DATA

The "expert" version shows all measurements published on
the site in the form of time-series for recurrent data.

An English site to allow non-French-speaking users toaccess information in the RNM database.

38

The website was also modernised in order to expand its
potential audience to non-French-speaking users:
translating the site into English appeared the natural
solution, opening up the 2.2 million data items currently
available via the site to the English-speaking scientificcommunity. An increase in users in foreign countries was
detected via an in-depth analysis of the locations of users
logging in during "radiological events" (such as when 106Ru
was detected from the south Urals in the autumn of 2017). Launching an English version of thewebsite will cover this underlying
requirement for information in foreigncountries.
FIGURE D / ENGLISH VERSION OF THE WEBSITE/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

RADIOLOGICAL MONITORING OF THE ENVIRONMENT / 01
The RNM (Réseau National de Mesures) for environmental radioactivity / 1.5

Laboratory approval processes
Laboratory approvals for environmental
radioactivity measurements as per article R. 133326 of the French public health code are issued in
the form of an ASN decision.
Laboratories must meet therequirements prior to approval:

following• submit an approval application to ASN listing
the requested types of approval and provingthat their measuring and sampling techniques
satisfy the requirements of standard NF EN ISO/IEC 17025 as applicable to test laboratories;• satisfy the comparative inter-laboratory tests
organised by IRSN on a regular basis.
Approvals are issued based on an ASN decision,
with reference to the opinion of the laboratory
approval committee, released after considering
the approval applications and the results obtainedby the laboratories in the comparative interlaboratory tests organised by IRSN. Approvals
are granted with a maximum validity period offive years.
Over sixty laboratories, including one foreignlaboratory, have applied for approval forenvironmental radioactivity measurements since
2003.
The following types of laboratories are approved
as part of the RNM:
• laboratories run by nuclear operators, whichmonitor the environment of the nuclear facilities
in application of the regulations in force;• laboratories run by government institutes oragencies, which measure radioactivity for healthsafety purposes;• university laboratories, which can measureradioactivity on behalf of nuclear operators
or public authorities (health safety testing for
drinking water);• private laboratories, which mainly invest inradiological testing for drinking water;• laboratories run by environmental protection
associations, which take their own independentmeasurements and provide a second opinion for
their own benefit or that of public authorities;• foreign laboratories, generally government
laboratories working in sectors aiming to protect
public health.
Just what are comparative inter-laboratory
tests?
The comparative inter-laboratory tests organised
by IRSN are intended to prove the technicalexpertise of the laboratories. With these expertise
tests, the results obtained by the laboratories
based on identical samples are compared with acontrol value.
These tests involving measuring artificial alpha-,beta- and gamma-emitting radionuclides, orradionuclides from natural uranium and thorium
chains. IRSN is responsible for preparing thesamples, delivering them to the laboratories
registered for testing, determining the control
values and processing the results obtained by thelaboratories for statistical purposes.
The samples prepared by IRSN are distributed
to the laboratories involved simultaneously inview of parallel measurements. The batch ofsamples provided by IRSN must be sufficiently
homogeneous in terms of radioactive content
to ensure that results will not differ due to aheterogeneous sample.
Up to 70 laboratories can participate in each test,
including a few foreign laboratories.
IRSN has organised this type of testing for thelast 40 years and currently sets up 4 to 5 test runs
each year as part of the RNM. The IRSN laboratoryorganising these tests has held COFRAC (Frenchaccreditation body) accreditation since 2006.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /39

Overview of approved laboratories as at
1 January 2018

The different types of tests proposed as part of the
RNM are scheduled for each type of environmental
matrix and radioactivity measurement category
based on the laboratory approval table definedin appendix to approved and amended ASN
decision no. 2008-DC-0099 of 29 April 2008, on
the organisation of the RNM for environmental
radioactivity, which also defines the laboratory
approval procedure.

58 laboratories had been approved for measuring
environmental radioactivity on 1 January
2018, including 40 laboratories run by nuclear
operators. The other 18 laboratories are run byprivate operators (6), universities (6), institutions(3) and associations (3). These laboratories hold atotal of 880 approvals in 51 approval categories.
Since the launch of a new type of approval for
gamma-emitting measurements in food as partof health safety tests in 2015, six laboratories (preselected by DGAL and DGCCRF) have applied for
ASN approval in order to contribute to the RNM.
This equivalence will allow these laboratories to
upload food data to the RNM.

Environmental matrices:• 7 groups are defined: water, soil, biologicalmatrices, aerosols, gases, the ambientenvironment and food;• 17 radioactivity measurement categories.
Comparative inter-laboratory tests allow thelaboratories involved to prove the quality of theanalysis techniques used, provide accreditation
bodies with information indicating their level ofexpertise in the analysis process and obtain ASN
approval as per regulations.

Most laboratories are approved for monitoringwater radioactivity with 57 laboratories holding up
to 13 different water monitoring approvals each(see figure 17).

40

FIGURE 17 / LABORATORY BREAKDOWN (including IRSN)

Number of approved laboratories
60

57

50
40

45
36
31

30

0

36

37

34

31
21

20
10

44

40

17
7

2

5 6
1 2

4 3
1 2

Water

Soils

Biological

44

5

6

5

3
1 0

0

Aerosols /filter

21

2

001

Gas /
air

Ambient
environment

University

Association

6

00 00

Food

Type of matrix
Operator

PrivateInstitution/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

Total

RADIOLOGICAL MONITORING OF THE ENVIRONMENT / 01
The RNM (Réseau National de Mesures) for environmental radioactivity / 1.5

Around fourty laboratories hold approval forbiological matrix (food chain), atmospheric dust, airor ambient gamma dosimetry measurements. 31
laboratories are approved for soil measurements.
While most laboratories are able to measure
gamma emitters in all environmental matrices,
only around a dozen laboratories are approved
to measure carbon-14, transuranic elements orradionuclides from natural uranium or thorium
chains in water, soil and biological matrices.

CILEI - IRSN's comparative inter-laboratoryenvironmental testing website
IRSN has launched a website exclusively for the
purpose of exchanging information between
laboratories involved in IRSN's inter-laboratory
tests for measuring radioactivity in the environment
and food: https://cilei.irsn.fr/© F. Levillain/Signatures/IRSN

41

Helium-3 degassing bench for seawater tritium measurements

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FOCUS ARTICLEFEEDBACK ON COMPARATIVEINTER-LABORATORY TESTING AS PARTOF THE LABORATORY APPROVAL PROCESSThe comparative inter-laboratory testingorganised by IRSN as part of the French
metrological network for environmental
radioactivity is intended to appraise the quality
and reliability of the measurements taken by thevarious laboratories involved.
With these expertise tests, the results obtained by
the laboratories based on identical samples are generally compared with a control value. IRSN is
responsible for preparing samples, determining control values and using results for these tests,
which are open to both French and foreign laboratories.
Initial comparative inter-laboratory tests were organised by IRSN in April 2003 based on the first
regulatory texts governing the monitoring of environmental radioactivity (decree no. 88-715 of 9
May 1988 on harmonising radioactivity measurements for the environment and food intended for
consumption, article R. 43-6 of the French public health code, amended by decree 2002-460 andthe order of 17 October 2003 on the organisation of a French metrological network forenvironmental radioactivity).
The laboratory approval committee, established by the order of 17 October 2003, met for the firsttime on 7 January 2004, and issued positive opinions on 29 approval applications. Approvals are
granted with a validity period of 5 years.

42

ASN decision no. 2008-DC-0099 of 29 April 2008 describes the organisation of the French
metrological network for environmental radioactivity and defines laboratory approval procedures.
This decision was amended by ASN decision no. 2015-DC-0500 of 26 February 2015, introducing
a new type of approval designed to allow laboratories approved by DGAL and DGCCRF to upload
their food measuring results obtained as part of health safety tests to the database of the French
metrological network (RNM) for environmental radioactivity.
Participating in comparative inter-laboratory tests (ILT) meets both the general requirements
specified in standard NF EN ISO/IEC 17025 on the expertise of testing and calibrationlaboratories and regulations requiring laboratories to submit the results of ILT when applying for
approval.
If the ILT results of a laboratory are not sufficiently conclusive, ASN may issue provisional
approval for a one- or two-year period, for example, or require additional elements asprerequisites for approval, potentially including further multi-party tests, based on the opinion of
the approval committee.
The number of ILT required each year has gradually increased since 2003 to cover the entire range
of approvals. IRSN organises 6 ILT each year on average, spread over two semesters. The
laboratory approval committee has met twice annually since 2010 in order to appraise the ILT
results of laboratories and issue an opinion to ASN on the applications for approval submitted by
the laboratories.
IRSN organised 70 ILT between 2004 and 2017, and on 1 January 2018, ASN had issued 880
current approvals to 64 laboratories.

●●●/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

RADIOLOGICAL MONITORING OF THE ENVIRONMENT / 01
The RNM (Réseau National de Mesures) for environmental radioactivity / 1.5●●●

The following table itemises the number of approvals granted to laboratories for each matrix andper year since ILT were introduced.
Starting
year forvalidity

Water

2004

24

2005

76

2006

58

2007

26

2008

17

2009

151

Soils andsediments

Biologicalmatrices

Aerosols

Air

Ambient
gamma
dose rate

Food

5
40
53

26
4

40
2
16

65

8

18

35

20
1

2010

62

73

18

17

1

2011

24

57

1

70

1

1

2012

14

8

25

2013

13

12

38

2014

119

1

74

25

2015

87

77

15

26

2016

76

60

2017

25

12

49
14
42

71
27

7

40
5

52

6

43

According to feedback, the 5-year intervals adopted for each type of ILT, matching the validity of
the corresponding approvals, are satisfactory. It would not be appropriate to extend this period as
it would not leave enough time to appraise the ability of the laboratories to maintain theirperformance levels over time based on personnel turnover, structural changes, or new standards
and measuring methods likely to occur during the validity period for the approval.
Since the initial ILT, ASN and IRSN have taken note of the improvements for approved laboratory
teams: the percentage of satisfactory ILT results has generally increased over time, meaning thatthe number of two-party tests organised by teams has decreased in relative terms. In fact, each of
the 29 two-party testing sessions organised between 2004 and 2012 included up to 4 laboratories.
Most of the 16 two-party testing sessions organised between 2013 and 2017 only included one or
two laboratories. The number of provisional approvals granted for one or two years, requiring
two-party testing or the submission of additional elements to the approval committee, also
decreased between 2004 and 2017.
On this basis, since 2003, ASN has considered that the organisation of comparativeinter-laboratory testing by IRSN is an effective, reliable and well-tested system which indeed
appraises the quality and reliability of the measurements taken by the various laboratories
involved. ILT helps to improve the expertise of laboratories and maintain their performancelevels over time, guaranteeing the quality of the environmental radioactivity measurements
published on the website of the French metrology network for environmental radioactivity:
www.mesure-radioactivite.fr.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Carbon-14 measurement bench based on benzene synthesis© A. Bouissou/MEDDE/IRSN

44/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

O2
BACKGROUND RADIATIONIN FRANCE

2.1. N ATURAL BACKGROUND RADIATION. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .  46
Cosmic radiation and cosmogenic radionuclides in the environment . . . . 46
Telluric radionuclides in the environment . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 48
2.2. B ACKGROUND RADIATION FROM OLD FALLOUT. . . . . . . . . . . . . . . . . . . . . . . .  61
Fallout from the atmospheric testing of nuclear weapons. . . . . . . . . . . . . . . . . . 61
Fallout from the Chernobyl accident. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 64
Fallout from the Fukushima accident. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 64
2.3. R ANGE OF POPULATION EXPOSURE LEVELS DUETO BACKGROUND RADIATION IN FRANCE. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .  66
Effective external doses due to cosmic and telluric radiation . . . . . . . . . . . . . 66
Effective doses received by ingesting natural radionuclides
via food or smoking . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 66
Effective dose received by inhaling radon. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 68
Effective doses due to residual radioactivity fromold fallout comprising artificial radionuclides . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 69
Report on effective doses received due
to background radiation in France . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 73

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /

45

O2

BACKGROUND RADIATIONIN FRANCE

46

Background radiation refers to the activities ofthe different radionuclides in the environment,
excluding any current anthropic contributions(nuclear industry, other industries, hospital waste,etc.). This background radiation is partially emitted
by natural sources, and partially residual fallout
comprising artificial radionuclides affecting allof France. This fallout is mainly the result of theatmospheric testing of nuclear weapons and theChernobyl accident. Residents are also exposed tothis background radiation. This chapter describes
natural background radiation (2.1) and artificial
background radiation (2.2), and details the inherent
radiological exposure faced by residents (2.3).

2.1. NATURAL BACKGROUNDRADIATION
Two sources of natural background radiation exist:
telluric radionuclides, which have been present
on Earth since it formed, and cosmic radiation,
which is permanently emitted by cosmogenic
radionuclides.

Cosmic radiation and cosmogenic
radionuclides in the environment
Cosmic radiation reaches our planet from thesun and space (other stars and galaxies). Cosmic
radiation mainly consists of protons. These protons
interact with atoms in the upper atmosphere, whichleads to "secondary" cosmic radiation comprising
electrons, protons, photons, neutrons, etc., andto the production of "cosmogenic" radionuclides
such as, primarily, tritium (3H), carbon-14 (14C),
beryllium-7 (7Be) and sodium-22 (22Na).

Variation in cosmic radiation
Cosmic radiation is attenuated by the thicknessof the atmosphere, which shields our planet. On
this basis, the dose rate from cosmic radiation
increases with altitude. Figures 1 and 2 highlight
this point.
Cosmic radiation also varies with latitude, but to alesser extent. This variation is due to the fact thatthe atmosphere is thicker near to the equator (15- 17 km) than at the poles (7 km).
Cosmogenic tritium
Tritium (3H) is the radioactive isotope of hydrogen.
Tritium is produced naturally when cosmic
radiation interacts with nitrogen, oxygen andargon atoms in the upper atmosphere. Tritium,
just like all hydrogen atoms, is a component ofwater molecules and organic matter. Tritium isknown as HTO in the form of water (tritiated water)
and as OBT (Organically-Bound Tritium) when partof organic matter (see focus article on pp. 29-31).
Tritium activity is often stated in Bq/L,
for free river water, water vapour in the air,water extracted from organic matter by drying
or water extracted from a sample by combustion(see focus article on tritium measurements inchapter 1). Natural tritium activity represents
approximately 0.1 - 0.6 Bq/L, which corresponds
to activity levels of approximately 0.001 - 0.006
Bq/m3 in air and 0.1 - 0.6 Bq/kg fresh in flora andfauna.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

BACKGROUND RADIATION IN FRANCE / 02
Natural background radiation / 2.1

FIGURE 1 / MAP OF THE AIRBORNE DOSE RATE INDUCEDBY COSMIC RADIATION (µSv/h)

FIGURE 2 / VARIATION IN DOSE RATE WITH ALTITUDE(µSv/h)Hourly doserate

Sea level

Current tritium activity measured in theenvironment systematically exceeds these values.
In fact, this natural tritium must be added to theresidual tritium from fallout from the atmospherictesting of nuclear weapons in the northernhemisphere between 1945 and 1980, primarily
between 1953 and 1963 (see chapter 2.2 on fallout
from nuclear tests).
Cosmogenic carbon-14
Carbon-14 is produced naturally when cosmic
radiation interacts with nitrogen atoms in the upper
atmosphere. Just like stable carbon, carbon-14 is acomponent of organic matter. Carbon-14 is mainly© Chromatiques

47

µSv/h
  0.037-0.050  0.051-0.080  0.081-0.120  0.121-0.220

present in the air as CO2 and is incorporated intoplants during photosynthesis, and subsequently
transferred into the fauna eating the plants.
The activity of this cosmogenic carbon-14
radionuclide is stated per stable carbon massunit and known as "specific activity". This value
was approximately 226 Bq/kg of stable carbon in
air and all terrestrial environmental components
prior to the start of nuclear testing (1945).
Large quantities of both tritium and carbon-14
were produced during the atmospheric testing of
nuclear weapons in the northern hemisphere. Dueto these tests, current environmental radioactivity
is still slightly above this value (see chapter 2.2 on
fallout from nuclear tests).

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Telluric radionuclides
in the environment

Le potassium-40
Potassium is widely available on Earth as part ofmany different minerals. Although potassium-40
only represents 0.0117% of the mass of potassium,
it is the most frequently found radionuclide in
the environment and its activity reaches several
hundred Bq/kg in soils and continental and marine
sediments (see figure 8). Potassium (including 40K)
is a key element for living organisms and is easilytransferred to flora and fauna, which explains
why its activity reaches hundreds of Bq/kg infood (see figure 9). Such an activity value is thehighest of any natural or artificial radionuclides
in the environment, excluding any local anthropic
impacts, by far.

Telluric radionuclides have existed on Earth since
it formed. The main telluric radionuclides arepotassium-40 (40K), and the decay chain productsof uranium-238 (238U), uranium-235 (235U) andthorium-232 (232Th). These four radionuclides
are still present in the Earth's crust due to theirvery long half-lives (around several billion years).
Uranium-238, thorium-232 and uranium-235
produce 36 radionuclides in their decay chain(see figure 3). On this basis, a total of aroundfourty telluric radionuclides are present in allenvironmental components: soil, air, water, floraand fauna (including people).

FIGURE 3 / U
 RANIUM-238, THORIUM-232 AND URANIUM-235 DECAY CHAINS

48

Head of the chain   

Uranium-235
Half-life: 0.7 billion years

Radionuclides of interest mentioned in this report

Uranium-238
Half-life: 4.5 billion years

U

235

Thorium-232
Half-life: 14 billion years

U

Pa

U

238

231

234

Pa

Th

230

Th

234

Th
Ra

Ra

227

Ra

Ra

223

Rn

219

224

Radium-226
1,600 years

Rn

220

Rn

222

Radon-222
3.8 days
Polonium-210
138 days

Po

Po

218

Bi

Pb

Po

210

Bi

210

Pb

210

Po

216

Po

214

214

214

227

Ac

228

228

Th

231

228

Ac

230

226

Th

Th

232

212

Bi

Pb

Pb

Bi

212

211

Pb

212

206

Po

215

208

Tl

208

Lead-210
22 years/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

Pb

Pb

211

207

Tl

207

BACKGROUND RADIATION IN FRANCE / 02
Natural background radiation / 2.1

Decay chain radionuclides for uranium-238,
thorium-232 and uranium-235
In unaltered rocks, the activities of all uranium
and thorium decay chain radionuclides areapproximately the same as that of the head of
the chain (238U, 235U or 232Th): they are said to beat equilibrium. For example, radium-226 activity
in a rock is equal to uranium-238 activity. This is
not true for water or living organisms, which havedifferent physical and chemical properties, leading
to different reactions and transfers. Up to radium,
telluric radionuclides are generally at equilibrium
in soils, although minor unbalance can occur
due to the presence of living organisms or soilleaching. No equilibrium is reached after radiumisotopes. When radium decays a radioactive gas
called radon (mainly 222Rn) is produced. This radonis transferred from the soil to the atmosphere,
breaking the equilibrium at the end of the
decay chain. When radon decays, the daughter
radionuclides fix to particles suspended in the air.
These radionuclides include polonium-210 (210Po)
and lead-210 (210Pb), which settle on the surfaceof the soil. This transfer slightly increases theactivity of the surface soils in 210Pb with respect touranium-238 or radium-226.
In France, at any given location, uranium-238 andthorium-232 activities will be approximately thesame in rocks and soils, however, uranium-235
activity will be 20 times less. A ratio of 20 to 1
between uranium-238 and uranium-235 activity
reflects enrichment in uranium-235 (enricheduranium); a higher activity ratio would indicate
depleted uranium. In addition, uranium-236(another uranium isotope) can only be measured in
the environment if the latter is affected by specificfacilities. If this isotope is detected, an industrial
source can be confirmed.

Variation in the uranium and thorium
composition of soils and variation in dose rate
attributable to telluric radiation
Uranium and thorium activities in the mainterrestrial environment components: air, flora,
fauna, surface water and sediments, and groundwater, will depend on the activity of the underlying
geological formations and soils.
IRSN has determined an average value of 40
Bq/kg dry for uranium-238 and thorium-232 in
all regions, covering all types of soil and sites,
however activity varies significantly from a few
Bq/kg dry to a few hundred Bq/kg dry dependingon the type of subsurface. In general, rocks in
sedimentary basins (Paris basin, Aquitaine basin)
and limestone formations contain less uranium
than older rock formations (Armorican massif,
Massif central, Vosges). These activities canreach a thousand Bq/kg dry in uraniferous soils.
Variation in soil composition in terms of uranium
and thorium daughters can be demonstrated
based on variation in the radiation (airborne doserate) they emit.
Figure 4 shows a map of variation in telluric
gamma dose rates throughout mainland France.
This map was prepared using measurements
obtained by control dosimeters (i.e. dosimeters
located in areas unaffected by any radiographic
device) in 17,404 dentist and veterinary clinics
spread throughout mainland France. The highest
dose rates are primarily detected in the Massif
central, the Armorican massif, Vosges and Corsica.
These regions all consist of geological formations
with relatively high uranium content (granitic
formations). This map should be compared with
figure 6, which also highlights these geologicalformations as the most likely potential source ofradon emissions in the air.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /49

FIGURE 4 / MAP OF VARIATION IN TELLURIC GAMMA DOSE RATES USING DATA OBTAINED FROM CONTROL DOSIMETERS
µSv/h

0.220
0.200
0.180
0.160
0.140
0.120
0.100
0.080
0.060
0.040
0.020

© IRSN50

IRSN's Ulysse onboard gamma spectrometer; the sensors are installed in the pods on each side of thehelicopter. This set-up was used, on a plane, to obtain the data shown in the map in figure 5A.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

BACKGROUND RADIATION IN FRANCE / 02
Natural background radiation / 2.1

Variation in the uranium and thorium compositionof soils and variation in the dose rate in the air
attributable to the former are also clearly apparent
at regional level On this basis, figure 5A shows
variation in dose rate throughout north Brittany.
This map was prepared directly using airborne
gamma dose rate measurements. If we compare
the uranium content of soils on a relative basis(see figure 5B), strong correlation appears: areas
with high uranium content, shown in turquoise anddark blue, coincide with the highest dose rates(shown in yellow-orange/red).

In addition, very local variations appear overdistances of just a few kilometres. To the southof Guingamp or to the north of Lannion, thedose rate climbs from less than 0.050 to over
0.100 µSv/h. Such variations in dose rate causedby the uranium-thorium composition of soils canalso be detected at micro-local level, where dose
rates can double, or more, over just a few hundred
metres.

FIGURE 5A / MAP OF THE DOSE RATE 1 M ABOVE THE
GROUND AS MEASURED WHILE FLYING OVER PART OF
BRITTANYFIGURE 5B / MAP SHOWING THE AVERAGE URANIUM
CONTENT OF GEOLOGICAL FORMATIONS IN NORTHBRITTANY

Plougasnou

PaimpolLannionMorlaix

Plougasnou

Étables-sur-mer

Morlaix

Étables-sur-mer

Guingamp
Saint-BrieucSaint-Connan

PaimpolLannion

Guingamp

Saint-BrieucSaint-Connan

Plédran

PlédranCarhaix-Plouguer

Carhaix-Plouguer Saint-Nicolas-du-Pélem

Saint-Nicolas-du-Pélem
Laniscar

Laniscar

Loudeac

LoudeacPontivy

Pontivy

Locminé

µSv/h
0.100
0.094
0.088
0.082
0.076
0.070
0.064
0.058
0.052
0.046
0.040

Lorient

Pluvigne

Map of equivalent gamma dose rates
acquired in 2013 using IRSN's airborne
radiological measuring system, ULYSSE,
during a joint operation with the civil
security teams.

LocminéHennebont

Hennebont

Lorient

51

Perros-Guirec

Perros-Guirec

Mean U content< 2 ppm
2 - 5 ppm
5 - 8 ppm
> 8 ppm

Pluvigne

Map showing the meanuranium content of geologicalformations in north Brittany.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Variation in radon content in ambient air
Radon is a radioactive gas and is omnipresent
on the surface of Earth, where it forms whennatural radionuclides (uranium, thorium) in therocks and soils decay. Three radon isotopes exist(219Rn, 220Rn and 222Rn), however only radon-222
has a long enough half-life (3.8 days) for
significant activity per volume to be detected in
the environment. Radon-222 is part of the decay
chain of uranium-238 and is the daughter productof radium-226 (see figure 3).
Variable quantities of radon are emitted fromsoils and rocks depending on the properties ofthe source material (geological properties, radium
content, porosity, air permeability). Radon activity
by volume in soil air is more significant in regions

52

where the rocks have high uranium content, suchas some types of granite and some metamorphic
rocks (Armorican massif, Massif central, Vosges,
Corsica, etc.), and even, on a more exceptional
basis, in sedimentary formations (e.g. in the Lodève
region) or in karst formations. Radon activity cantherefore vary substantially throughout France.
The same applies for dose rates, at regional andeven local level. What's more, some geologicalstructures (faults, underground caverns, thermal
springs, etc.) can make it easier for the radon totransfer to the surface. A national map showing
potential radon content (see figure 6) was preparedbased on geological knowledge of France. Thismap can be used to target the areas where radonis the most likely to be produced and transferredto the surface and the atmosphere.

FIGURE 6 / MAP SHOWING THE POTENTIAL RADON CONTENT OF GEOLOGICAL FORMATIONS WITH A SCALE OF 1: 1,000,000

Radon potential
Low
ModerateHigh/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

BACKGROUND RADIATION IN FRANCE / 02
Natural background radiation / 2.1

Radon activity by volume in soil air generally varies
between 1,000 and several hundred thousand Bq/
m3 and varies substantially depend on the type ofsoil and underlying geological formations. Table 1
shows the ranges of radon activity by volume as
measured in soil air.
The radon released to the atmosphere will also
depend on weather conditions, in addition to
the properties of the soils and rocks. Weather
conditions (wind, rain, low temperatures, etc.) willaffect variations in radon activity over time at any
given location.

to the varying concentrations of uranium in theunderlying rocks, with a transition from granitic
rocks to the north (which are relatively rich inuranium) to volcano-sedimentary rocks to thesouth (which contain significantly less uranium).

FIGURE 7 / RADON-222 ACTIVITY BY VOLUME MEASUREDDURING ONE NIGHT (from 22:00 to midnight) USING A
PORTABLE LABORATORY (measurements were taken 2 mabove the ground)

Activities per volume measured in the atmosphere
are much lower than in the soil: airborne activity
varies between a few Bq/m3 and around a hundred
Bq/m3, with a mean value of a few tens of Bq/m3.
Many factors affect activity, including the geologyof the location in question, the distance to thesoil, topography and atmospheric conditions. For
example, if we consider a distance covering a few
hundred metres, activity may differ between thebottom of a narrow, but deep, valley, with limited
air flow, where the radon can concentrate, andan intermediate position half way up a slope, or awell-ventilated summit where the radon will more
rapidly disperse (see the Écarpière site describedin chapter 4 for forming mining sites). Finally, daily
fluctuations can occur at one single location, withhigh activity at ground level at sunrise and sunset,
when air movements are reduced.

53

Figure 7 shows radon activity by volume in theatmosphere measured two metres above theground along a road in the southern Vosges.
These measurements were taken using a portable
laboratory travelling very slowly by night. As isclear on the map, activity varied substantially overthe length of the road covered. Activity varied due

TABLE 1 / VARIATION IN RADON ACTIVITY BY VOLUME IN SOIL AIR BASED ON GEOLOGICAL PROPERTIES, AS MEASUREDIN SEVERAL REGIONS OF FRANCE

Range of radon activity by volume
in soil air (Bq/m3)

Mean radon activity by volume
in soil air (Bq/m3)

Granites, orthogneiss

10,000 – 500,000

100,000

Sedimentary andmeta-sedimentary formations

1,000 – 150,000

40,000

Basic volcanic formations

1,000 – 90,000

20,000Type of rocks

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Variation in the activity of telluric radionuclides
in the environment
Radionuclides in the soil can be absorbed byplant roots. Airborne radionuclides, particularlypolonium-210 and lead-210, radon daughter
products, settle onto the plant leaves. These two
radionuclides have the highest activities in food of
all telluric radionuclides (see figure 9). In general,
far higher levels of radium isotopes are absorbedby plant roots than uranium or thorium isotopes.
This means that radium activity is higher in flora.

54

The levels of uranium and thorium decay chain
daughter products in surface water and groundwater vary substantially due to different rock andsoil compositions, as well as the physical andchemical characteristics of the water, which canalso vary. In rivers, uranium-238, uranium-234,
radium-226 and radium-228 activities are mostly(over 95%) below 0.1 Bq/L, but can range fromless than 0.001 Bq/L to exceptional figures suchas 1 Bq/L. Higher values have been measured insurface water near to former mining sites (seechapter 4).

Activity is mainly transferred to livestock andrelated foodstuffs (milk, meat, eggs) via the foodchain. On this basis, radium, polonium-210 and
lead-210 levels in food of animal origin are also
higher than uranium or thorium isotope content.

Lead-210 and polonium-210 activities are
generally low and less than 0.01 Bq/L, however
they can reach 0.6 and 0.1 Bq/L respectively in
exceptional cases.

Natural radionuclides reach the seas and oceans
via drainage systems from continental land areas
and radon degassing. Telluric radionuclides
behave differently in this environment due to theirdifferent chemical properties, therefore activity
varies substantially between the different marine
components. In water, uranium and radium aremainly dissolved, with activities of approximately
30 to 40 mBq/L for uranium-238 (as was thecase for soils, 235U activity is 20 times lower) andapproximately 3 mBq/L for radium-226. On theother hand, thorium fixes to particles settling into
sediment and activity for thorium-232 dissolved in
the water is extremely low. Lead and polonium also
have a strong tendency to fix to particles, however,
due to surface enrichment from the atmosphere(radon decay), activity in surface seawater
is approximately 0.3 - 5 mBq/L. The marine
environment has one special characteristic: very
high polonium-210 content in marine foodstuffs.
This situation is caused by high assimilation byplankton. The marine organisms which depend
the most directly on plankton also contain thehighest levels of lead-210. This is particularly true
for molluscs, shellfish and small fish (sardines,
herrings, anchovies).

Figures 8 to 13 show activities for the mainradionuclides measured in France considered as
background radiation in mainland France. Theseradionuclides are either natural or residual
elements from old fallout (see chapter 2.2).
The data used to compile these charts have beenacquired by IRSN since 2009 in various contexts.
Some series with specific sources have been
added to ensure a comprehensive overview. Box
plots are used to indicate the ranges of activity
corresponding to 80% of the significant values
measured (activity between the 10% and 90%
percentiles is shown as a coloured box), mode
values (50% percentile) shown as a line cutting thecoloured boxes in half, and peak measurements(top lines). These statistics are representative of
IRSN measurements, but only approximate theactual situation. More specifically, only significant
measurements, i.e. those above the decisionthreshold (see chapter 8 of the appendices) areconsidered; the lowest levels of environmental
activity cannot be measured and are not shown.
No minimum values are shown for the box plots
for this reason. In general, the more data are
available, the more representative the statistics
are. For information, the number of analyses andComments on figures 8 to 13/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

BACKGROUND RADIATION IN FRANCE / 02
Natural background radiation / 2.1

the number of significant measurements used
are indicated on the x-axis for each data series.
The statistics shown may still be biased, even
if the number is high, particularly for naturalradionuclides. Natural radionuclide levels
indeed vary substantially in France, between
the sedimentary basins and the older massifs.
However the older massifs contain higher levelsof uranium and thorium daughter products, but
are poorly represented in the samples collected

and analysed by IRSN. To offset this bias, figure 11
can be used to compare activity at sites with a HighLevel of Natural Radioactivity (or HLNR), withactivity throughout the rest of mainland France.
In addition, a box plot format was selected to show
as much information as possible, despite the factthat very little data is actually available, if thestatistics provided would appear realistic. Finally,
it is important to highlight that values above thepeak values shown can still be measured.

FIGURE 8 / ACTIVITIES OF THE MAIN RADIONUCLIDES IN SOILS AND SEDIMENTS IN FRANCE
Although mean plutonium-239+240 content in soils and sediments, the result of nuclear testing fallout, would appear fairly
homogeneous in France, the degree of variation detected in soils without crops reflects the variation in deposition shown on the map infigure 15: plutonium activity is higher in mountain areas due to higher mean annual precipitation. Soil caesium activity is generally
consistent with the map showing the total deposition of fallout from nuclear testing and the Chernobyl accident (figure 18): activities
are lower to the west (mean value of 7 Bq/kg dry) than the east (mean value of 11 Bq/kg dry), and are higher in areas with greater
fallout (zones where mean residual radionuclides reach 26 Bq/kg dry; see focus article on p. 70). In addition, hot spots occur at altitude
corresponding to small surface areas of less than 1 m2 where snow concentrated in May 1986. These hot spots have much higher
activity levels: around 10,000 Bq/kg dry. Soil caesium-137 activity is much higher than strontium-90 activity for two main reasons: onthe one hand, fallout from the Chernobyl accident, particularly in east France, combined with fallout from nuclear testing, and on theother hand, strontium transfers more easily in soils, therefore a higher percentage of the activity initially deposited migrates to greater
depths. In terms of the levels of natural telluric radionuclides, uranium and thorium decay chain daughter isotopes, soils andsedimentary basins are easily identifiable using the data (mean value of 26 Bq/kg dry), and can be differentiated from the soils of older
massifs (mean value of 44 Bq/kg dry), and soils with a very high level of natural radioactivity (data for Haute-Vienne and Saône-etLoire). Finally, potassium-40 activity is higher and homogeneous across soils and sediments, as expected. The number ofmeasurements used (results above the decision threshold) and the number of analyses performed (e.g. 262/270) are shown for eachsoil or sediment category.

Bq/kg dry

239+240

100,000

Pu

137

Cs

90

U, 234U, 226Ra, 232Th

Sr

238

40

K

10,000
1000
100
10
1
0.1
0.01

Fluvial sediments (187/187)

Ocean sediments (308/308)

Soil without crops (658/671)(97/97)
Soil with crops(BRGM) sediment (119/119)(32/32)(Orano) HLNR soil

Fluvial sediment (145/167)(9/11)(NRGM) ref. soil

Older massifs (248/382)

Sedimentary soil (133/148)(16/70)Fluvial sediments

All soils (439/593)(4/16)
Ocean sediments

Soil without crops (103/118)(38/40)
Soil with crops(68/115)
Ocean sediments

Fluvial sediments (128/129)(4/4)"Hot points" in the Alps

Zones de rémanence (262/270)(75/82)
Soil with crops

Fallout zones (230/235)(37/87)
Fluvial sediments

West soil with crops (121/122)(23/39)
Ocean sediments

Soil without crops (120/120)

Soil with crops(20/20)0.001

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /55

FIGURE 9 / ACTIVITIES OF THE MAIN NATURAL RADIONUCLIDES IN FOOD PRODUCED IN FRANCE
The activities of the main natural radionuclides in food produced can be broken down into 4 orders of magnitude. Terrestrial uranium
activities are lower than radium activities due to less absorption by roots. These values are higher in the oceans as uranium is soluble
in seawater. Terrestrial lead-210 and polonium-210 food activities are higher than radium activity as these two radionuclides aredeposited onto plant leaves from the air after the emanation of radon. While these two radionuclides have similar levels of activity inthe air and in terrestrial components, polonium-210 activity is considerably higher in the oceans. In fact, for reasons which are notentirely understood by scientists, polonium concentrates in plankton and therefore in all living organisms feeding off plankton:
molluscs, shellfish, and to a lesser extent, small fish. As an essential nutrient, the potassium content and therefore the potassium-40
activity of the organic matter is the highest possible value. The number of measurements above the decision threshold and the numberof analyses performed (e.g. 10/12) are shown for each food category.

Bq/kg freshU238

Ra ou 214Bi

226

210

Pb ou 210Po

Po

210

40

K

1000
100
10
1
0.1
0.01
0.001
0.0001

Milks(10/12)Meat(14/14)
Cereal(14/47)
Leaf vegetables(10/10)
Fruits(4/19)
Fresh water fish
(17/17)
Sea water fish
(1/2)
Molluscs(24/24)Milks(3/24)
Meat(7/19)
Cereal(34/36)
Leaf vegetables(7/12)
Other fruit and vegetables(10/12)
Fresh water fish
(7/24)
Sea water fish
(7/24)
Molluscs(20/30)Milks(7/214)Meat(12/95)
Cereal(48/79)
Leaf vegetables (215/245)
Other fruit and vegetables(31/106)
Mushrooms(23/66)
Fresh water fish
(34/471)
Sea water fish (131/286)
Shellfish(34/69)Molluscs (465/478)
Fresh water fish
(11/11)
Sea water fish
(12/12)
Crustacés marins(5/5)
Molluscs(43/43)Milks (1 720/1 720)
Meat (106/106)
Cereal (434/434)
Leaf vegetables (595/595)
Fruits (203/203)
Mushrooms(174/174)
Wine(54/54)Cheese(35/35)
Fresh water fish (359/359)
Sea water fish (669/669)
Shellfish(90/90)
Molluscs (534/534)

56/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

BACKGROUND RADIATION IN FRANCE / 02
Natural background radiation / 2.1

FIGURE 10 / ACTIVITIES OF THE MAIN ARTIFICIAL RADIONUCLIDES IN FOOD PRODUCED IN FRANCE
Figure 10 shows the activities of the main artificial radionuclides in food produced in France. These activities are primarily attributableto residual fallout from nuclear tests and the Chernobyl accident (for caesium-137).
Plutonium-239+240 activities are lower for three main reasons: (1) during fallout periods after nuclear testing, 239+240Pu deposits wereapproximately 100 times lower than caesium-137 or strontium-90 deposits;(2) caesium-137 in fallout from the Chernobyl accident combined with the fallout from nuclear tests,and (3) less plutonium will transfer to roots than caesium or strontium. Although caesium-137 activity in the soils hosting theseradionuclides is much higher than strontium-90 activity (see figure 8), the levels of these two radionuclides are similar in food asstrontium transfers to roots more easily. Wild food (mushrooms, berries and game) are a special case as residual fallout from the
Chernobyl accident is much higher in forests (see focus article on areas with residual fallout p. 70). Terrestrial tritium activity is fairly
constant in any type of food, at equilibrium is reached with the air, the host reservoir for this radionuclide. This activity is primarily
attributable to residual fallout from nuclear tests, although current levels are approaching natural cosmic radioactivity. This natural
cosmogenic radiation, which is approximately 10 times lower, can be detected in the oceans, which remain almost unaffected by fallout
from nuclear testing due to the abundance of cosmogenic hydrogen. In the same way, carbon-14 occurs naturally, but is mainly residual
fallout from nuclear weapons testing. The number of measurements used (above the decision threshold) and the number of analyses
performed (e.g. 262/270) are shown for each food category.

Bq/kg fresh
1000

239+240

Pu

137

Cs

90

Sr

3

H lié

C

14

100
10

57

1
0.1
0.01
0.001
0.00010.000001

Milk(3/11)
Game(3/4)
Cereal(4/18)
Leaf vegetables(6/12)
Fruits(3/8)
Root vegetables(2/5)
Other vegetables(3/7)
Fresh water fish
(9/17)
Sea water fish
(5/23)
Molluscs(10/21)
Milk (441/1 697)
Cheese (24/30)
Cereal (73/431)
Meat (76/115)
Game(70/73)Mushrooms (112/116)
Berries(11/15)
Herbs(17/23)
Leaf vegetables (161/412)
Other vegetables(-/-)
Fruits(15/99)Wine(7/54)
Herbs(17/23)
Molluscs(26/90)Fresh water fish (165/190)
Sea water fish (281/309)
Milk (137/210)
Cheese(40/40)Game(3/5)
Cereal(59/65)
Fruits(-/-)
Leaf vegetables(23/24)
Other vegetables(5/9)
Mushrooms(4/80)
Fresh water fish
(14/17)
Sea water fish
(14/31)
Milk(163/-)
Meat(2/2)
Cereal(24/24)Mushrooms(4/4)
Leaf vegetables (50/50)
Fruit and other vegetables(14/19)Fresh water fish
(23/23)
Sea water fish
(7/7)
Molluscs(6/6)
Milk (113/113)
Meat
(2/2)
Cereal(8/8)
Leaf vegetables(51/51)
Mushrooms(4/4)
Other vegetables(4/4)
Fruits(14/14)
Fresh water fish (50/50)
Sea water fish
(3/3)
Molluscs(43/43)0.00001

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 11 / COMPARISON OF ACTIVITIES FOR SOME FOODSTUFFS PRODUCED IN ZONES WITH A HIGH LEVEL OF
NATURAL RADIOACTIVITY (HLNR - mainly Haute-Vienne and Saône-et-Loire) WITH FOODSTUFFS MAINLY PRODUCED IN
SEDIMENTARY AREAS (Paris basin, Aquitaine basin, river valleys, etc.)
As mentioned previously, the data shown in figure 9 are generally representative of large scale alluvial plains and sedimentary basins,
where uranium levels in soils are low to moderate. Figure 11 illustrates areas with a High Level of Natural Radioactivity (HLNR) which
can be found in the Massif central, Amorican massif, Vosges or Corsica. This figure can be used to compare activity levels in the
different HLNR areas (darker colours on the graphic) with the "reference" values indicated on figure 9 (paler colours on the graphic) for
each food category. In HLNR areas, activity ranges for natural radionuclides are generally higher than, or much higher than, activity
levels in the rest of France. Activities measured near to former mining sites, as described in chapter 4, must be compared with HLNR
data. The number of measurements used (above the decision threshold) and the number of analyses performed (e.g. 262/270) are
shown for each food category.

Bq/kg fresh

Ra or 214Bi

U

226

238

1000

210

Pb or 210Po

100
10
1
0.1
0.01
0.001

(3/3)

(48/79)HLNR cereal studies

Ref. cereals(7/41)

Other ref. fruit and vegetables (31/106)(17/46)HLNR fruit

HLNR leaf vegetables

Other HLNR vegetables(24/48)

Ref. meats

Ref. leaf vegetables (215/245)(3/29)(12/95)

HLHR meats(5/24)(7/214)
Ref. milks

HLNR fruit/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

HLNR milks(7/12)(3/21)

Ref. leaf vegetables

Other ref. fruit and vegetables (10/12)(7/19)(13/25)

Ref. meats

HLNR leaf vegetables(3/16)(4/19)(5/15)

Ref. fruit

HLNR milks(3/24)(7/25)HLNR fruit

Ref. milks(16/31)Other HLNR vegetables

HLHR meats(17/31)(10/10)Ref. leaf vegetables

Ref. cereals

HLNR leaf vegetables(6/6)(14/47)HLNR cereals(6/19)(14/14)
Ref. meats(10/12)
Ref. milks

HLHR meats(8/20)

0.0001HLNR milks

58

BACKGROUND RADIATION IN FRANCE / 02
Natural background radiation / 2.1

FIGURE 12 / VARIATION IN THE ACTIVITY OF THE MAIN ARTIFICIAL RADIONUCLIDES MEASURED IN THE AIR IN FRANCEAND GERMANY OVER THE LAST 60 YEARS
Figure 12 shows data acquired by IRSN in France and by Physikalisch-Technische Bundesanstalt (source: H. Verschofen) in Germany.
These German data for background radiation in France are fully representative of radionuclides from nuclear test fallout; strontium-90
and plutonium data acquired by IRSN since 2012 particularly corroborate the German data. Krypton-85 activity measured in Germany
can be considered as representative of background radiation in France, from four different sources: natural (very low), nuclear
weapons tests, the Chernobyl and Fukushima accidents and all effluents discharged from fuel processing plants. In France, effluentsdischarged from the La Hague plant merge with this background radiation (see chapter 3.3 La Hague). Xenon-133 was released during
nuclear weapons tests, and during the Chernobyl and Fukushima accidents, and is discharged by many nuclear facilities, particularly
NPP. However, discharges by the radio-pharmaceutical industry are the main source of xenon-133. On this basis, IRE (Institut nationaldes radioéléments - National institute of radioelements) based at Fleurus in Belgium is the main source of xenon-133 in the air in
France and Germany. Mean monthly values are shown for all radionuclides, covering France as a whole. These mean values willsmooth out any temporary high or low measurements. For example, on 1 May 1986 after the Chernobyl accident, caesium-137 activity
in the air reached 7 Bq/m3 (7,000,000 µBq/m3) in Verdun. In the same way, caesium-137 activity measured at the La Seyne-sur-mer
station after a source of caesium-137 was accidentally incinerated on 25 May 1998 at Algeciras in Spain, reached 2 480 µBq/m3 early
June. Finally, peak activity for radionuclides with a half-life less than 3 years (mainly 131I and 134Cs) temporarily reached almost
10,000 µBq/m3 (including 7,500 µBq/m3 of gaseous iodine-131 and 2,000 µBq/m3 of particulate iodine-131), and 250 µBq/m3 of
caesium-137, between 25 March and 20 April 2011 after the Fukushima accident. Plutonium-238 activities are 30 times less thanplutonium-239+240 activities. These radionuclides were released during nuclear weapons tests and when a satellite (SNAP 4) poweredby this radionuclide was destroyed in the atmosphere in 1964. Finally, americium-241, a plutonium-241 daughter product released
during nuclear testing, is not shown in this graphic. Airborne activity over the last two decades has reached approximately half that ofplutonium-239+240 activity, as shown by figure 13.

Fallout from atmospheric testingof nuclear weapons59

1961-1962: 180 Russianand American explosionsµBq/m3
10,000,000

Chernobyl accident

Peak values after each
Chinese explosion

1,000,000
100,000
10,0001000

Algeciras accident

100

Fukushima accident

10
1
0.1
0.01
0.001
0.00010.00001
1959
Kr
Xe

85

133

1963

1986

1998

2011

2018

C Source: IRSN since 1994; international prior to 1994
H Source: Lausanne and Ottawa universities

14

Source: H. Wershofen

Cs
Half-lives < 3 years (1)
137

1981
3

Source: IRSN

Sr

90

Pu

239+240

Pu

238

Source: H. Wershofen
based on 137Cs or 239+240Pu
Source: IRSN

1. Radionuclides with half-lives of less than 3 years: 131I, 140Ba, 141Ce, 103Ru, 89Sr, 91Y, 95Zr, 144Ce, 54Mn, 106Ru, 55Fe, 125Sb, 134Cs…

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 13 / MEAN ACTIVITIES FOR A FEW NATURAL AND ARTIFICIAL RADIONUCLIDES MEASURED IN THE AIR IN FRANCESINCE 2009
Figure 13 shows the mean activities for a few natural and artificial radionuclides measured by IRSN over the last decade. The numberof measurements used (results above the decision threshold) and the number of analyses performed (e.g. 15/20) are shown for eachradionuclide.

µBq/m31,000,000
100,000
10,000
1000
100
10
1
0.1
0.01
0.001
0.0001/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017234
Th
(15/15 317)

228
Ac
(87/17 179)

210
Pb
(2490/19 449)

40K
(232/17 179)7
Be
(19 769/19 912)

C
14

H
3

241
Am
(20/20)Pu(20/20)239+240

238
Pu(10/20)137
Cs(1 139/-)

60

90
Sr
(15/20)0.00001BACKGROUND RADIATION IN FRANCE / 02
Background radiation from old fallout / 2.2

2.2. BACKGROUND RADIATIONFROM OLD FALLOUT
Fallout from the atmospheric testing of
nuclear weapons
Between 1945 and 1980, over 500 atmospherictests were carried out for nuclear weapons by theUnited States, the USSR, Great Britain, China andFrance. Most radioactive fallout was generated
in two specific periods: between 1951 and 1958
and between 1961 and 1962, before the Test Ban
Treaty was signed in 1963. Many radionuclides
were released into the atmosphere during thesetests, and around twenty were regularly measured
in the air in France (see figure 12), in rainwaterand various foodstuffs. In 1963, when radioactive
fallout peaked, the mean activity from artificial
radionuclides reached 8 Bq/m3 in air (including
6 Bq/m3 for tritium), 650 Bq/kg fresh in lettuce(1/3 tritium and 1/5 carbon-14), and 450 Bq/L inmilk (see figure 14). During the same year, people
in France were subjected to an estimated average
dose of 300 μSv, mainly by ingesting contaminatedfood. Most radionuclides with a short half-life(less than 3 years) released as part of this fallout,
have disappeared. Today, only tritium, carbon-14,
caesium-137 (137Cs), strontium-90 (90Sr), plutonium
isotopes 238, 239, 240 and 241 (238Pu, 239Pu, 240Pu et
241Pu), and americium-241 (241Am) from the decayof plutonium-241 remain.
With the exception of tritium and carbon-14,
the soil is currently the main reservoir for
all of these radionuclides, feeding the otherenvironment components: air when raised
into suspension, plants when absorbed via theroots or when particles in suspension settle
onto the leaves, rivers from soil drainage andfauna via ingestion. Figure 15 shows the mapof total plutonium-239+240, caesium-137 andFIGURE 14 / PEAK ACTIVITY MEASURED IN LETTUCES (Bq/kg fresh) AND MILK (Bq/L) IN FRANCE DUE TO FALLOUT FROMTESTING NUCLEAR WEAPONS (1963), AND FALLOUT FROM THE CHERNOBYL ACCIDENT (1 - 5 May 1986), LATE MAY 1986,
IN 2009 AND EXPECTED IN THE COMING YEARS

Bq/kg fresh or Bq/L
En 1963

1-5 May1986

Other artificial radionuclides (FP and AP)
Mainly artificial 14C
Mainly artificial 3H
Telluric radionuclides: mainly 40K

3000

Late-May 19862009
2015-2020

800

500

10-20% artificial
radionuclides,
mainly 14C

300
150
0

Lettuce

Milk

Lettuce

Milk

Lettuce

Milk

Lettuce

Milk

Almost no artificial 3H or 14C(from nuclear tests)

Lettuce

Milk

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /61strontium-90 deposits in soils. In old fallout(from nuclear weapons and satellite destruction;
see comments for figure 12), regardless ofwhich environmental component is considered,plutonium-238 activity is 30 times less thanplutonium-239+240 activity.
Tritium and carbon-14
Most tritium and carbon-14 can be found in the air.
These two radionuclides are integrated in organic
matter in flora via photosynthesis. They are thentransferred to fauna when the flora is ingested.

62

Variation in carbon-14 composition since the1950's due to fallout from nuclear tests can bemeasured in all environmental components in theform of the specific activity in Bq/kg of carbon. On
land, the carbon-14 content of flora and fauna isin equilibrium with the air, which gives the same
specific activity in both components. These specificactivity is precisely determined and varies eachyear. Furthermore, this activity does not vary overterrestrial environmental components. Figure 16
shows variation in specific activity for the entire
northern hemisphere since 1950.
This specific activity increased from cosmogenic
levels (226 Bq/kg of C; see chapter 2.1 oncosmogenic radionuclides) to around 420 Bq/kg
of C in 1963, when test fallout peaked, and when
US-USSR atmospheric testing ceased. While
the total activity of the atmospheric component
has only decreased slightly since that time(insignificant radioactive decay and low absorption/
fixation by organic matter), specific activity has
dropped substantially due to the increase in CO2
of fossil origin. In fact, the specific activity ofthis CO2 is at cosmogenic levels, and dilutes theresidual carbon-14 from nuclear testing. The
current specific activity of 227 Bq/kg of C is close
to cosmogenic levels. If specific activity differs bymore than 3 Bq/kg of C, a local anthropic impact canbe assumed: effluents discharged from a nuclear
facility if the specific activity measured exceeds
this value, industrial discharges from fossil CO2
generation if the specific activity measured is lessthan this value. On this basis, specific activity canbe used to detect very low local impacts whichcannot be detected by measuring activity by mass
(Bq/kg fresh).
The specific activity of carbon-14 in rivers andlakes is systematically less than that recorded
for the other environmental components as theradionuclides are diluted by former carbonates
to varying degrees. These carbonates are notaffected by fallout from nuclear testing in theenvironment. The specific activity of carbon-14 inrivers currently varies between 200 and 220 Bq/kg
of C depending on carbonate levels.
In the same way as carbon-14, residual tritium
fallout from nuclear weapons testing is present in
the atmosphere. Carbon-14 is also transferred toorganic matter via plant photosynthesis, with anactivity in Bq/L of water (see focus article in chapter
1) at equilibrium (with the same activity) withatmospheric water vapour. The activity of rivers
also depends on the atmosphere, particularly due
to precipitation. Rainwater activity can therefore beconsidered as a proxy for variation in background
tritium in the atmosphere/terrestrial environment/
continental aquatic environment. Figure 17 hows
how tritium activity in rainwater in the northernhemisphere suddenly increased from 1950 fromcosmogenic levels (0.1 to 0.6 Bq/L; see chapter 2.1)
and peaked at approximately 600 Bq/L in 1963 at
the high point for atmospheric fallout from nuclear
weapons testing. This activity has since decreased,
as the tritium is diluted in the oceans, a largehydrogen reservoir. In fact, thanks to the shear
size of this reservoir, fallout from nuclear tests has
had little impact on the tritium activity of sea water,which has remained at cosmogenic levels.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

BACKGROUND RADIATION IN FRANCE / 02
Background radiation from old fallout / 2.2

FIGURE 15 / CAESIUM-137, STRONTIUM-90 AND PLUTONIUM-239+240 DEPOSITS AFTER THE ATMOSPHERIC NUCLEARTESTING
Deposition peaked after the fallout from the atmospheric testing of nuclear weapons (1945-1980) in Bq/m2 during rain, therefore
ground activity measurements reflect mean annual precipitation.

Bq/m2
Pu
100
75
50

239+240

Cs or 90Sr
15,00010,000
8,000
3,000

137

63

FIGURE 16 / VARIATION IN THE SPECIFIC ACTIVITY OF CARBON-14 IN THE NORTHERN HEMISPHERE SINCE 1950 (Bq/kg ofcarbon)Bq/kg of carbon
450

Nydal & Lövseth, 1983
Mc Gee et al., 2004
Isogai et al., 2002
Otlet et al., 1997
Roussel-Debet et al., 2006
Mc Namara & Mc Cartney, 1998
IRSN

400

350

300

250

200
1940

1950

1960

1970

1980

1990

2000

2010

2020

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 17 / VARIATION IN TRITIUM ACTIVITY IN RAINWATER (Bq/L; source: IAEA)
Matching data from Canada (Ottawa) and France (Thonon-les-Bains) demonstrate how homogeneous levels of atmospheric tritiumfrom residual fallout after nuclear weapons testing are throughout the northern hemisphere.

1000
OttawaThonon-les-Bains

Bq/L

100

10

1

0.1
Jan-5364

Jan-63Jan-73Jan-83

Fallout from the Chernobyl accident
The air masses contaminated by the Chernobyl
accident reached France early May 1986, mainly
between 1 and 5 May 1986. Due to highly variable
rain levels in east France during this period,
radioactive deposits (particularly iodine-131 andcaesium 134 and 137) were higher in this area
compared with the rest of France, and varied
substantially (see figure 18). Food contamination
peaked immediately after fallout deposition andaffected vegetables, mainly leaf vegetables andmilk (see figure 13) as well as sheep and cattle ata later stage. Iodine-131 activity disappeared after
3 months due to radioactive decay and caesium
activity was divided by 100 to 1,000 over the same
period. As the accident occurred early in thegrowing season for most crops, cereal and fruit
harvests were relatively unaffected. During 1986,
the effective doses reaching adults in east France
represented 0.75 mSv on average (May-December1986). These doses later gradually decreased year
by year (see figure 19). These effective doses werere-assessed in 2015 using measurements acquiredin 2013-2014 as part of the radiological overview
of residual artificial radioactivity (see p. 69 andthe focus article on p. 70). Mean equivalent doses
reaching the thyroids of children living in east
France between May and July 1986 represented
approximately 10 mSv. Most of these doses werereceived by eating contaminated food, particularly

Jan-93Jan-03Jan-13

fresh vegetables and milk, during the first threemonths after the radioactive fallout.
Note: in east France, caesium-137 is mainly
attributable to fallout from the Chernobyl accident,
while in the western 2/3, a large percentage,
potentially even most, of this radionuclide comesfrom atmospheric fallout from nuclear weapons
testing.

Fallout from the Fukushima accident
Radionuclide levels in atmospheric fallout inmainland France from the Fukushima accident of
11 March 2011 in Japan, were very low and rapidly
dispersed: traces of iodine-131, caesium 134 and137 were detected from late-March to May 2011
in the air, rainwater and a few foodstuffs (leafvegetables, milk, etc.) with activities 500 to over
1,000 times less than those measured in France
early-May 1986 after the Chernobyl accident.
These depositions were undetectable from mid2011 (see IRSN report DEI 2011-01 "Analyse del’impact de l’accident de Fukushima en France àpartir des résultats de la surveillance renforcéede la radioactivité de l’environnement" (Analysisof the impact of the Fukushima accident in France
based on the results of the reinforced monitoring ofenvironmental radioactivity available from the IRSN
website in French).

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

BACKGROUND RADIATION IN FRANCE / 02
Background radiation from old fallout / 2.2

FIGURE 18 / MAP OF CURRENT SURFACE CAESIUM-37 ACTIVITY IN SOILS IN FRANCE (Bq/m2) DUE TO RESIDUAL FALLOUTFROM NUCLEAR WEAPONS TESTING (see figure 14) AND THE CHERNOBYL ACCIDENT
While most caesium-137 in the western 2/3 of France is substantially and mainly the product of nuclear testing, in east France, where
it rained early May 1986, a very high percentage of caesium can be considered as fallout from the Chernobyl accident.

Cs
Bq/m2

137

40,00035,00030,00025,00020,00015,00010,000
6,000
3,000

65

FIGURE 19 / VARIATION IN THE TOTAL ANNUAL EFFECTIVE DOSE FOR ALL RADIONUCLIDES AND ALL MEANS OF
TRANSMISSION IN FRANCE PER ADULT (mSv/year) ATTRIBUTABLE TO FALLOUT FROM THE CHERNOBYL ACCIDENTmSv/year
101

0.1
Mean activity inthe most affectedareas: 40 μSv/year

0.01

0.001
1986

Mean value forFrance as a whole:
5 μSv/year

1989

1992

1995

1998

2001

2004

2007

2010

2013

2016

The most affected areas in east France
The most affected areas in west France
RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /2.3. RANGE OF POPULATIONEXPOSURE LEVELS DUETO BACKGROUND RADIATIONIN FRANCE
Most of the information provided below, on
the effective doses received by people in France
due to natural sources of radiation or residual
old fallout, was obtained from IRSN report
2015-00004 "Exposition de la population française
aux rayonnements ionisants" (Exposure to ionisingradiation for people in France) available from the
IRSN website in French.

Effective external doses due to cosmic
and telluric radiation

66

If we consider the map of cosmic radiation in France(see figure 1, chapter 2.1), and that people spend
most of their time indoors ( 22 h/day on averageand 16 h/day for people who work outdoors), andthat buildings reduce cosmic radiation by 20%,the mean effective dose reaching an adult due tocosmic radiation is estimated at 0.31 mSv/year.
This figure is less than 0.36 mSv/year for 95%
of individuals, but can reach 1.68 mSv/year for
high-altitude areas. On this basis, exposure tocosmic radiation varies little for most people,
with the exception of high-altitude areas andexposure during air travel. In fact, exposurelevels are higher for people travelling by air. As
most individuals do not travel frequently by air,
this additional exposure is only 0.01 mSv/year on
average for the entire French population, however,it reaches 0.55 mSv/year on average for frequent
travellers, i.e. people flying between ten and thirty
times annually (approx. 11% of passengers or 3%of the French population). Flight crews face thehighest levels of ionising radiation, on average,
with a mean effective dose per person of 1.9 mSv/
year in 2013 (see IRSN/PRP-HOM report 2014-007"Exposition professionnelle aux rayonnements
ionisants en France : bilan 2013" - Professional
exposure to ionising radiation in France: 2013
overview).

Levels of exposure to telluric radiation depends on
the sub-surface and materials used. Construction
materials are considered to add an extra 40% to
the outdoor dose rate, for people indoors, to give
worst-case figures. The measurement data used
are obtained from control dosimeters installedin 17,404 dentist and veterinary clinics spreadthroughout France (see chapter 2.1). If cosmic
radiation is deducted from these results, themean effective dose for telluric radiation reachingan adult is equal to 0.62 mSv/year. Most people(90% of the population) are subjected to a doseof between 0.36 and 1.1 mSv/year. This dose canreach 2 mSv/year in some municipalities.

Effective doses received by ingesting
natural radionuclides via food or smoking
The average effective dose of natural radionuclides(cosmogenic and telluric) absorbed by an adultdue to eating food and smoking is estimated at
0.55 mSv/year. This dose varies due to individual
consumer habits rather than geographic location,
particularly for fish/seafood, ranging from 0.4 mSv/
year for individuals who do not eat these foodstuffs
to over 3.1 mSv/year for those consuming large
amounts (see figure 20). Although potassium-40
is a significant percentage (30%) of this dose,
this figure is fairly constant for all individuals
and does not depend on food preferences, as thehuman body can regulate its potassium levels.
Furthermore, the contribution of cosmogenic
radionuclides is low (0.02 mSv/year, or less than4%). The mean effective dose for the daughter
products of the uranium and thorium decay chainsin foodstuffs represents 0.32 mSv/year, which isaround 60% of the total dose received by ingesting
food. This figure varies substantially as it depends
on the level of consumption of fish, and above
all molluscs and shellfish, which contain high210
Po levels. When compared with an individual
who never eats molluscs or shellfish, regularconsumption (once or twice weekly) will lead toan additional effective dose of 0.54 mSv/year,
doubling the mean total dose attributable to eating
food. In the same way, a heavy smoker can absorb
an additional effective dose of approximately 0.3
mSv/year when compared with a no smoker,
mainly due to the 210Po level in tobacco.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

BACKGROUND RADIATION IN FRANCE / 02
Range of population exposure levels due to background radiation in France / 2.3

Finally, drinks (tap and mineral water) containa wide range of radionuclide levels. The dose
reaching any individual will depend on their tap or
selected mineral water. No national mean value
can be provided. On this basis, the dose absorbed
by adults drinking water will only exceed 100 μSv/
year for less than 0.2% of the population, for thosedrinking tap water, or may be higher for people

drinking one of the 4% of mineral water types withhigher doses on a regular basis (2 L/day, or 730 L/year). The equivalent dose received by drinking
water is probably between a few μSv/year and100 μSv/year for the vast majority of adults.

FIGURE 20 / SUMMARY OF DOSES (in mSv/year) ATTRIBUTABLE TO ADULTS INCORPORATING NATURAL RADIONUCLIDESThe lower value is true for a non-smoker, who does not drink water with a high level of natural radionuclides and does not eat molluscs
or shellfish; the high "food" value is true for someone who eats large quantities of sea food; the high "water" value is true for someone
who drinks water with high levels of natural radionuclides.

mSv/year
3.5
3.0

0.30
0.19

2.5

0.19
67

2.0
2.13

1.5

2.13

1.0
0.5
0

0.19
0.18

0.19
0.13
0.18

Low value

Mean value

0.18

0.19
0.13
0.30
0.18

0.30
0.19
0.13
0.18

High value(food)High value(water)Heavy
smokers

0.30
0.18
High value(food, water,
heavy smokers)■ Smoking■ U-TH chains, excluding fish/sea food
■ U-TH chains in fish/sea food
■ Water■ 40K■ 14C, 87Rb, 7Be, 11Na and 3H

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Effective dose received by inhaling
radon
Radon daughters will fix to aerosols in the airand, when inhaled, will settle in and irradiate
the respiratory tracts. Radon can accumulate inconfined spaces such as buildings, however thisphenomenon will vary depending on the locationand type of soils and underlying rocks, the typeof building, the construction method used for thebuilding and the behaviour of building occupants.
The mean radon-222 concentration inside homes
in mainland France, weighted by type of group andhome, is equal to 60 Bq/m3. The corresponding
average dose is estimated at 1.43 mSv/year. The
map showing potential radon activity by volume
inside housing (see figure 11) highlights thesignificant variation between most of France,
where activity is less than 150 Bq/m3, and a few
areas in the Massif central, Vosges, Armorican
massif and west Corsica, where activities areover 400 Bq/m3. On this basis, while 90% of theFrench population absorbs an effective dose ofradon between 0.54 and 3.15 mSv/year, the meandose in départements such as Lozère or Cantal
reaches 5 - 6 mSv/year. Higher values can bereached in specific locations (20 mSv/year). It isalso important to realise that, if houses are built
on top of old mining remains, radon levels in the
air can reach several thousand Bq/m3 with thecorresponding higher dose rates.
The radon dose conversion factor (used todetermine the dose-to-activity ratio for radon
inhaled) must be increased in the near future
based on recent epidemiological studies andnew dosimetric calculations, as recommended
by the International Commission on RadiologicalProtection (ICRP). At the time of writing, thisrecommendation had not yet been incorporated
into French regulations. The above radon doses
could be doubled based on this recommendation.

68

FIGURE 21 / POTENTIAL RADON ACTIVITY PER VOLUME INSIDE HOUSING BASED ON THE UNDERLYING ROCK TYPES (Bq/m 3)
The highest concentrations exceed 400 Bq/m3 and are recorded in the older massifs (Armorican, Central,
Vosges and north-western Corsica), while the lowest values are recorded in sedimentary basins (Paris and Aquitaine), dropping below
100 Bq/m3.

Bq/m3
500
450
400
350
300
250
200
150
100
50

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

BACKGROUND RADIATION IN FRANCE / 02
Range of population exposure levels due to background radiation in France / 2.3

Effective doses due to residual
radioactivity from old fallout
comprising artificial radionuclides
Current exposure levels for people in France due toresidual fallout from nuclear weapons testing andthe Chernobyl accident were recently re-assessedon the basis of the measurement results obtained
during the radiological overview completed by
IRSN in 2013-2014 (see focus article on p. 70).

As explained in the focus article, the doses
potentially received by people living in the French
regions most affected by this fallout can be muchhigher, particularly for fans of mushrooms andgame (see focus article on p. 72).

This dose is currently approximately 6 µSv/year for
most adults. This dose is mainly (87%) attributable
to exposure to the extreme radiation emitted by
137
Cs in soils (see figure 22). Only 13% of this doseis absorbed by eating food. Residual strontium-90(90Sr) from nuclear weapons testing is the main
component of the dose absorbed by eating, aheadof caesium-137 from both sources and well aheadof plutonium and americium.

69
FIGURE 22 / ESTIMATED EFFECTIVE DOSES ATTRIBUTABLE TO RESIDUAL FALLOUT FROM NUCLEAR TESTS AND THE
CHERNOBYL ACCIDENT ABSORBED BY MOST FRENCH ADULTS (these data are valid for people who do not live in the areas
most affected by the fallout)

Dose absorbed by eating 90Sr:
0.62 µSv/year
Dose absorbed by eating 137Cs:
0.19 µSv/year

Dose absorbed by eating 241Am:
0.002 µSv/year

Dose absorbed by eating 238+240Pu:
0.008 µSv/year

Dose absorbed byexternal exposure to 137Cs:
5.2 µSv/year

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FOCUS ARTICLE
A RADIOLOGICAL OVERVIEW OF RESIDUALARTIFICIAL RADIOACTIVITY

This overview aims to update reports on artificial
radionuclides still detected in the areas mostaffected by deposits from the atmospheric testingof nuclear weapons (between 1950 and 1980) andthe Chernobyl accident (1986) and to assess the
exposure of local inhabitants.

Research strategy
This study mainly focuses on mountain areas in east France, which were significantly affected by
fallout from the Chernobyl accident (Vosges, Jura, South Alps and Corsica), and the Pyrenees,
where radionuclide deposits from the atmospheric testing of nucear weapons are decisive.
Caesium-137 (137Cs) released during Chernobyl fallout and atmospheric tests is omnipresent in
the environment. Levels vary depending on the location, but quantities can generally bemeasured, meaning that this radionuclide can be used as the main indicator of levels of artificial
radioactivity in the samples tested. Strontium-90 (90Sr), and plutonium (239+240Pu) andamericium-241 (241Am) isotopes were released as fallout from atmospheric tests.

70

Various samples (soils, grass, milk, cheese, berries, mushrooms and game) were taken in 2013 and2014 from the area covered by the study. Caesium-137, strontium-90 and plutonium isotopes were
measured in the samples. Samples of surface water, sediments, aquatic mosses and fish were takenfrom the aquatic environment: six Mercantour lakes and three coastal rivers in east Corsica (FiumOrbo, Tavignano and Golo). Measurements had been taken for these sites in the weeks
immediately following the Chernobyl accident.
Main study results
According to the aquatic measurements, artificial radioactivity levels have not varied substantiallysince 1986 in the Mercantour lakes, with the exception of the mosses, where caesium-137 activity
is decreasing thanks to an effective half-life of approximately 6 years. Artificial radionuclides areclearly persisting in these "contained" environments in water (137Cs: 0.2 - 1.7 mBq/L), aquaticmosses (241Am: 2.5 - 5 Bq/kg dry) and sediments (137Cs and 241Am exceed 1,000 and 1 Bq/kg dry,respectively). If we compare these values with an "open" environment, such as the rivers draining
east Corsica, caesium-137 activity in fish and sediments (0.05-0.09 Bq/kg fresh and 4-14 Bq/kg
dry, respectively) has dropped significantly since the initial measurements taken in 1986-1987 (1100 Bq/kg fresh and 10-700 Bq/kg dry, respectively). The effective half-life of caesium-137 in thesediments of the Var river and its tributaries is similar to that recorded in other rivers in France,with no local anthropic impacts.

●●●/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

BACKGROUND RADIATION IN FRANCE / 02
Range of population exposure levels due to background radiation in France / 2.3●●●

Three key points appear if we summarise the activities of artificial radionuclides in a terrestrial
environment:• caesium-137 activity is highest in the soils in massifs in east France (Vosges, Jura, South Alpsand Corsica), reaching over 10,000 Bq/m2 at some sampling points. These observations matchthe levels expected in these areas, where Chernobyl fallout combined with the activity from
nuclear testing. Caesium-137 activity is lower in soils in the Pyrenees (137Cs activity exceeds
3,000 Bq/m2), and mainly the outcome of nuclear testing. These results corroborate the levels
calculated from deposition models (see map in figure 18). Plutonium (239+240Pu activity from
nuclear weapons tests) activity in soils in hilly areas (100-200 Bq/m2) matches the map shown infigure 15, i.e. two to four times higher than soils in low-lying flat areas (50-80 Bq/m2). Thirty
years after the Chernobyl accident, very high caesium-137 activity (over 10,000 Bq/kg at somespecific locations) is still detected at the high-altitude flat "hot spots" in the Alps, which varyfrom surface areas of a few dm² to a few m². At these locations, caesium-137 concentrated in thesnowbanks formed by the snow which precipitated as the air masses carrying fallout from the
Chernobyl explosion travelled over the Alps (in May 1986);• data also highlight vertical migration in soils and the transfer of fission products (137Cs and 90Sr)
to plants in fields and forests. As expected, as strontium-90 transfers more easily thancaesium-137, strontium-90 has achieved greater depths in soils and transferred more
substantially to plants in low-lying flat areas. Details of migration and transfers depend on thephysical and chemical properties of soils (particle size, pH, organic content and exchangeable
cations) and anthropic factors such as land use and crops grown;71• food activity in the hilly areas studied is generally higher than in low-lying flat areas. To give one
example, caesium-137 activity in the milk samples taken in residual fallout areas (mean value:
0.32 Bq/L) is ten to a hundred times higher than in milk samples taken in areas near to EDF
nuclear power plants (between 0.004 and 0.03 Bq/L). These observations match soil activity
measurements, which are one order of magnitude higher in hilly areas, on average, whencompared with data for low-lying flat areas.
One key difference arises between the level of activity measured in food from low-lying flat areas(average value for 137Cs: 0.32 Bq/L in milk) and food from forests (berries, mushrooms andgame), where caesium-137 activity varies more widely over approximately two orders ofmagnitude depending on the species and sampling area) and can exceed 100 Bq/kg fresh (formushrooms and wild boar meat).

●●●

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /●●●The effective doses absorbed by adults living in the areas most affected by artificial radioactivity
were estimated based on caesium-137 activities measured in food and in situ measurements of theairborne dose rate (see table A).
TABLE A / DOSES IN AND OUT OF THE AREAS MOST AFFECTED BY ARTIFICIAL RADIOACTIVITY (in µSv/an)External exposure

72

Internal exposure (ingestion)

Outside of the most affectedareas

5 µSv/year

1 µSv/year

Inside the most affected
areas

Up to 40 µSv/year

From a few dozen to a few hundred µSv/year forliving organisms eating mushrooms and gameThe external dose reached after exposure to caesium-137 (40 µSv/year) fallout was calculatedusing airborne dose rate measurements (2 - 7 nSv/h) (1). The highest dose rate values (100 nSv/h)are measured at Mercantour "hot spots" (with a surface area varying between a few dm² and one
m², and where caesium-137 activity reaches a few tens of thousands of Bq/kg). If one individual
remained in contact with these soils for several hours (bivouac camping or afternoon nap, lying
down), the effective external dose would reach a few tens of µSv/h. Eating food from areas with ahigh level of residual artificial radioactivity would lead to the ingestion of 1 µSv/year. However,eating food from forest areas (mushroom and game), with a caesium-137 activity of several
hundred Bq/kg fresh, could lead to a dose representing a few tens to a few hundreds of µSv/year,
depending on the quantities eaten.
For more info.: http://www.irsn.fr/FR/expertise/rapports_expertise/surveillance-environnement/
Documents/IRSN_Constat-Remanence-France_201604.pdf
1. Subjects are assumed to spend 8 hours a day outdoors and to benefit from a protection factor of 0.4 when indoors.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

BACKGROUND RADIATION IN FRANCE / 02
Range of population exposure levels due to background radiation in France / 2.3

Report on effective doses received due
to background radiation in France
The mean exposure of people in France tobackground radiation, as defined above, andexcluding medical exposure, is estimated at
2.9 mSv/year. This dose varies based on thegeographic location (radon accumulated in theair, telluric radiation) and lifestyle (shellfish eaten,
smoking, air travel).
Figure 23 shows doses for two very different
scenarios: the first covers an individual with thelowest exposure levels in France, and the second
an individual with high levels of exposure dueto their home address and lifestyle (high radon
exposure, ingestion of natural radionuclides, airtravel, smoking).
As mentioned previously (see the paragraph onradon exposure), it is important to consider thatthe radon contribution could shortly double dueto the ICRP's recommendation on how to assess
the impact of this radionuclide. In this case, radon
exposure would become clearly decisive for the
French population. Exposure incurred due to
medical operations must also be added to thisbackground radiation (see IRSN report 201500004 "Exposure of French citizens to ionisingradiation").

FIGURE 23 / EFFECTIVE DOSES ATTRIBUTABLE TO NATURAL RADIATION FOR 2 DIFFERENT EXPOSURE SCENARIOS (mSv/year)
Taken from IRSN report 2015-00004 "Exposure of French citizens to ionising radiation"

SCENARIO 1 : 1.6 mSv/year
Data for a non-smoking adult living in an area with low radon levels and a low level of telluric radiation, little affected by residual fallout,
eating food with low levels of natural radionuclides.

Residual fallout

CosmicIngestion

TelluricRadon

SCENARIO 2 : 8.6 mSv/year
Data for an adult who smokes and travels by air frequently, living in an area with high radon levels and a high level of telluric radiation,
substantially affected by residual fallout, eating large amounts of food with high levels of natural radionuclides.

Residual fallout

Ingestion

Cigarettes

CosmicTelluric

Radon
RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /73

Cattenom NPP

Gravelines

Channel centre
La Hague
Flamanville

Chooz

Penly

Cherbourg

PaluelCattenom
Fontenay-aux-Roses

SaclayBruyères-le-Châtel

Brest Île-Longue

Soulaines
Morvilliers

Nogent-sur-Seine

Brenillis

Fessenheim

Dampierre-en-BurlySaint-Laurent-des-EauxValducBelleville-sur-Loire
Chinon74

Civaux
Bugey

Creys-MalvilleSaint-Alban
Le Blayais

Grenoble

Romans-sur-Isère
Pierrelatte

Cruas-Meysse
Tricastin

Marcoule

GolftechCadarache
Malvési© A. Bouissou/MEDDE/IRSN

OPERATIONAL NUCLEAR
POWERPLANTS (NPP) UCLEAR POWERPLANTS IN
N
THE DECOMMISSIONING PROCESSRESEARCH SITESNUCLEAR NAVAL BASES

INDUSTRIAL SITESUranium conversion
Uranium enrichment
Production of fuel assemblies
Spent fuel processing and recycling
Surface storage of radioactive waste/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

ToulonO3DATA FORTHE DIFFERENT NUCLEAR
SITES IN FRANCE

3.1. O PERATIONAL NUCLEAR POWERPLANTS (NPP). . . . . . . . . . . . . . . . . . . . . . . . 76
Discharged radioactive effluents . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 77
Monitoring plans for the immediate environment of an NPP . . . . . . . . . . . . . . 78
The impact of NPP on their immediate environment
and associated public exposure. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 80
Conclusions . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 103
3.2. N UCLEAR POWERPLANTS IN
THE DECOMMISSIONING PROCESS. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 106
Creys-Malville site. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 106
Brennilis site. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 112
3.3. INDUSTRIAL SITES . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 116
Malvési site. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 116
Tricastin site . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 122
Romans-sur-Isère site. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 130
La Hague site. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 135
Aube storage centre and Morvilliers storage centre. . . . . . . . . . . . . . . . . . . . . . . . . 180
3.4. RESEARCH SITES . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 188
Marcoule site . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 188
Valduc site . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 199
Cadarache site . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 210
Grenoble sites. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 216
CEA DAM centre/Île-de-France region. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 224
Saclay site. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 229
Fontenay-aux-Roses site . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 238
3.5. NUCLEAR NAVAL BASES . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 244
Brest military port and Île-Longue operational base . . . . . . . . . . . . . . . . . . . . . . . 244
Cherbourg military port . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 244
Toulon military port . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 244
Radiological monitoring of the environment. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 245
Site impacts on the environment . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 248

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /

75

O3

DATA FORTHE DIFFERENT NUCLEAR
SITES IN FRANCE

3.1. OPERATIONAL NUCLEAR
POWERPLANTS (NPP)EDF SA is currently operating 19 nuclear
powerplants in France Each NPP includes 2 to 6
reactors, representing a total of 58 operational
reactors: 34 reactors with a unit power of
900 MWe, 20 reactors at 1,300 MWe and 4 reactors
at 1,450 MWe.

FIGURE 1 / LOCATION OF OPERATIONAL EDF NUCLEAR POWERPLANTS,
THOSE IN THE DECOMMISSIONING OR CONSTRUCTION PROCESS, NUMBER AND POWER OF OPERATIONAL REACTORS

76

900 MWe reactor
1,300 MWe reactor
1,450 MWe reactor

1,600 MWe reactor(construction in progress)
Reactors in the decommissioning process(UNGG, PWR, FNR)

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Operational Nuclear PowerPlants (NPP) / 3.1

Discharged radioactive effluents

However, actual discharges by operators
remain below, frequently significantly below, themaximum authorised discharge levels basedon optimisation and limitation policies. Tables 1
and 2 show the ranges (minimum and maximum
levels) for atmospheric and liquid discharges persite based on the number of reactors at the NPP
and their ratings, over the period covered by thisradiological report focusing on the environment.

Radioactive effluents are produced when
operating an NPP. Specific authorisation must
be obtained for each powerplant, defining theconditions for discharging these effluents into theenvironment. These effluents are discharged into
the atmosphere, rivers or at sea after radioactivity
levels have been checked/monitored. As per
regulations, each NPP has obtained specificauthorisation defining the volumes of radioactive
substances which can be discharged into the airor adjacent rivers or at sea and the applicableconditions, among other provisions.

If we consider the levels of activity discharged,
ignoring noble gases (xenon, argon and, above all,krypton, which are only found in the air and are nottransferred to other environmental components
as they are chemically inert), tritium andcarbon-14 represent the highest concentrations ofradionuclides in the effluents discharged, whether
atmospheric or liquid (see tables 1 and 2).

Discharge conditions must guarantee that public
exposure remains below 1 mSv/year in accordancewith article R.1333-8 of the French Public Health
Code in all normal operating conditions andranges, including worst-case operating conditions.

TABLE 1 / RANGES OF ANNUAL ATMOSPHERIC EFFLUENTS DISCHARGED PER YEAR (min. and max.) (GBq/year) FOR THE
PERIOD 2014-2016 DEPENDING ON THE POWER OF THE REACTORS INSTALLED AT EACH SITE

NPP

Noble gas

3

H

14

C

Iodines

FP/AP*

Gravelines

3 950-6 320

2 760-3 380

830-1 1300.113-0.152

0.013-0.021

Cattenom, Paluel

510-850

1 480-3 320

640-9100.034-0.048

0.007-0.011

Bugey, Cruas, Chinon,
Dampierre Tricastin, Blayais

430-7 250

620-1 740

410-6800.014-0.196

0.002-0.017

Civaux, Chooz

360-1 370

620-1 880

280-6700.015-0.146

0.001-0.005

Belleville, Flamanville, Golfech,
Nogent, Penly, St-Laurent

350-3 260880-2 290

280-6700.009-0.075

0.001-0.009

Fessenheim, St-Alban

120-4 710

630-910200-350

0.008-0.035

0.001-0.002* FP/AP: fission products / activation products: cobalt-60, cobalt-58, argent-110m, caesium-137, etc. (see glossary in chapter 8).

TABLE 2 / RANGES OF ANNUAL LIQUIDS DISCHARGED PER YEAR (min. and max.) (GBq/year) FOR THE PERIOD 2014-2016
DEPENDING ON THE POWER OF THE REACTORS INSTALLED AT EACH SITE

NPP

H

14

C

Iodines

FP/AP*

Gravelines

59,000-77,500

51.3-67.3

0.03-0.05

2.06-3.02

Cattenom, Paluel

52,800-122,000

30.0-68.2

0.01-0.02

0.64-2.10

Bugey, Cruas, Chinon, Dampierre Tricastin, Blayais

28,500-56,800

17.3-62.7

0.01-0.04

0.33-2.90

3

Civaux, Chooz

36,600-69,800

35.0-44.9

0.005-0.01

0.21-1.08

Belleville, Flamanville, Golfech, Nogent, Penly,
St-Laurent

38,800-72,500

15.2-44.4

0.004-0.02

0.17-0.70

Fessenheim, St-Alban

16,900-30,100

9.0-22.80.004-0.01

0.33-0.61* FP/AP: fission products / activation products: cobalt-60, cobalt-58, argent-110m, caesium-137, etc. (see glossary in chapter 8).

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /77

Monitoring plans for the immediate
environment of an NPP
EDF monitors discharges at source (before,
during and after discharge into the receiving
environment) and radioactivity in the immediate
environment of the sites for all operational
NPP. Only environmental monitoring provisions
are described in this document. EDF produces
approximately 50,000 measuring results for all
NPP each year.

In general, regulatory requirements relating
to environmental monitoring are defined in
ASN (French nuclear safety authority) decision
no. 2013-DC-0360 dated 16 July 2013 on controlling
disturbances and the effects of basic nuclear
facilities on health and the environment, amended
by ASN decision no. 2016-DC-0569 dated 29
September 2016, and by ASN decision no. 2017DC-0588 dated 6 April 2017, on water consumption
and sampling provisions, effluent discharges andenvironmental monitoring for pressurised water
reactors at nuclear powerplants. On this basis,these requirements are listed in the specificdecisions for each NPP.

TABLE 3-A / EXAMPLE OF A STANDARD MONITORING PLAN DRAFTED BY EDF (regulatory monitoring) AND BY IRSN

Environment
monitored or type of
testing

78

EDF

IRSN

• 4 daily measuring and sampling points for gross β activity
with a filter
Soil air• γ spectrometry if values > 2 mBq/m 3 andtotal for monthly filters• 1 continuous aerosol sampling station with aflow of 80 m 3/h with weekly γ spectrometry• 1 weekly tritium (3H) measurement under the prevailingwinds• 10 sensors around the edge of the site
• 4 sensors at a distance of 1 km and 4 at a distance of 5 km

• Up to 16 Téléray sensors within a radius of 10 to
30 km around the siteRain

• 1 bimonthly gross β and tritium measurement• 1 monthly tritium measurement

Terrestrial plants• 1 grass sampling point and monthly γ spectrometry,
HTO and OBT measurements Quarterly 14C andtotal C measurements• 1 leaf vegetable sampling run for 3H, 14C andγ spectrometry analyses

Ambient g radiation• Annual focus on agricultural output including
γ spectrometry and 14C, HTO and OBT measurements
Milk• 2 sampling points for monthly γ spectrometry, HTO, OBT
and 40K measurements and annual 14C measurements

Soils• 1 annual sampling run for γ spectrometry analysis

The receiving
environment for liquid
effluents discharged• 1 gross β measurement for suspended solids and 1 3H
measurement mid-discharge for NPPs located on rivers
or after dilution in cooling water, or bimonthly seawatermeasurements for coastal NPPs*

Aquatic flora

Aquatic fauna

Ground water• 1 annual cereal sampling run for 14C andγ spectrometry analyses• 1 6-monthly milk sampling run for 3H andγ spectrometry analyses• 1 monthly γ spectrometry measurement on
suspended solids (plus annual α, U, Sr, gross α
and gross β analyses for each drainage area)• 1 3H measurement in water mid-discharge for
NPPs located on rivers or after dilution incooling water for coastal NPPs

• 2 aquatic plant sampling runs (upstream and downstreamof NPPs located on rivers)• 1 annual sampling run for γ spectrometry and 3H (HTO)
analyses• 2 fish sampling runs (upstream and downstream of NPPs
located on rivers)• 1 annual sampling run for γ spectrometry, 14C and 3H (HTO)
analyses• 1 fish sampling run for annual γ spectrometry,
14
C and 3H (OBT) analyses• Monthly gross β and 3H analyses and samples* These samples and analyses are intended to ensure that discharges meet requirements rather than monitor the environment; this is particularly
true for coastal NPPs, where samples are taken in the discharge channel, and not in the actual environment, as is the case for NPPs on rivers.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Operational Nuclear PowerPlants (NPP) / 3.1

IRSN also monitors nuclear facilities in general, and
EDF NPP in particular, as part of its assignments(see table 3-A, column 2). Approximately 30,000
analysis results are produced on an annual basis
in this respect. Most of these results relate to air
and water, i.e. the receiving environment for theeffluents discharged.
EDF has organised annual monitoring basedon radioecological expertise at its NPP for over
25 years now, to complement the above monitoring
provisions. This radioecological monitoring is
also complemented with ten-year radioecologicalreports carried out by IRSN and SUBATECH.

Table 3-B shows a typical example of samples andanalyses in this context. Thanks to the use of moreadvanced metrological techniques, to match thetargets assigned to expertise-based monitoring,
complementing routine monitoring, combinedwith the appropriate biological indicators,
radionuclides (natural and artificial) in aquaticand terrestrial components, such as tritium andcarbon-14, can be identified.
Other radionuclides can be characterised on an
ad hoc basis, however it is important to take notethat the contents of terrestrial food are too low
to be measured, even using the most effective
available devices, with the exception of residual
caesium-137 from fallout from the Chernobyl
accident and/or the atmospheric testing of nuclear
weapons (see chapter 2).

TABLE 3-B / EXAMPLE OF A STANDARD SAMPLING AND ANALYSIS PLAN DRAFTED BY IRSN AND SUBATECH AS PART OF
ANNUAL RADIOECOLOGICAL MONITORING ON BEHALF OF EDF IN ADDITION TO THE REGULATORY MONITORINGDESCRIBED IN TABLE 3-A

79

Analyses
Environment

Terrestrial

Matrices

Spectrometry

Mosses and/or lichens2

Low-lying grasslands

1

Goat's or cow's milk

1

Drinking water supply
Aquatic
continental

Oceans2

Mosses and aquatic plants

3

Molluscs

free

bound

Carbon-14

Iodine 1312

11

Sediments

Algae

Tritium

2

2

2

2

3

3

3

3

2

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /The impact of NPP on their immediate
environment and associated public
exposure
It is easiest to characterise the impact of NPP
in the environment for carbon-14 and tritiumradionuclides due to their relative high activities
discharged and their extent to which they easilytransfer in the environment. Despite their low
radiotoxicity, these two radionuclides are the main
contributors to the potential exposure of residents
living near to these facilities.
The impact of effluents discharged into theatmosphere: carbon-14
Levels of carbon-14 in the immediate environment
around NPP due to atmospheric discharges are
low, however they can be detected thanks toadvanced analytical techniques. Carbon-14 content

80

was quantified during a series of measurements
taken by IRSN at Cruas from May 2015 to May 2016(see focus article, pp. 84-85). According to thesemeasurements, 14C activity in the air can reachlevels up to twice ambient background radiation
for this radionuclide at the south site fence, lessthan 1 km from the stack on the leeward side.
However, including for an individual living at this
precise location all year round, the dose inhaled
due to this added atmospheric carbon-14 activity
is insignificant: approx. 0.001 μSv/year.
As explained in the focus article, only one third of
EDF discharges take the form of CO2 likely to beabsorbed by plants during photosynthesis. The 14C
activity added from atmospheric discharges from
NPP into the terrestrial environment is too low to
be quantified by measuring activity by mass. This
activity can only be measured using the specificactivity of 14C expressed as Bq/kg of carbon.

FIGURE 2 / VARIATION IN THE SPECIFIC ACTIVITY OF 14C (Bq/kg of carbon) MEASURED IN 2014-2016
IN VARIOUS TERRESTRIAL ENVIRONMENTAL COMPONENTS NEAR TO THE SAINT-ALBAN, CRUAS AND PALUEL NPPS,
BASED ON DISTANCE FROM SITE DISCHARGE POINTS

Bq/kg of carbon
270
265
260
255
250
245
240
235
230

227 Bq/kg of C.

225
220

0

5

10
15
20
Distance to the site in km

25

Cruas Grass and tree leaves
Cruas Milk
Cruas Plant-based food

Paluel Grass and tree leaves
Paluel Milk
Paluel Plant-based foodBackground radiation range

St-Alban Grass and tree leaves
St-Alban Milk
St-Alban Plant-based food

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 201730

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Operational Nuclear PowerPlants (NPP) / 3.1

This indicator is highly sensitive and can beused to identify weak local effects (see chapter
1, focus article p. 32 and chapter 2). This
indicator is measured around NPP as part ofenvironmental monitoring by IRSN and as part of
the radioecological monitoring of sites by IRSN
and SUBATECH at the request of EDF.
Figure 2 shows variation in the specific activity of
14
C measured in the various terrestrial components
near to the Cruas, Saint-Alban and Paluel NPPs,
based on distance from the site. At a distanceof between 1 and 2 km, the activity added fromdischarges reaches a mean value of + 8%, and canoccasionally reach + 15 to + 20% of backgroundradiation (BR = 227 Bq/kg of C over the 20142016 period; see chapter 2), which matches theairborne results described previously (BR + 36%
at a distance of less than 1 km). Activity also varies
the most within a short distance from the site: 224- 268 Bq/kg of C. Specific activity then decreases
with distance until it reaches background radiationlevels at 10 - 15 km. In general, this decrease iseasiest to detect from the measurements taken
for all types of plants. Milk analysis results reflect
the source of the feed supplied to the animals
and their drinking water. However, the activities
measured in milk are still consistent with plant
analysis results.

which corresponds to a mean activity by massadded of + 0.3 Bq/kg fresh for a lettuce, + 0.7 Bq/
kg fresh in fruit or cow's milk, + 2 Bq/kg fresh inbeef and up to + 4 Bq/kg fresh in cereals.
The extra activity added within a radius of 10 km,
determined using 206 measurement results, will
also be lower: +7 Bq/kg of C, or BR +3%.
Local residents are mainly exposed to atmospheric
14
C discharges via the potential consumption offood grown locally due to the physical properties ofthis radionuclide. If we consider the food intake andpercentage of food grown locally as per the figuresin chapter 8, doses attributable to 14C absorbed byeating food grown within a radius of 5 km aroundan NPP are estimated at 0.075 µSv/year, comparedwith 0.05 µSv/year when grown within a radiusof 10 km around an NPP. These estimates are
similar to the figures calculated by EDF based ondischarges from 2016. For information, a figureof 0.026 μSv/year was calculated for Cruas and0.023 µSv/year for Gravelines. These estimates
corroborate the figure of 0.1 µSv/year indicatedin the previous Radiological report (2011-2014),
which had been established on the basis of a moregeneral approach using measurements taken
between 1994 and 2004 and assuming that all foodeaten was grown near to the sites.

The activity by mass of carbon-14 added to fresh
food due to effluents discharged from NPP canbe deducted from the total specific activity added
to the environment. On this basis, the mean
specific activity added represents + 11 Bq/kg of C,© EDF/Media library

The mean specific activity added within a radiusof 5 km around an NPP, determined based on 348
measurement results acquired during the 20142016 period at 19 EDF sites, is equal to + 11 Bq/
kg of C (or BR + 5%). The highest activity levels
measured around the Tricastin site were not used
to calculate this mean value to avoid bias due todischarges from other facilities, in addition to the
NPP. It is also important to take note that thismean specific activity added to the environment
is conservative due to the larger amount of dataobtained in the immediate vicinity of the sites(< 2 km).

81

Saint-Laurent-des-Eaux NPPRADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /The impact of effluents discharged into theatmosphere: tritium
Tritium in atmospheric water vapour (HTO in theair) is analysed on a weekly basis in the immediate
vicinity of each of the 19 NPPS as part of regulatory
monitoring. For 99% of the 2,694 samples takenover the 2015-2017 period, activity levels are too
low to be measured with the test methods used
for routine monitoring, however it would appear
that activity is less than 0.25 Bq/m3. This value
should be compared with the regulatory limit of
50 Bq/m3. Over this 2015-2017 period, activity
measurements peaked at 0.43 Bq/m3 during
the 1st week of June 2017, near to Tricastin. In
general, all of the data acquired since 2011 imply
that tritium activity in the air reaches its highest
value near to the Tricastin site (figure 3). There are
two reasons for this distribution:• other industries also discharge tritium at the
Tricastin nuclear site;82• the site is near to the Marcoule centre, which
had some of the highest discharge levels in
France until recently.

Tritium content in the air due to an NPP could only
be quantified during a series of expertise-based
measurements taken by IRSN at the Cruas site
between May 2015 and May 2016 (see focus article).
According to the results, activity by volume at a distanceof less than 1 km on the leeward side of the discharge
point are generally between 0.03 and 0.1 Bq/m3,
with a mean value of 0.07 Bq/m3. These activity
measurements match the values obtained by EDF
and are indeed often too low to be quantified during
routine monitoring. However, this value, measured
in the immediate vicinity of the NPP, is 7 times higher
than background radiation for this radionuclide.
According to the study carried out at Cruas, thetritium in the water vapour (HTO), measured as partof routine monitoring by EDF, represented 86% of
the tritium released. The dosimetric impact andactivities of the other forms of tritiated hydrogen(HT) and tritiated methane (CH3T) in the air wereconsiderably less. Despite this, for an individualliving at this precise location all year round, thedose inhaled or absorbed transcutaneously due tothis added atmospheric tritium activity represents
approximately 0.007 μSv/year.

FIGURE 3 / TRITIUM ACTIVITY IN ATMOSPHERIC WATER VAPOUR NEAR TO THE TRICASTIN SITE (Bq/m3) MEASURED AS
PART OF REGULATORY MONITORING SINCE 2009

Bq/m 3
1.4
1.2
1
0.8
0.6
0.4
0.2
0
July-09 July-10 July-11 July-12 July-13 July-14 July-15 July-16 July-17
Decision thresholds

Measuring result/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Operational Nuclear PowerPlants (NPP) / 3.1

This estimate corroborates the value calculated by
EDF on the basis of effluents discharged in 2016,of 0.0024 μSv/year, although the figure is slightly
higher as the station is located less than 1 km
from the discharge point while EDF's estimate
refers to the control group (see chapter) located in
the municipality of Savasse 3.5 km from the site.
Tritium in water vapour is transferred to plants
during photosynthesis. The activity added to theair, in this form, from NPP discharges, will thenlead to a local increase in activity in plants andin the rest of the downstream food chain. This
increase can also be detected by measuringorganically-bound tritium (OBT) activity in all
biological environmental components. This OBT
activity is measured in various plant samples,particularly leaf vegetables, and in milk samples
taken near to NPPs as part of the radioecologicalmonitoring of sites by IRSN and SUBATECH at therequest of EDF.
The mean organically-bound tritium (OBT) activity
for the samples taken less than 5 km from thedischarge points, determined over the 2014-2016

period using 95 sample results for the immediate
environment of the 19 NPP, is equal to 2.6 Bq/L.
This value is within the current backgroundradiation range, which fluctuates from less than 1
to 3 Bq/L. However, this value can be differentiatedfrom mean background radiation, estimated as
1.3 Bq/L. As shown in figure 4, beyond a distanceof 10 km, tritium activity determined using 74
measurements, drops to the range of backgroundradiation with a mean value of 1.4 Bq/L if effluentsare discharged in the vicinity, versus 1.3 Bq/L withno additional discharges. As is the case with 14C,
the decrease in activity with distance cannot be
identified based on activity measured in milk,
which reflects the source of the feed supplied tothe animals and their drinking water.
In the same way as carbon-14, local residents aremainly exposed to atmospheric tritium discharges
via the potential consumption of food grown locally.
If we consider the food intake and percentage offood grown locally as per the figures in appendix
8 to chapter 8, the dose of tritium absorbed byeating food grown within a radius of 5 km aroundan NPP is estimated at 0.003 µSv/year.

FIGURE 4 / VARIATION IN TRITIUM ACTIVITY IN ORGANIC MATTER (Bq/L of combustion water) MEASURED IN 2014-2016 IN
VARIOUS TERRESTRIAL ENVIRONMENTAL COMPONENTS NEAR TO THE 19 NPPS, BASED ON DISTANCE FROM SITEDISCHARGE POINTS

Bq/L
8
7
6
5

Activity measured in plants
Activity measured in milk
Mean value for 36 samples taken less than 2 km from NPPs: 3.0 Bq/L
Mean value for 95 samples taken less than 5 km from NPPs: 2.6 Bq/L
Mean value for 156 samples taken less than 10 km from NPPs: 2.0 Bq/L
Mean value for 74 samples taken less than 10 km from NPPs: 1.4 Bq/L
Range and mean value for the 52 samples taken as representative of
background radiation: 1.3 Bq/L

4
3
2
1
0

0
5
10
15
20
25
30
Distance from site discharge sites (i.e. discharge stack) in km

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /83

FOCUS ARTICLESTUDY OF ATMOSPHERIC
RADIOACTIVITY LEVELS FOR CARBON-14 AND
TRITIUM NEAR TO THE CRUAS-MEYSSE NPP

Although NPP mainly discharge tritium andcarbon-14, advanced metrological techniques are
required to quantity their activity in the air. These
techniques cannot be used for routine monitoring.
IRSN installed two sampling devices designed foratmospheric carbon-14 and tritium between May
2015 and May 2016 as part of an atmospheric characterisation programme organised to the southof the Cruas-Meysse site and at the same time as analyses on aerosols (see focus article below).

Two bubbler type samplers (SDEC) were used for the purposes of liquid scintillation analyses fortritium (MARC 7000) and carbon-14 (HAG 7000). These bubblers were installed in the immediate
vicinity of the site, less than 1 km from the discharge points (as per figure A). Bimonthly samples
were taken. By combining these devices with advanced metrological techniques, the different
chemical forms of these radionuclides in the ambient air can be studied: mainly CO2 and CH4 forcarbon-14, HTO (tritiated water vapour) and HT (tritiated hydrogen) for tritium.
FIGURE A / LOCATION OF THE 3H AND 14C BUBBLERS SOUTH OF THE CRUAS-MEYSSE NPP

84

Carbon-14 activities measured during this study represented between 0.042±0.018 Bq/m3 and
0.25±0.023 Bq/m3 (figure B) with a mean value of 0.095 Bq/m3, which is approximately double
background radiation levels for this radionuclide (0.047 Bq/m3 with zero discharges). These results
corroborate the total activity measurements by added volume calculated by the operator. The 14C inthe samples is mainly found as dioxide (14C02=67.4% of total atmospheric carbon-14 on average).
However, only 27% of this 14C02 is attributable to NPP discharges, the rest is all natural. This
percentage of 14C02 added by NPPs can be assimilated by plants during photosynthesis, which
explains the low levels detected in plants in the immediate vicinity of EDF NPPs. However, the mainradionuclide in site discharges is CH4 (64% of all carbon-4 discharged), which represents almost allof this form measured in the air as the percentage of 14CH4 attributable to ambient backgroundradiation is very low (approx. 0.0002 Bq/m3 vs. 0.031 Bq/m3 of 14CH4 actually measured).

●●●/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Operational Nuclear PowerPlants (NPP) / 3.1●●●

FIGURE B / 14C02 AND 14CH4 ACTIVITY MEASURED IN THE AIR TO THE SOUTH OF THE CRUAS-MEYSSE NPP
BETWEEN MAY 2015 AND MAY 2016
Bq/m 3
0.3

Carbon-14 as CO 2

Carbon-14 as CH 4

0.25
0.2
0.15
0.1
0.05

26
/0
09 5-0/0 9
2 3 6-2 /06/0 3
07 6-0 /06/0 7
22 7-2 /07/0 2
06 7- 0 /07/0 6/
03 8-0 08/0 3
15 9-1 /09/0 5
2 9 9-2 /09/ 9
13 09-1 /09/ 3
2 9 10 -2 /10/ 9
12 10 -1 /10/ 2
24 11-2 /11/ 4
0 8 11- 0 /11/ 8
17 12-1 /12/1 7
05 2- 0 /12/ 5
19 01-1 /01- 0 9/
0 2 1/ 0 0 1/ 2
16 02-1 /02/0 6
01 2- 0 / 0 2/0 1
08 3-0 /0 3
/0 8
15 3-1 /0 3
/0 5
2 9 3-2 /0 3
/0 9
12 3-1 /0 3
/0 2 /
4- 0 426/0
40Tritium activities measured during this study represented between 0.036±0.004 and 0.124±0.007
Bq/m3 (figure C). Facility discharges multiply background radiation with no additional inputs,
which is around 0.01 Bq/m3, by approximately 7. These tritium activity measurements, mainlyreferring to HTO water vapour (≈ 86%) and attributable to NPP discharges, corroborate themeasurements taken in the different terrestrial components.
The other forms of ambient tritium measured (HT and CH3T) represent very small amounts andfail to or barely contaminate the environment as they are not assimilated during photosynthesis byplants.
FIGURE C / HTO AND HT-CH3T ACTIVITY MEASURED IN THE AIR TO THE SOUTH OF THE CRUAS-MEYSSENPP BETWEEN MAY 2015 AND MAY 2016
Bq/m 3
0.14

Tritium as HTO

Tritium in other forms (HT, CH 3T, etc.)

0.12
0.1
0.08
0.06
0.04
0.02

26
/0
09 5-0/0 9
2 3 6-2 /06/0 3
07 6-0 /06/0 7
22 7-2 /07/0 2
06 7- 0 /07/0 6/
03 8-0 08/0 3
15 9-1 /09/0 5
2 9 9-2 /09/ 9
13 09-1 /09/ 3
2 9 10 -2 /10/ 9
12 10 -1 /10/ 2
24 11-2 /11/ 4
0 8 11- 0 /11/ 8
17 12-1 /12/1 7
05 2- 0 /12/ 5
19 01-1 /01- 0 9/
0 2 1/ 0 0 1/ 2
16 02-1 /02/0 6
01 2- 0 / 0 2/0 1
08 3-0 /0 3
/0 8
15 3-1 /0 3
/0 5
2 9 3-2 /0 3
/0 9
12 3-1 /0 3
/0 2 /
4- 0 426/0
40Precise tritium and carbon-14 levels were measured
in the ambient air in the immediate vicinity of an NPP directly due to atmospheric discharges
from the facility. These levels are indeed lower than those measured during routine monitoring
and well below the decision thresholds defined in regulations and applicable to the operator. These
results also confirmed the dominance of HTO for tritium and CH4 for carbon-14 in NPP
discharges.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /85

The impact of effluents containing otherradionuclides discharged into the atmosphere

Once the radioactive aerosols have been released
into the air, they fall back to ground level andcan be absorbed by plants. However, plant
activity levels are too low to be measured, evenusing the most advanced techniques available.
However, activity in food grown locally can beassessed using airborne activity measurements.
In this way, if we consider the foodstuffs with thehighest sensitivity to atmospheric fallout, such asleaf vegetables (lettuce, spinach, etc.), activities
remain below 1 mBq/kg fresh for all of the above
radionuclides; these levels are well below thedetection limits for the most effective metrological
techniques (approx. 3 - 10 mBq/kg fresh for60
Co, 58Co and 110mAg). Added 137Cs activity cannot be
differentiated from residual fallout (see chapter),de facto demonstrating the low impact of NPP on
ambient levels for this radionuclide.

© DR

86

The activities of the other radionuclides in theeffluents discharged represent approximately
10,000 - 100,000 times less than tritium andcarbon-14 activities. These radionuclides mainly
include the radioactive isotopes of iodine,caesium-134 and 137, cobalt-58 and 60 andsilver-110m. The activities of these radionuclides
in the air or the terrestrial environment are
far too low to be measurable as part of routine
monitoring by EDF or IRSN. However, thanks torecent metrological developments, IRSN has beenable to perform expertise-based measurementsof these radionuclides in atmospheric aerosols(see focus article) near to some NPPs. The
results of measurement runs at the Cruassite from May 2015 to May 2016, and data
currently being obtained (since May 2017) at theGravelines NPP, confirm the figures acquiredat the Tricastin site in the 2012-2013 period.
Activities range from under 0.1 µBq/m3 to over
1 µBq/m3 for the four radionuclides measured
on a regular basis (58Co, 60Co, 110mAg and 137Cs).
Although the effluents discharged by the otherfacilities at the Tricastin site only represent about
a tenth of the NPP discharges, they contribute to
the activities measured and cannot therefore be
attributed to the NPP alone. On the other hand,
the location of the station set up at Cruas is optimalin terms of the prevailing local weather conditions,
implying that the activity levels measured at thissite are representative of the highest activities likely
to be reached due to effluents discharged from an
operational NPP. Despite higher discharge levels
from the Gravelines site, activity measurements
are lower than at Cruas due to more consistentwind characteristics.

Local populations are exposed to the radionuclides
characterised via inhaling, as well as external
exposure due to the radiation emitted by someradionuclides in the air. A person living at the
precise location of the sampling stations would
absorb a dose well below 0.001 μSv/year, almost
exclusively by inhaling. External exposure
would only represent a few percent. This doseis insignificant and corroborates the figure
calculated by EDF based on discharges from 2016.

Fishing on the Garonne river downstream from the Golftech NPP/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Operational Nuclear PowerPlants (NPP) / 3.1

FOCUS ARTICLESTUDY OF THE RADIOACTIVITYLEVELS OF ATMOSPHERICAEROSOLS NEAR TO EDF NPPSIn addition to regular monitoring, IRSN measures
the activity of atmospheric aerosols near to
nuclear powerplants as part of specific studies
organised in coordination with EDF. Four
campaigns have been carried out since 2011,near to the Golfech (July 2011 - April 2012),
Cruas-Meysse (May 2015 - May 2016), Gravelines (since May 2017, see figure A), and Tricastin
NPPs. This latter site is home to other nuclear facilities, in addition to the NPP (January 2012 August 2013). An atmospheric aerosol sampler with a high flow rate (300 m3/h) was installed foreach of these studies. The sampler operates 24/7 and complements EDF's systems installed in theimmediate vicinity of sites as per regulations.
Thanks to the performance levels of the sampling system and the associated laboratory metrology
techniques, very low levels of radioactivity can be measured: approx. 0.01 µBq/m3, which meetsthe targets of the set study.
FIGURE A / LOCATION OF IRSN AEROSOL COLLECTION STATIONS NEAR TO 4 EDF NPPS (source: airborne
images from the geoportail)87

Scale: 1:17055

Scale: 1:17055

Scale: 1:17055●●●

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /●●●In addition to natural radionuclides (7Be, 40K, 22Na, 210Pb, etc.) with similar activity levels to thosemeasured in areas unaffected by the atmospheric discharges of the facilities, thanks to the dataobtained in these measuring runs and the performance levels of the (sampling and metrology)
systems used, the activities of the radionuclides in NPP atmospheric discharges can be quantified(figure B).
FIGURE B / ACTIVITIES OF THE MAIN ARTIFICIAL RADIONUCLIDES MEASURED BY IRSN DURING THE 4
MEASURING CAMPAIGNS ORGANISED NEAR TO EDF NPPS
137
Cs
Activity measurement
Decision threshold

10

Golfech110m
Ag
Activity measurement
Decision threshold

58
Co
Activity measurement

60
Co
Activity measurement

Decision threshold

Decision threshold

Cruas-Meysse

Tricastin

GravelinesµBq/m 3

1

Jul-17Oct-17

Apr-17Jan-17

Jul-16Oct-16

Apr-16

Jan-16

Jul-15Oct-15

Apr-15Jan-15

Jul-14Oct-14Apr-14Jan-14Jul-13Oct-13Apr-13Jan-13

Jul-12Oct-12

Apr-12Oct-11

0.01

Jan-12

0.1

Jul-11

88

Residual caesium-137 from fallout (from the atmospheric testing of nuclear weapons and theChernobyl accident) is routinely measured by IRSN at 10 samplers with high flow rates (700 m3/h)
located outside of areas affected by atmospheric discharges from nuclear facilities.
This radionuclide can also be detected in atmospheric discharges from NPPs and was the mostfrequent artificial radionuclide measured during these studies (76 - 100% of filters). These activity
levels vary between 0.03 and 1.62 µBq/m3, with the highest measurements recorded for the
sampler filters in the Rhône valley, the area the most affected by fallout from the Chernobyl
accident. 137Cs activity levels fluctuate to match fluctuating 40K and dust levels, mainly due tonatural phenomena (mineral dust on the ground raised into the air, pollen, forest fires, etc.), but
do however remain well above background radiation levels in areas unaffected by discharges.
110m
Ag, 60Co and 58Co are the other main radionuclides measured. These radionuclides, which are
typically found in atmospheric discharges by NPP, along with iodines, are the most frequently
detected fission and activation products in NPP discharges (after tritium and carbon-14), despite
filters. The activity levels measured during these studies, for these three radionuclides, vary
between 0.03 and 5.2 µBq/m3 (table A) and corroborate the activity levels calculated by theoperator based on dispersal.
●●●/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Operational Nuclear PowerPlants (NPP) / 3.1●●●

TABLE A / ACTIVITIES OF THE MAIN ARTIFICIAL RADIONUCLIDES MEASURED BY IRSN DURING THE 4
RADIOACTIVITY STUDIES FOCUSING ON ATMOSPHERIC AEROSOLS NEAR TO EDF NPPS

Activity in µBq/m3

137

Cruas-Meysse NPP

Cs

0.12 – 1.62

Number of filters (out of 49)
Frequency of detection
Tricastin site

110m

Ag

58

0.047 – 0.96

Co60

0.03 – 2.8

Co

0.04 – 0.41

49

30

24

22

100%

61%

49%

45%
0.1 – 5.2

0.07 – 1.59

0.07 – 4

0.08 – 4.4

Number of filters (out of 75)

69

22

19

30

Frequency of detection

92%

29%

25%

40%
0.61

Golfech NPP

0.05 – 0.6

0.76

0.18 – 1.2

Number of filters (out of 24)

20

1

2

1

Frequency of detection

83%

4%

8%

4%
0.06 – 1.34

Gravelines NPP

0.03 – 0.18

0.05 – 0.13

0.04

Number of filters (out of 21)

16

5

1

12

Frequency of detection

76%

24%

5%

57%

The activities measured near to the Golfech (2 x 1 300 MWe reactors) and Gravelines (6 x 900
MWe reactors) NPPs for the 4 target radionuclides, were measured the least frequently and gavethe lowest peak values. On the other hand, the activities measured near to the two NPPs in the
Rhône valley (4 x 900 MWe reactors) were measured the most frequently and gave the highest
peak values. Given that all samplers were installed at point AS1 at each NPP, at the distancerequired by regulations from the discharge point(s), based on the prevailing winds, it would
appear that activity measurements depend on the radionuclides discharged, but also on thelocation of the equipment and its exposure to discharges, which fluctuates based on local windconditions. If we consider the Cruas-Meysse site (or the Tricastin site), wind direction is very
regular and generally comes from the north, with little variation. On this basis, the sampler ismainly affected by discharges from the facility. If we compare with the Gravelines site (or the
Golfech site), wind is far more variable, and the percentage of discharged effluents reaching thesampler will fluctuate substantially.
Other radionuclides have also been measured near to the Tricastin site (54Mn, 95Zr, 95Nb, 124Sb, 51Cr
and 57Co), however far less frequently (for 1 to 12% of filters) (table B). These radionuclides were
measured during both maintenance operations (with the reactor shut down) and during
production phases, although levels appear higher when the reactor is shut down. Effluentsdischarged from other facilities at the site probably increased the activity measured for theseradionuclides to above the detection threshold. Note: 95Zr and 95Nb activities were also measured
at a filter at the Gravelines station, giving results of 0.6 and 1 µBq/m3 respectively.
TABLE B / OTHER ARTIFICIAL RADIONUCLIDES MEASURED DURING IRSN STUDIES AT POINT AS1 AT THE
TRICASTIN SITE

Activity in µBq/m3

54

Mn

95

Zr

95

Nb

124

Sb

Cr

51

57

Co

Tricastin site
(January 2012
to August 2013)0.08 – 0.9

0.28 – 1.47

0.39 – 3.0

0.24 – 0.4

2.5 – 3.4

0.06

Number of filters(out of 75)

9

4

4

2

2

1

Frequency of detection

12%

5%

5%

3%

3%

1%

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /89

The impact of carbon-14 in liquid effluentsdischarged
Carbon-14 activity in fish upstream anddownstream of all NPPs is analysed on anannual basis, by IRSN as part of its monitoring
programme, and by IRSN and SUBATECH at therequest of EDF as part of annual radioecologicalmonitoring.
The monitoring results obtained as part of thetwo programmes demonstrate that carbon-14
activity in fish in French rivers, where NPPs
discharge carbon-14 in liquid effluents, leads toan increase in the activity by mass of fish in therivers in question, however this increase varies
substantially.

90

On this basis, 14C activity in fish fluctuates overthe entire length of the Rhône river depending on
effluents discharged from the nuclear facilities
installed on this river, particularly NPPs on the
Rhône river, and due to varying levels of dilution
by river flow, particularly when tributaries join themain river. Figure 5 shows this variation in activity
over the length of the Rhône river and highlights
how activity is stable over time, by comparing 2
periods: 2001-2011 and 2012-2016.

Upstream from the Bugey site, at BrégnierCordon or Sault-Brenaz, activity measurementsfrom 2016 are in the background radiation range
for 14C in French freshwater fish: 22 - 29 Bq/kg
with a mean value of 24 Bq/kg fresh (see chapter2). Mean activity in fish captured downstream
from the Bugey NPP represented 33 Bq/kg fresh
over the 2012-2016 period, which is a + 9 Bq/kg
increase over mean Background Radiation (BR).
Assuming an annual fish consumption of 1.3 kg,
which corresponds to the catch of an amateur
fisherman, the dose corresponding to this added
activity would be equal to 0.007 μSv/year. This
figure would reach 0.03 μSv/year for people eatingsuch fish more regularly (5.3 kg/year). 14C activity
at Chavanay, upstream from Saint-Alban, is similar
to the level of background radiation due to dilution,
particularly as the Ain and Saône rivers join themain river. Mean 14C activity in fish increases due
to discharges from the Saint-Alban, Cruas andTricastin NPPs, ranging up to 105 Bq/kg fresh(BR + 81 Bq/kg fresh) after Cruas over the 20122016 period, and 113 Bq/kg fresh (BR + 89 Bq/kg
fresh) at Mornas downstream of Tricastin overthe 2001-2011 period. These activity increases
correspond to doses of approximately 0.06
to 0.07 μSv/year for occasional consumers (1)FIGURE 5 / VARIATION IN CARBON-14 ACTIVITY IN FISH (Bq/kg fresh), OVER THE FULL LENGTH OF THE RHÔNE RIVER, ON
THE BASIS OF MEASUREMENTS TAKEN OVER THE 2001-2011 PERIOD (shown in blue) AND OVER THE 2012-2016 PERIOD(shown in red)

Mean, min. and max. values over the 2001-2011 period(1)Mean, min. and max. values over the 2012-2016 period

Bq/kg fresh
180
160
140

Viviers

Mornas Caderousse

120
100

Livron

80
60
40

Arles
Brégnier-Cordon

SaultBrenaz

Villetted’Anthon
Chavanay

AlbaronBackground radiation range

20
0

Sablons

Upstream Creys (2)
Rhône

Bugey

St-Alban Valence Cruas Tricastin Marcoule Avignon Camargue
Lyon
Saône/Ain
Isère
DuranceRhône river flow

1. Prior to 2009, data only existed for some years (ten-year reports and specific studies)2. The location of this site is indicated for information only; carbon-14 discharges are not authorised here.
/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Operational Nuclear PowerPlants (NPP) / 3.1(1.3 kg/year) and 0.2 - 0.3 μSv/year for regularconsumers (5.3 kg/year). 14C activity in fish willreach the level of background radiation with
distance and when diluted in Durance riverwater, particularly for the Camargue, where theimpact of discharges from the nuclear facilities
on the Rhône approximates background radiation:
30 Bq/kg fresh (BR +6 Bq/kg fresh).

The liquid effluents discharged from the Belleville,
Dampierre and Saint-Laurent NPPs increase
this activity, which reaches approximately
60 Bq/kg fresh between Saint-Père-sur-Loireand Muides-sur-Loire. This activity adds +35
Bq/kg to background radiation levels, which
would give the following doses: 0.03 μSv/year
for occasional fish consumers (1.3 kg/year) and
0.1 μSv/year for regular fish consumers (5.3 kg/year). 14C fish activity is diluted by the Cher river(among other less significant inputs), falling to
44 Bq/kg fresh (or BR +20 Bq/kg) at Saint-Martin
island, before increasing again due to the liquid
effluents discharged at Chinon to 54 Bq/kg fresh(BR +30 Bq/kg fresh) near to Chouzé-sur-Loire.

C measurements in fish captured in the Loireriver vary in a similar manner for the 20082012 and 2013-2015 periods (see figure 6).
At Sury-Pré-Léré, upstream from the Belleville
NPP, where a mean activity of 26 Bq/kg fresh wasrecorded over the 2013-2015 period, 14C activity
in fish remains at background radiation levels.
14

FIGURE 6 / VARIATION IN CARBON-14 ACTIVITY IN FISH (Bq/kg fresh), OVER THE FULL LENGTH OF THE LOIRE RIVER, ON
THE BASIS OF MEASUREMENTS TAKEN OVER THE 2008-2012 PERIOD (shown in green) AND OVER THE 2013-2015 PERIOD(shown in red)

Mean, min. and max. values over the 2013-2015 period
Min. and max. values over the 2008-2012 period

Bq/kg fresh
100Saint-Père-sur-Loire

90

Muides-sur-Loire

80
70

Châtillon-sur-Loire

Tavers60
50

Chouzé-sur-LoireÎle St-Martin

Montoire

40
30

Sury-pré-Léré

Background radiation range

20
10
0

Orléans

Belleville NPP

Dampierre NPP

ToursSaint-Laurent NPP Cher

Chinon NPP

Loire river flow

1. Note: fishing is partially prohibited in various sections of the Rhône river due to chemical pollution unrelated to NPPs.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /

91

92

Figure 7 compares 14C activities in fish upstream
and downstream from a few NPP since 2012. This
figure shows how the flow rate of the receiving rivers
affects fish activity by diluting/dispersing the liquid
effluents discharged by NPP. Fish were captured
downstream from discharge points. With the
exception of the samples taken for Golfech in 2013,
all of the activities in fish samples taken upstreamof NPP are within the background radiation range.
This exception does highlight how fish can travel
both upstream and downstream from discharge
points. Activity measurements downstream ofsites vary substantially and depend directly on river
flow rates. The Garonne river flows fast enough tomaintain activity levels downstream from Golfech
at similar levels to (or lower than) those detected
for the Loire river in an earlier study. On the other
hand, 14C activity levels in fish captured in the
Moselle and Vienne rivers downstream from theCattenom and Civaux sites are higher than thosemeasured at downstream locations on the Rhône,
where discharges from various sources aggregate:
168 Bq/kg fresh on average downstream fromthe Cattenom NPP (BR + 144 Bq/kg fresh) and
137 Bq/kg fresh downstream from the Civaux NPP(BR + 113 Bq/kg fresh).

However, despite these activity levels, which arehigher than those mentioned above, the doses
absorbed by eating these fish remain extremely
low: 0.1 μSv/year for occasional consumers and0.4 μSv/year for regular consumers. For
information, the dose absorbed when eating fish
captured downstream from the Cattenom NPP, ascalculated by EDF based on discharges from 2016,
is equal to 0.2 μSv/year.
In general, the mean dose absorbed by eating fishcontaminated by the liquid effluents discharged
from NPPs containing 14C, covering all sites, forthe regular consumption of 5.3 kg of fish per year,
was estimated at 0.12 μSv/year in the previous
radiological report (2011-2014). This figure wasconfirmed for the 2014-2016 period, estimated at
0.15 μSv/year, which is extremely similar to theprevious value. The 14C contribution discharged
by NPPs to the dose absorbed after eating one kg
of fish still only represents 1% of the total doseof 12 μSv/year due to the natural radioactivity offish (see page 70 of the radiological report for the
2011-2014 period).

FIGURE 7 / SPECIFIC ACTIVITY FOR 14C (Bq/kg of carbon) MEASURED SINCE 2012 IN FISH CAPTURED UPSTREAM AND
DOWNSTREAM OF THE CATTENOM, CHOOZ, GOLFECH AND CIVAUX NPP

Bq/kg fresh
250
Upstream from Cattenon
Downstream from Cattenom

200

Upstream from Chooz
Downstream from Chooz
Upstream from Golfech
Downstream from Golfech

150

Upstream from Civaux
Downstream from Civaux

100

Background radiation range
50

0
Apr-2012

Apr-2013

Apr-2014

Apr-2015

Apr-2016

Apr-2017/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Operational Nuclear PowerPlants (NPP) / 3.1

The impact of liquid discharges containing
tritium
Most of the tritium detected in river water
downstream from NPPs was added by the liquid
effluents discharged from the facilities. Residual
fallout from the atmospheric testing of nuclear
weapons combined with natural cosmogenic
tritium (see chapter 2) gives a total "backgroundradiation" of approximately 1 - 3 Bq/L. The
activities measured for samples collected using
a permanent IRSN sampling system (2) are due tothe effluents discharged from each site, the river
flow rate and therefore its ability to disperse theeffluents, and, for sites located downstream fromother sites, combined effluents (figures 8, 9, 10
and 11 show variation over the years and table 4shows mean values for the last 3 years).

On this basis, the lowest mean annual activities
are measured in the Alsace canal and in the Rhône
river, despite the number of facilities discharging
this radionuclide into these rivers: 3 Bq/L in the
Alsace canal downstream from Fessenheim,
6 Bq/L downstream from St-Alban and up to
11 Bq/L downstream from Bugey (near to the
Bugey NPP, the main Rhône tributaries have notyet joined the main river and flow rate is a mere
450 - 600 m3/s). Activity levels in the Loire riverare fairly homogeneous and range from 14 Bq/L
downstream from Belleville to 21 Bq/L downstream
from Dampierre. The highest mean activities were
measured at locations with the weakest flow rates:from 22 Bq/L on the Vienne river downstream from
Civaux to 35 Bq/L on the Seine river downstream
from Nogent. These figures are below regulatory
limits and approximately 300 to 3 000 times lessthan the WHO's guide value for tritium in drinking
water (10,000 Bq/L).

FIGURE 8 / MEAN ANNUAL TRITIUM ACTIVITY FOR LOIRE RIVER WATER DOWNSTREAM FROM THE BELLEVILLE,DAMPIERRE, CHINON, SAINT-LAURENT AND CIVAUX NPPS (Bq/L)
According to recurrent mean annual tritium activity measurements, as taken by IRSN from the Loire river water since the 1980's, liquid
tritium discharged from EDF NPPs has remained stable since the first decade of the 21st century. Higher activity levels were also
recorded downstream from the Chinon site up to 2000. After 2000, mean annual activity varied less from year to year. This may bepartially due to the fact that the NPPs now coordinate their discharges prior to actual release: the Saint-Laurent-des-Eaux NPP
coordinates discharges from all NPPs releasing effluents into this river. No two NPPs may discharge effluents simultaneously, unless
an exemption is granted. Tritium activity increased in the river due to severe weather conditions in May-June 2011, with insufficient
rain levels. Activity beat the 1996 record for the first time. Tritium activity measured in Loire river water downstream from theDampierre site was also slightly higher than usual between July and December 2015.

Bq/L
160
140
120
100
80
60
40

0

1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
2005
2006
2007
2008
2009
2010
2011
2012
2013
2014
2015
2016
2017

20

Belleville NPP

Chinon NPP

Civaux NPP

Dampierre NPPSaint-Laurent NPP

2. Sequential samples are taken to obtain permanent measurements; on this basis, the activity measured is representative of mean monthly
activity levels (see chapter 1, p. 17).

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /93

FIGURE 9 / MEAN ANNUAL TRITIUM ACTIVITY FOR MEUSE, MOSELLE AND SEINE RIVER WATER AND WATER IN THE
ALSACE CANAL DOWNSTREAM FROM THE CHOOZ, CATTENOM, FESSENHEIM AND NOGENT NPPS (Bq/L)
Tritium activity in the Meuse river dropped substantially in the early 1990's, from 40 Bq/L to 10 Bq/L per year on average, with the final
shutdown of the Chooz-A NPP in 1991. Since the mid-1990s, mean annual tritium activity levels in the Meuse river have increasedslightly, but constantly, to the current value of approx. 30 Bq/L. Mean monthly activity in the Moselle river downstream from theCattenom NPP has progressively increased, from the 1985 level of 15 Bq/L to the current level of approx. 30 - 40 Bq/L. Mean annual
tritium activity downstream from the Fessenheim NPP has steadily decreased since 1976. Mean annual activity measurements for the
Seine river since 2014 have represented between 27 and 48 Bq/L.

Bq/L
70

Cattenom NPP

Chooz NPP

Fessenheim NPP

Nogent NPP

60
50
40
30
20

0

FIGURE 10 / MEAN ANNUAL TRITIUM ACTIVITY FOR GARONNE RIVER WATER DOWNSTREAM FROM THE GOLFECH NPPAND GIRONDE RIVER WATER DOWNSTREAM FORM THE BLAYAIS NPP (Bq/L)
The location of the IRSN water sampling system fitted downstream from the Blayais NPP was modified in 2007. The system was initiallyinstalled at Laspeyres, and was moved nearer to the NPP discharge point, which explains why activity measurements are higher, since
the effluents are less diluted. Since 2007, samples have been taken directly at the NPP discharge point, leading to tritium activity
measurements of 5 - 40 Bq/L. After the effluents have been diluted/dispersed in the estuary, no activity can generally be detected atVitrezay or Pauillac. In addition, activity has constantly decreased and has been divided by 3 since 1981. Tritium activity measured in
Garonne river water downstream from the Golfech NPP has also progressively decreased since the late 1980's. Mean annual activity
measurements since 2014 have represented between 5 and 10 Bq/L.

Bq/L
30

Blayais NPP

Golfech NPP

25
20
15
10
5
0
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
2005
2006
2007
2008
2009
2010
2011
2012
2013
2014
2015
2016
2017

94

1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
2005
2006
2007
2008
2009
2010
2011
2012
2013
2014
2015
2016
2017

10

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Operational Nuclear PowerPlants (NPP) / 3.1

FIGURE 11 / MEAN ANNUAL TRITIUM ACTIVITY FOR RHÔNE WATER DOWNSTREAM FROM THE BUGEY, SAINT-ALBAN,CRUAS AND TRICASTIN NPPS (Bq/L)
Tritium activity in Rhône river water downstream of NPPs has been divided by 3 to 4 since the early 1980's.
As activity measurements were increasingly below 10 Bq/L, in 2008-2010, IRSN decided to improve its metrological performance toallow lower activity levels to be measured, down to a decision threshold of 1 Bq/L.
IRSN aims to quantify water activity well below regulatory limits.
Monthly activities measured downstream from the Cruas and Bugey NPPs in 2017 represented between 18 and 34.9 Bq/L,
demonstrating increases in mean annual activity levels.

Bq/L
30

Bugey NPP

Cruas NPP

St-Alban NPP

Tricastin NPP

25
20
15
10
5

1980
1981
1982
1983
1984
1985
1986
1987
1988
1989
1990
1991
1992
1993
1994
1995
1996
1997
1998
1999
2000
2001
2002
2003
2004
2005
2006
2007
2008
2009
2010
2011
2012
2013
2014
2015
2016
2017

0

Tritium activities above background radiationlevels are regularly detected in some drinking
water samples taken from rivers: 12 Bq/L at
Beaumont-en-Véron nnear to Chinon in 2014, 8
and 19 Bq/L in 2014 and 14 Bq/L in 2015 at PetitPuy also near to Chinon, 24 Bq/L in 2014 at Blois
due to the St-Laurent NPP, 6.3 and 12 Bq/L at theMornas pump station near to the Tricastin site,
8.2 Bq/L at Chavanoz near to Bugey in 2017, etc.
Unlike most radionuclides discharged in a liquid
effluent, tritium is not "stopped" by drinking water
treatment systems. On this basis, the activity
levels measured in drinking water can match
those recorded in river water samples.

Note: the highest tritium activities in river water
samples as measured by EDG are recorded in
the French Metrology network database. These
analyses were carried out on samples taken
during active discharge, as per regulations(see sampling mid-discharge in table 3-A) in orderto ensure that the liquid effluents are discharged
in compliance with the applicable requirements.
It would therefore appear entirely natural for
activity measurements to be up to 6 times higher,
on average, than those measured by IRSN in theform of continuous sampling throughout the year
(see page 80 of the radiological report for the
2011-2014 period).

The tritium dose absorbed if a person drinks
2 L of water per day over one year would reachapproximately 0.04 μSv/year downstream from
Fessenheim, 0.4 μSv/year downstream from
Cattenom and 0.5 µSv/year downstream from
Nogent, based on activity measurements. The
highest of these doses are lower than those
calculated by EDF using activity measurements
for the effluents discharged: from 0.05 to 4.8 μSv/
year for Fessenheim and Cattenom respectively.

70% of the results of analyses performed by EDF
on ground water, as part of routine monitoring
programmes, were below the decision threshold.
However, due to malfunctions or incidents,
ground water samples taken on EDF sites cancontain tritium on a temporary basis (see page78 of the radiological report for the 2011-2014
period). In particular, several incidents withsignificant environmental effects were detectedby IRSN(3) for all NPPs between late-2014 and3. FT/AV/PSN report-2018-00036: EDF-PWR, analysis of feedback; trends based on EDF declarations of incidents with significant environmental
effects for the years 2015 and 2016.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /95

late-2016, including one event when a pipe
carrying tritiated effluents started leaking at thethe Bugey site towards the end of 2014. The tritiumcontaminated the ground water near to the site
due to this incident. According to the results ofanalyses carried out on water samples taken at
piezometers N0 SEZ006 PZ and N0 SEZ013 PZ(figure 12) and the results acquired as part ofreinforced monitoring (figure 13), tritium activity
remained above background levels until 2017 atsome locations. The results of analyses carriedout on samples taken at other piezometers during
this period remained within the usual range,demonstrating the highly local effects of thecontamination caused by this incident.

FIGURE 12 / TRITIUM ACTIVITY IN GROUND WATER (Bq/L) AT THE BUGEY SITE NEAR TO PIEZOMETERS N0 SEZ006 PZ AND
N0 SEZ013 PZ AFTER THE INCIDENT WITH SIGNIFICANT ENVIRONMENTAL EFFECTS IN DECEMBER 2014

Bq/L
1200

Piezometer
N0 SEZ006 PZ

1000

Piezometer
N0 SEZ013 PZ

800
600
96

400
200
0

Mar-14 Sep-14 Apr-15

Oct-15 May-16 Nov-16 Jun-17 Dec-17

FIGURE 13 / TRITIUM ACTIVITY IN GROUND WATER (Bq/L) AT THE BUGEY SITE MEASURED AS PART OF REINFORCED
MONITORING BY EDF LAUNCHED AFTER THE INCIDENT WITH SIGNIFICANT ENVIRONMENTAL EFFECTS IN DECEMBER
2014

Bq/L
1600
1400
1200
1000
800
600
400
200
0

Jun-14 Dec-14

Jul-15Jan-16 Aug-16 Mar-17 Sep-17 Apr-18/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Operational Nuclear PowerPlants (NPP) / 3.1

Tritium activity in fish captured in rivers containing
effluents discharged from NPPs is measured aspart of regulatory monitoring. Figures 14 and 15
show that variation in tritium activity in fish overthe lengths of the Rhône and Loire rivers is very
similar to the variation in carbon-14 described

previously (figures 5 & 6): activity increases
downstream from each NPP and decreases
after each major tributary (Saône, Ain, Isère andDurance for the Rhône rivera and Cher for the
Loire river) joins the main river due to the higher
flow rate promoting the dispersal of the activity

FIGURE 14 / VARIATION IN TRITIUM ACTIVITY IN FISH (Bq/kg fresh), OVER THE FULL LENGTH OF THE RHÔNE RIVER, ON THE
BASIS OF MEASUREMENTS TAKEN OVER THE 2001-2011 PERIOD (shown in blue) AND OVER THE 2012-2016 PERIOD (shownin red)Mean, min. and max. values over the 2001-2011 period*
Mean, min. and max. values over the 2012-2016 period

Bq/kg fresh
40
35
30
25
20
15
10

97

5
Background radiation range
Lyon
Avignon Camargue
St-Alban Valence Cruas Tricastin Marcoule
Saône/Ain
Isère
DuranceRhône river flow
* Prior to 2009, data only existed for some years (ten-year reports and specific studies)0

Upstream Creys
Rhône

Bugey

FIGURE 15 / VARIATION IN TRITIUM ACTIVITY IN FISH (Bq/kg fresh), OVER THE FULL LENGTH OF THE LOIRE RIVER, ON
THE BASIS OF MEASUREMENTS TAKEN OVER THE 2010-2015 PERIOD

Bq/kg fresh
25

Mean, min. and max. values over the 2010-2015 period

Muides-sur-Loire

20

TaversSaint-Père-sur-Loire15
10

Île St-Martin
Chouzé-sur-Loire

Châtillon-sur-Loire Montoire

5
Sury-pré-Léré
0

Belleville
NPP

Orléans
Tours
DampierreSaint-Laurent Cher
NPP
NPP
Loire river flow

Background radiation range
ChinonNPP

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /added. If we compare activity measurements overthe 2001-2011 and 2012-2016 periods along thefull length of the Rhône, the effects of these NPPs
would appear stable over time.
Figure 16 shows how the Moselle river is lesseffective at dispersing the effluents discharged
from the Cattenom NPP, as was the case forcarbon-14 (figure 7), with similar, or higher,
activity levels measured downstream from thissite, when compared with the activity of the Rhône
river downstream from all NPP.
In general, tritium activity in fish correlates withwater activity as measuring in the samples takenusing sampling systems. According to table 4, thefish/water activity ratio is systematically equal toapproximately 1.

The tritium dose absorbed after eating fishis insignificant compared with the equivalentcarbon-14 dose: approximately 1,000 times less.
Tritium and carbon-14 are discharged in liquid
effluents from the Flamanville, Paluel, Penly andGravelines NPPs on the Channel. Based on theactivities of these radionuclides as measured
during IRSN campaigns and the radioecologicalmonitoring programme run by EDF, the impactof liquid discharges from NPPs cannot be
differentiated from that of the discharges fromthe Orano facility in La Hague, which are over 150
times higher, including at local level.

FIGURE 16 / TRITIUM ACTIVITY IN FISH CAPTURED DOWNSTREAM FROM THE CATTENOM, CHOOZ, CIVAUX AND GOLFECHNPPS (Bq/kg fresh)

98

Bq/kg fresh
60
Upstream from Cattenon
Downstream from Cattenom

50

Upstream from Chooz
Downstream from Chooz

40

Upstream from Civaux
Downstream from Civaux
Upstream from Golfech
Downstream from Golfech

30

20

10

0

Background radiation range
2009 2010 2011 2012 2013 2014 2015 2016 2017 2018

TABLE 4 / MEAN TRITIUM ACTIVITY IN WATER SAMPLES COLLECTED USING SAMPLING SYSTEMS (Bq/L)
AND FISH CAPTURED DOWNSTREAM OF THE NPP (Bq/kg fresh)

NPP
Water

Bel.

Civ.

Cho.

Cat.

Nog.

Gol.

Bug.

Tri.

Cru.

St-Al.

Chi.

St-La.

Dam.

13.9

21.7

26.7

31.8

34.9

8.3

8.2

6.6

11.0

5.7

15.0

18.1

21.5

Fish

13.6

22.1

22.9

32.5

33.0

7.7

10.2

9.1

9.0

6.6

12.3

14.9

11.0

Fish/water

1.0

1.0

0.9

1.0

0.9

0.9

1.2

1.4

0.8

1.2

0.8

0.8

0.5

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Operational Nuclear PowerPlants (NPP) / 3.1

The impact of liquid discharges containing
other radionuclides
Gamma-emitting radionuclides in river water are
analysed on a monthly basis by IRSN via settlingsludge samples obtained from the water collectedusing the 24 water sampling systems installed on
the main rivers hosting the effluents discharged
from the nuclear facilities. Sludge activity levels are
representative of those of the particles suspended
in the water, particularly for radionuclides
which are mainly carried in rivers as particles(other radionuclides such as antimony-124 and
125 are dissolved). The main gamma-emitting
radionuclides in the liquid effluents discharged by
NPP were all detected at least once over the 20142017 period. As expected, cobalt-60 is discharged
the most, and is the most frequently detectedradionuclide (43% of analyses) in sludge from IRSN
water sampling systems, with the highest activity
levels (up to 46 Bq/kg dry). Silver-110m ranks
second after cobalt-60 (18% of total radionuclides
detected with a peak activity of 7.7 Bq/kg dry),followed by cobalt-58 (9.5% of total radionuclides
detected with a peak activity of 13 Bq/kg dry), as
was the case for discharges. Manganese-54, andcaesium-134 are discharged far less frequently in
NPP effluents, and are only rarely detected (1.7%
and 0.69% of analyses respectively, with peak
activities of 2.8 and 0.8 Bq/kg dry). Caesium-137
is frequently detected due to its presence inbackground radiation from residual fallout from
nuclear tests and the Chernobyl accident. Highactivity levels comprising iodine-131 (up to 68 Bq/
kg dry) are mainly recorded downstream of large
hospitals using nuclear-based medical systems
due to their discharges. Iodine-131 activity isalso frequently higher upstream of NPP thandownstream. Finally, ruthenium-106 was detected
in settling sludge from the water sampling system
twice, in November 2013 and December 2015,
for the Flamanville NPP discharge zone. This
radionuclide is not discharged by the NPP, it wasprobably released at La Hague, and transited via
the seawater used to disperse the NPP's effluents.

Gamma-emitting radionuclides have also
been detected in some biological indicators(aquatic plants), although very rarely in
sediments, and never in fish, in recent years.
These radionuclides can only be detected using
the most advanced technologies available,
implemented as part of the studies conductedby IRSN and SUBATECH at the request of EDF.
60
Co and 58Co are regularly detected, while 54Mn and
110m
Ag are occasionally detected, and 134Cs has notbeen detected in the last three years. Figures 17
and 18 show 60Co and 58Co activity levels measured
in aquatic plants sampled at various locations on
the Rhône river, downstream from the Nogent,
Chooz and Cattenom NPPs, since 2008. According
to these figures, since the substantial decreasein discharge levels during the 1980-1990 period,
when a minima was reached, activities haveremained stable. The highest activity levels in the
Rhône river are measured downstream from the
Bugey NPP due to the low flow rate for the Rhône,
which decreases the dispersal of the radionuclides(compare the flow rate of 450 - 600 m3/s at Bugey
with the 1,040 m3/s recorded after the confluencewith the Saône and Ain tributaries and 1,410 m3/s
at Valence after the Isère river joins the mainflow). According to the results of samplingruns downstream from the Saint-Alban (Bugey
discharges) and Tricastin (Cruas discharges) sites,
the impact of effluents discharged from NPPs canbe detected over several tens of kilometres. 110mAg
activity measurements are also higher and more
frequently detected downstream from the Bugey
NPP (figure 19). Iodine-131 can be measured inaquatic components, however not systematicallyand levels vary substantially. As is the case forsettling sludge, this radionuclide is mainly addedby hospitals, where it is used for therapeutic
purposes and diagnostics and later discharged.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /99

FIGURE 17 / COBALT-58 AND 60 ACTIVITY IN AQUATIC PLANTS (mosses and phanerogams)
COLLECTED AT VARIOUS POINTS ON THE RHÔNE RIVER (Bq/kg fresh)

Bq/kg fresh

10

Co
58
Co
60

1

0.1

100

Upstream
Downstream
from St-Alban from St-Alban

Upstream
Downstream
from Tricastin from Tricastin

Co
Co

60
58

Downstream
from Cruas

Co
Co

60
58

Downstream
from Bugey

0.01
2006 2008 2009 2010 2012 2013 2014 2016 2017 2019

FIGURE 18 / COBALT-58 AND 60 ACTIVITY IN AQUATIC PLANTS (mosses and phanerogams) IN SEINE, MEUSE AND
MOSELLE RIVER WATER DOWNSTREAM FROM THE NOGENT, CHOOZ AND CATTENOM NPPS (Bq/kg dry)

Bq/kg fresh
10

1Cattenom Nogent Chooz

Co
58
Co
60

0.1

0.01
2008

2009

2011

2012

2013

2015

2016

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Operational Nuclear PowerPlants (NPP) / 3.1

FIGURE 19 / 110MAg ACTIVITY IN AQUATIC PLANTS (mosses and phanerogams) IN THE RHÔNE RIVER DOWNSTREAM OF THE
BUGEY NPP (Bq/kg dry)

Bq/kg fresh
0.5
0.45
0.4
0.35
0.3
0.25
0.2
0.15
0.1
0.05
0
2007 2008 2009 2010 2011 2012 2013 2014 2015 2016 2017

101

Finally, most radionuclides measured in the
Channel, including near to NPPs, are discharged
as part of liquid effluents from the Orano facilities
in La Hague or the Sellafield plant (Great Britain,
see chapter 3.3 La Hague). The contribution ofliquid effluents discharged from the NPPs is
probably very low, and cannot be differentiated or
measured, with the exception of 110mAg, which ismore specifically discharged by these facilities.
This radionuclide is measured and characterised
in suspended solids or settling sludges taken as
samples from discharge channels (vertical or
horizontal) as part of routine monitoring by IRSN.
Activity levels can reach a few Bq/kg dry (witha peak value of 2.9 Bq/kg dry measured in theGravelines sea channel in September 2014).

© DR

The activity of this radionuclide in algae andsediments is too low to be detected in theenvironment, with a few very rare exceptions.
110m
Ag activity has never been quantified in the 250
analyses in fish since 2001, however levels mustbe less than 0.04 Bq/kg fresh.

Fish (catfish) captured in the Rhône river

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /On the other hand, this radionuclide ismeasured in one in three analyses in molluscs(mussels, limpets, oysters, etc.) and shellfish(shrimp, crabs, spider crabs), on average.
Activity levels do not differ significantly between
the various types of food. Figure 20 shows theresults for all food types, but for various samplingstations near to the Flamanville, Paluel andGravelines sites (activity levels near to Penly are
lower and rarely mesurable). Nearly all activity
measurements are between 0.1 and 1 Bq/kg
fresh, although results can fluctuate widely ateach sampling station, as shown by the samples
taken near to the discharge point at the Gravelines
facility, which oscillate between activities of0.02 Bq/kg and 0.6 Bq/kg. The highest activity
measured over the last 16 years reached 1.5 Bq/
kg fresh in a limpet sample taken at Huttes piernear to Gravelines in 2013.

102

Even for a person eating large quantities ofsea food (31 kg/year of molluscs, 61 kg/year ofshellfish), the potential dose of 110mAg absorbed/
ingested would be extremely low according
to these results, falling below 0.02 μSv/year.
The dose calculated in the previous Radiologicalreport on the basis of the results acquired at
the Gravelines site alone was estimated at
0.05 μSv/year. These doses are lower than those
calculated by EDF using activity measurements
for the effluents discharged from the Gravelines
site: 0.08 μSv/year for average consumers and0.16 μSv/year for very regular consumers.

FIGURE 20 / 110MAg ACTIVITY IN MOLLUSCS AND SHELLFISH CAPTURED IN THE CHANNEL NEAR TO NPP (Bq/kg fresh)

Bq/kg fresh
10

1

0.1

0.01
Oct-00 Jun-03 Mar-06 Dec-08 Sep-11
Offshore from Gravelines
Near to the Gravelines site
Huttes pier near to Gravelines

Jun-14 Mar-17

Flamanville carteret
Flamanville Diellette
Flamanville Goury/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

Paluel L'éperon
Near to the Paluel site
Paluel St-Pierre en port
Paluel St-Valéry en cauxDATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Operational Nuclear PowerPlants (NPP) / 3.1

Conclusions
No radiological anomaly has been detected overthe last three years in the immediate environmentof EDF nuclear powerplants, particularly forsampling stations fitted on an aerosol filter. The
reference gross beta activity index in air (2 mBq/m3) was only exceeded during the period due toincreases in natural radioactivity (mainly lead 210),
due to transient weather conditions.
Several incidents with significant environmental
effects were detected by IRSN(4) for all NPPs
between late-2014 and late-2016, including one
event when a pipe carrying radioactive effluents
started leaking at the the Bugey site towards theend of 2014. The tritium contaminated the groundwater near to the site due to this incident. This
contamination was measured in water samples
taken up to 2017, at 2 out of the 9 routine monitoring
piezometers and in the samples taken as part ofa reinforced monitoring plan implemented after
the incident in order to better characterise andtrack variation.
The other incidents had no measurable
consequences on the environment as per
regulatory monitoring rules. This was particularly
the case for the effluents discharged into theatmosphere by the Golfech NPP on 19 October
2016, estimated at 136 GBq of noble gases.
Neither the operator's ambient gamma dose ratemeasuring sensors installed around the site, nor
IRSN's sensors, were activated by this discharge
as the associated dose rate was very low after
dispersal. Noble gases are also chemically inert,
and will disperse in the air without contaminating
the environment.

During the 2015-2017 period, the expected
activities were measured in all environmental
components around NPPs. These values are
fairly constant compared with earlier years.
The two main radionuclides found in effluent
discharges are carbon-14 and tritium. Only theseradionuclides can be measured in terms of the
impact of NPPs in most continental aquatic andterrestrial components, particularly in food.
According to the activities measured in the air
and in the terrestrial environment, the impact ofeffluents discharged into the atmosphere rapidly
decreases with distance from the site, particularly
over the first 5 kilometres, and cannot be
differentiated from background radiation beyond
10 kilometres. Exposure due to inhaling air isextremely low and insignificant when comparedwith the potential exposure involved in eating local
food, which is itself very low. The dose absorbed
by eating local food, assuming the produce wasgrown within a 5 km radius around the site, would
reach approximately 0.075 μSv/year. This dose isalmost exclusively attributable to carbon-14.
The effects of liquid effluents containing carbon-14
and tritium, discharged, can be detected
downstream from all NPP. These effects aremeasured in all aquatic components for tritium
and in fish for carbon-14. The average doseabsorbed if an individual occasionally eats fish
captured on a leisure basis downstream from an
NPP installed on a river is estimated at 0.15 mSv/
year. This dose can be higher downstream from
specific sites, potentially reaching 0.4 μSv/year.
For information, this dose is almost entirely due
to carbon-14 and only represents a few percent of
the total dose absorbed by eating fish due to theirnatural radioactivity levels, which is estimated at
12 μSv/year.

4. FT/AV/PSN report-2018-00036: EDF-PWR, analysis of feedback; trends based on EDF declarations of incidents with significant environmental
effects for the years 2015 and 2016.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /103

Drinking river water from downstream of NPPs
would lead to a dose of between 0.004 μSv/year
and 0.5 μSv/year due to the presence of tritium.

104

The activities measured in the environment andthe estimated doses likely to reach local residents
fully match the dosimetric assessments conductedby EDF in its annual reports. These doses are morethan one thousand times less than the maximum
permissible dose from artificial radionuclides(excluding medical exposure) according toregulations: 1 mSv/year.

© DR

Radionuclides other than carbon-14 and tritium(60Co and 110mAg in particular) in NPP discharges
cannot be measured in the air and in some aquaticcomponents due to their extremely low activities,
even using the best available techniques. The
associated doses are insignificant comparedwith those of tritium and carbon-14, which
are themselves low. Although NPP discharges
may potentially include 137Cs activity, most ofthese radionuclides measured in the immediate
environment of NPPs are residual fallout from the
Chernobyl accident and the atmospheric testing of
nuclear weapons (see chapter 2).

Taking moss samples on a bridge over the Rhône river/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Operational Nuclear PowerPlants (NPP) / 3.1© Noak/Le bar Floréal/IRSN

105

Taking aquatic plant samples near to the Tricastin nuclear site

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /3.2. NUCLEAR POWERPLANTS
IN THE DECOMMISSIONINGPROCESS

Discharges and monitoring the environment

Nine EDF reactors are currently being
decommissioned Seven of these reactors arelocated at sites where reactors are operational.
These reactors are covered in chapter 3.1.
This chapter only describes the two sites with nooperational reactors: Creys-Malville and Brennilis.

Creys-Malville site

106

The Creys-Malville nuclear facility is located in
the Isère département, on the left bank of the
Rhône river, in the municipality of Creys-Mépieu,around fifty kilometres upstream from the urban
agglomeration of Lyons. The site hosts two basic
nuclear facilities (INB): the Fast Neutron Reactor(FNR) powerplant which was commissioned in
1985, finally shut down in 1998 and is currently
in the decommissioning phase, and a series offacilities, including the fuel storage area (APEC).

The Creys-Malville site holds special authorisation
to discharge radioactive substances into theenvironment, as required by regulations.
The radioactive liquids discharged comprisesome of the water used by the facilities. The
radioactive gases discharged are output frombuilding ventilation systems. Most of the activity
discharged is tritium by far: 98 - 99.9% of of theliquid and gaseous effluents discharged. Table
1 shows the activity levels discharged over the2011 - 2016 period. Figure 1 shows variationin tritium discharged in gaseous and liquid
phases between 2002 and 2016. As shown,liquid discharges increased in 2015 and 2016
and gaseous discharges climbed progressively
between 2002 and 2010 by 0.1 and 1 TBq, reaching
10 TBq between 2011 and 2013, and then 48 TBq
in 2014 and 2016. In 2015, tritium gaseousdischarges were 100 times lower than in 2014
and 2016. These peaks were directly caused bydecommissioning operations. The Creys-Malvilleregulatory environmental monitoring programme
is shown in figure 2. This programme is completedwith annual radioecological studies entrusted
to IRSN by EDF. IRSN also conducted a special
study between 24 September and 9 November
2012, at the request of EDF, to characterise theenvironmental impact of a series of atmosphericdischarges, containing tritium, in detail.

TABLE 1 / ACTIVITY LEVELS DISCHARGED FROM THE CREYS-MALVILLE FACILITIES OVER THE 2011 - 2016 PERIOD

Unit

Activity level discharged
2011

2012

2013

2014

2015

2016

Radioactive liquids discharged
Tritium

TBq

0.72x10-3

0.91x10-3

0.2x10-3

2.63x10-3

1.53x10-2

3.86x10-2

Excluding tritium

GBq

7.7x10-3

1.72x10-2

1.7x10-2

1.22x10-2

1.76x10-2

4.19x10-1

Radioactive gases discharged
Tritium

TBq

13.32

15.73

14.85

47.9

3.26x10-1

48.3

Activation or fission
products

GBq

1.5x10-3

1.5x10-3

3.2x10-3

5.37x10-3

2.43x10-3

2.31x10-3

Noble gases (85Kr)

GBq

0.27

0.05

0.05

0.02250.024

0.0375/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Nuclear powerplants in the decommissioning process / 3.2
CREYS-MALVILLE SITE

FIGURE 1 / VARIATION IN GASEOUS AND LIQUID TRITIUM DISCHARGED FROM THE CREYS-MALVILLE SITE BETWEEN 2002
AND 2016 (TBq/year)

TBq/year
100
10
1
0.1
0.01
0.001
0.0001
2002 2003 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013 2014 2015 2016
GaseousLiquids

107
FIGURE 2 / MAP SHOWING THE STANDARD ENVIRONMENTAL MONITORING PLAN DRAFTED BY EDF FOR THE
RADIOLOGICAL MONITORING OF THE IMMEDIATE ENVIRONMENT OF THE CREYS-MALVILLE SITE
Sampling point (Quantity)
Aerosols (4)Ambient dose (12)Bubbler (1)Rainwater (1)Steam or river (1)Ground water (5)Milk (2)Fruit, vegetables and cereals (5)Terrestrial mosses and grass (5)Phanerogams, aquatic mosses (2)Fish (2)Soils (1)
Sediments (2)Road networks, hydrographics andsite boundaries
Departmental road
Permanent river or stream
Seasonal river or stream
Site boundaryLand use
Construction or building
Anthropic surface (Structure)
Anthropic surface (Industry or shops)
ForestRiver, stream or lake
Other(source: RGE-BDTOPO@ & BDCARTO@ by IGN - 2015 ed.)

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /TABLE 2-A / REGULATORY MONITORING PLAN DRAFTED BY EDF FOR THE IMMEDIATE ENVIRONMENT OF
THE CREYS-MALVILLE SITE

Environment
monitored ortype of testing108

Measurements, samples and analyses

Ambient gamma
radiation• 10 sensors around the edge of the site
• 4 sensors at a distance of 1 km
• 4 sensors at a distance of 5 km

Soil air• 4 daily measuring and sampling points for gross beta activity with a filter• γ spectrometry if values > 2 mBq/m3• 1 monthly γ spectrometry run for combined daily filters at one single sampler• Continuous sampling based on the prevailing winds with weekly atmospheric tritium
measurements

Rainwater• Continuous sampling based on the prevailing winds with bi-monthly measurements for tritium andgross beta activity

The receiving
environment for liquid
effluents discharged• Hourly aliquots taken mid-discharge: gross beta activity, potassium and tritium in filtered water
samples + gross beta activity for TSS samples• Tritium activity with daily aliquots + γ spectrometry if > 140 Bq/L (during discharges) or > 100 Bq/L
outside of discharges

Ground water• 5 sampling points: monthly 3H, 40K and gross beta activity measurements for filtered water andgross beta activity measurements for TSS

Soils• 1 annual sampling run for topsoil layers: gamma spectrometry

Plants• 2 monthly grass samples (including 1 in the prevailing wind direction):
γ spectrometry + annual OBT and HTO

Milk• 2 monthly milk samples (including 1 in the prevailing wind direction):monthly gamma spectrometry runs + quarterly tritium measurements

Soils• 1 annual sampling run: γ spectrometry

Aquatic flora• 2 annual sampling runs (upstream/downstream: γ spectrometry

Aquatic fauna• 2 annual sampling runs (upstream/downstream): γ spectrometry + OBT

Sediments• 2 annual sampling runs (upstream/downstream: γ spectrometry

Farm output• 1 annual sampling run for the main farming output: γ spectrometry, HTO and OBT

TABLE 2-B / ANNUAL RADIOECOLOGICAL MONITORING PLAN FOR THE IMMEDIATE ENVIRONMENT OF
THE CREYS-MALVILLE SITE IN 2017

Matrix

Gamma

Grassland soils

HTO
1

OBT

Grass

1

1

Milk

1

1

Terrestrial moss

2

Oak tree leaves

2

Sediment
Aquatic moss
Aquatic phanerogams

C-14

Ni-63

1

2

2

2

2

2

2

2

2
2

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Nuclear powerplants in the decommissioning process / 3.2
CREYS-MALVILLE SITE

The impact of the Creys-Malville site on its
immediate environment and associated doses
The impact of tritium discharges from theCreys-Malville site cannot be clearly detectedfrom measurements performed on environmental
samples, as these discharges fluctuate over eachyear. Mean total tritium activity in air samplednear to the Creys-Malville site represented
4.14 Bq/m3 in 2016, which is considerably higher
than background radiation (between 0.005 and0.01 Bq/m3). However, this mean value wasachieved due to increases over short periods (afew days) corresponding to discharge phases.
Figure 3 shows tritium activity measured in the air
at the Creys-Malville site by EDF between June
2011 and December 2017. As shown on this figure,the considerable increase in atmospheric tritium
discharges in 2014 and 2016, compared with
figures for previous years, led to an increase in
the number of significant measurements, and thelevels measured. On the other hand, the very low
discharge levels for atmospheric tritium in 2015
also reflected a lack of significant measurements
during this period.

Figure 4 shows tritium activity measured inrainwater at the Creys-Malville site by EDF and
IRSN between June 2011 and December 2017.
Rainwater analyses reflect an increase in activity,
however this indicator is less sensitive (due to thefact that the effluents discharged are diluted inrainwater) and less frequently viable (as rain is notcontinuous). 93% of the 163 measurements are
below the decision thresholds (approx. 5 - 6 Bq/L),
only 11 measurements indicate significant values
between 2.1 and 16.5 Bq/L. Transient increases
in ambient activity moderately affect the otherterrestrial components for a very short period.
Grass, vegetable, cereal and milk samples do not
integrate these transient increases. On this basis,mean tritium activity levels between 2011 and 2017
in grass (3.18 Bq/kg fresh), vegetables (2.91 Bq/
kg fresh), cereals (1.64 Bq/kg fresh) and milk
(1.77 Bq/L), measured as part of radioecologicalstudies, are low and within the backgroundradiation range for environmental tritium (fromless than 1 to 3 Bq/L).
109

FIGURE 3 / TRITIUM ACTIVITY MEASURED IN THE AIR IN THE IMMEDIATE VICINITY OF
THE CREYS-MALVILLE SITE BETWEEN JUNE 2011 AND DECEMBER 2017 (Bq/m3)

Bq/m 3
18
16
14
12
10
8
6
4
2
0
June
2011

June
2012

June
2013

June
2014

Decision thresholds

June
2015

June
2016

June
2017

Activity measurements

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 4 /TRITIUM ACTIVITY MEASURED IN RAINWATER IN THE IMMEDIATE VICINITY OF THE CREYS-MALVILLE SITE
FROM JUNE 2011 TO DECEMBER 2017 (Bq/L)

Bq/L
18
16
14
12
10
8
6
4
2

110

0
June
2011

June
2012

June
June
2013
2014
Decision thresholds

EDF asked IRSN to organise a specific measuring
campaign to improve the characterisation ofdischarges: 12 TBq of tritium was discharged
between 24 September and 9 November 2012.
This measuring campaign confirmed that theincrease in tritium activity was moderate andtransient after the discharge. On this basis, after
a peak in ambient activity was reached at 0.96
Bq/m3, at the same time as rainwater activity of
16.5 Bq/L, the activity levels measured in grass
and milk (3.9 Bq/L) remained close to backgroundradiation levels. Only oak leaves reached a levelof 12 Bq/kg fresh. This impact is very low due tothe fact that the tritium discharged is tritiatedhydrogen (HT), which does not easily transfer tothe living environment compared with tritiatedwater vapour (HTO). Plant contamination was also
limited due to autumn. Tritium levels returned tonormal figures from the end of November, i.e.
after just a few weeks.

June
June
June
2015
2016
2017
Activity measurements

99% of measurements for Rhône water samples
downstream from the Creys-Malville site are below
decision thresholds. Tritium activity is significant
for a few measurements at approx. 5 - 6 Bq/L
and particularly those obtained from the water
sampling system located downstream from theCreys-Malville (see figure 5). These measurements
are slightly above background radiation (1- 3 Bq/L).
Tritium activity is not regularly recorded in Rhône
river water, upstream from this site, therefore noconclusion can be reached in terms of the sourceof the tritium measurements. Tritium activity
measurements in ground water are all below thedecision threshold (6 Bq/L).
With the exception of iodine-131 from medical
sources, measured in aquatic plants, all othermeasurements taken in the immediate environment
around the Creys-Malville site is at backgroundradiation levels, i.e. natural radioactivity andresidual fallout from the Chernobyl accident or
the atmospheric testing of nuclear weapons.
Bound tritium and 14C measurements in fish areillustrated in chapter 3.1 "Operational NPP".

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Nuclear powerplants in the decommissioning process / 3.2
CREYS-MALVILLE SITE

FIGURE 5 / VARIATION IN MONTHLY TRITIUM ACTIVITY MEASURED IN THE RHÔNE RIVER DOWNSTREAM FROM THE
CREYS-MALVILLE SITE (Bq/L)

Bq/L
16
14
12
10
8
6
4
2
0
1985 1987 1989 1991 1993 1995 1997 1999 2001 2003 2005 2007 2009 2011 2013 2015 2017
Decision thresholds

Activity measurements

Mean values prior to 2011

111

According to the study of radiologicalmeasurements for environmental samples taken in
the vicinity of the Creys-Malville site, only tritium is
involved in the impact of discharges from this site.
However, tritium activity levels in farming output
and drinking water are similar to those measured
in areas unaffected by facilities. Tritium discharges
from the site do not reach measurable levels in
food, therefore the dose absorbed by eating local
food grown near to the site cannot be assessed.
On the other hand, doses absorbed by inhalingor transcutaneously can be calculated based on
the concentration measured in the air. This doseis assessed for an adult spending all of their timeon the site and the mean significant measurement(4.14 Bq/m3) is used as the concentration in the
air. 20 out of the 28 measurements taken in 2016
were significant and 8 were below the decisionthreshold. On this basis, the concentration in
the air will be weighted by a coefficient of 20/28
to integrate the presence or absence of tritium
activity above background radiation levels.
The flow inhaled per day by local residents is taken
as 24 m3/day. Based on the above assumptions,the dose inhaled and percutaneous transfer
represents approx. 0.06 μSv/year if we assume
that the tritium discharged is 90% HT and
10% HTO, as shown by the study from 2012.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Brennilis site
The Monts d’Arrée site (SMA) is located in the
Finistère region, in the Brennilis municipality, just
35 km to the south of Morlaix. The site is at theend of Saint-Michel lake. The site is home to the
Brennilis nuclear powerplant and the Saint-Michel
and Saint-Herbot hydraulic dams. The Brennilis
nuclear powerplant ran from 1967 to 1985, with arating of 70 MW. The site was definitively shut downin 1985, and is currently being decommissioned.
Discharges and monitoring the environment
While the plant was operating, the main gaseousand liquid effluents authorised for discharge
comprised tritium. Gaseous tritium continued
to be produced after the site was shut down,
but at lower levels. Liquid effluents continued
to be discharged into the Ellez river up to 1992
and ceased after this time. Less liquid effluents112

are currently sent to an external operator forprocessing, and these effluents do not containtritium. The Monts d'Arrée site holds special
authorisation to discharge radioactive substances
into the environment, in gaseous phase, as
required by regulations. The radioactive gases
discharged are output from building ventilation
systems. Most of the activity discharged is tritium.
Table 1 shows the activities discharged for the2012 - 2016 period. Discharge levels fluctuate due
to decommissioning operations.
The Monts d'Arrée regulatory environmental
monitoring programme is shown in table 2 andfigure 1. This programme is completed withannual or ad hoc radioecological studies entrusted
to external laboratories by EDF. This programmemonitors:• rainwater (Brennilis weather station);• surface water (Ellez river, St-Herbot lake);

TABLE 1 / MAP SHOWING THE LOCATIONS OF SAMPLES TAKEN UNDER THE ENVIRONMENTAL MONITORING PLAN FOR
THE BRENNILIS SITE IN 2016

Sampling point (Quantity)
Aerosols (3)Ambient dose (4)Stream or river (3)Rainwater (1)Spring (1)Milk (1)Grass, moss and tree leaves (3)Vegetables and cereals (2)Phanerogams, aquatic mosses (3)Fish (2)Soils (1)
Sediments (4)Road networks, hydrographics and siteboundaries
Mont d’Arée site

Departmental road
Permanent river or stream
Seasonal river or stream
Site boundary
Municipal borderLand use
Anthropic surface (Structure)
Anthropic surface (Industry or shops)
ForestRiver, stream or lake
Other(source: RGE-BDTOPO@ & BDCARTO@ by IGN - 2019 ed.)/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Nuclear powerplants in the decommissioning process / 3.2
BRENNILIS SITE

• ground water (Vierge spring at Brennilis, groundwater under the site);• the air (Brennilis, La Feuillée, and Forc’han
weather stations);• the food chain (salads, wheat and milk at
Kermorvan, Roz-an-Eol and Tromathiou);• terrestrial plants (grass and underlying soil at
Roz-an-Eol and Tromathiou, mosses at Brennilis
and Landivisiau, oak leaves at Kerrolland andLandivisiau);• sediments, aquatic plants (mosses andphanerogams) and fish in the Ellez river, upstream
and downstream from the Brennilis fish;• ambient radiation (Brennilis and La Feuillée
weather stations).
The impact of the Brennilis site on its
immediate environment
All environmental monitoring measuring results
for the immediate environment around the site are
below decision thresholds, including for tritium,reflecting the fact that no liquid effluents aredischarged and gaseous discharges remain atvery low levels.
EDF has run an environmental monitoring
programme for the site since 2012 in order
to better characterise the potential impact ofdecommissioning operations on the environment.
According to gamma and alpha spectrometry
measurements for the various samples
taken in terrestrial and aquatic components,
radioactivity levels can exceed mean values inFrance, but represent either natural radioactivity(radionuclides from the natural decay of uranium),or residual fallout from the testing of nuclear
weapons (137Cs and plutonium isotopes), and theChernobyl accident to a lesser extent. High levelsof natural and artificial radioactivity can be causedby specific soil and geology configurations andby high rain levels at the site respectively. In theterrestrial component, 3H and 14C activity levels
correspond to ambient levels measured in areas
unaffected by industrial operations. In the aquaticcomponent, 14C levels in fish captured upstream
and downstream are approximately similar. In
the same way, no 14C and 3H have been detected
in aquatic plants since 2012. On the other hand,organically bound tritium and 14C are still detected
in sediments, demonstrating residual fallout at
the site, as revealed in previous studies by IRSN
in 2002 and 2008, and in annual radioecologicalmonitoring. This contamination is, however,decreasing, as the site has not discharged liquid
effluents since 1992.

TABLE 1 / ACTIVITY LEVELS DISCHARGED FROM THE
BRENNILIS FACILITY OVER THE 2012 - 2016 PERIOD

Overview of atmospheric discharges (GBq/year)
Activitylevelsdischarged
2012

Tritium

Other gamma- or
beta-emitting
activation or
fission products

Carbon-14

39.9

0.00118

0.06942013

39.8

0.000025

0.2

2014

31.6

0.0000096

0.233

2015

27.7

0.0000976

0.251

2016

26.4

0.000109

0.049

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /113

TABLE 2-A / REGULATORY MONITORING PLAN DRAFTED BY EDF FOR THE IMMEDIATE ENVIRONMENT OF THE
BRENNILIS SITE

Environment
monitored or type of
testing

114

EDF

Ambient gamma
radiation• 4 dosimeters around the edge of the site
• 5 dosimeters within a radius of 1 km
• 1 dosimeter within a radius of 5 km
• 1 gamma sensor within a radius of 1 km

Soil air• 3 daily measuring and sampling points for gross beta activity with a filter• γ spectrometry if values > 2 mBq/m3• 1 monthly γ spectrometry run for combined daily filters at one single sampler• Continuous sampling based on the prevailing winds with weekly atmospheric tritium
measurements

Rainwater• Continuous sampling based on the prevailing winds with bi-monthly measurements for tritium andgross beta activity

Ground water• 6 sampling points: (3 shafts + 3 pump manifolds): monthly 3H, 40K and gross beta activity
measurements and/or γ spectrometry runs for filtered water and gross beta activity
measurements for TSS

Soils• 1 annual sampling run for topsoil layers: γ spectrometry

Plants• 2 monthly grass samples (including 1 in the prevailing wind direction): monthly γ spectrometry
analyses + annual 14C, HTO and OBT

Milk• 1 quarterly milk sample (including 1 in the prevailing wind direction):
γ spectrometry + tritium + annual 14CSoils• 1 annual sampling run: γ spectrometry

Aquatic flora• 2 annual sampling runs (upstream/downstream: γ spectrometry

Aquatic fauna• 2 five-year sampling runs (upstream/downstream): γ spectrometry + OBT + 14C

Sediments• 2 annual sampling runs (upstream/downstream: γ spectrometry

Farm output• 1 annual sampling run for the main farming output: γ spectrometry, 14C, HTO and OBT

TABLE 2-B / ANNUAL RADIOECOLOGICAL MONITORING PLAN FOR THE IMMEDIATE ENVIRONMENT OF THE BRENNILIS
SITE IN 2017

Gamma
spectrometry

Matrix

HTO

OBT

C-14

Grassland soils

2

Grass

1

Milk

1

Terrestrial moss

2

Oak tree leaves

Fish

2

2

4

4

2

2

2

Aquatic phanerogams

Fe-55

Alpha
spectrometry

1

1
2

Sediment
Aquatic moss

Ni-63

3
2

2

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

4

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Nuclear powerplants in the decommissioning process / 3.2
BRENNILIS SITE

FIGURE 2 / ORGANIC TRITIUM ACTIVITY IN AQUATIC PLANTS AND SEDIMENTS UPSTREAM AND DOWNSTREAM FROM THE
BRENNILIS SITE OVER THE 2012 - 2017 PLANT (Bq/L of combustion water)

Bq/L of combustion water
10,000Downstream sediments
Upstream sediments

1000

Downstream aquatic plants
Upstream aquatic plants
Current background radiation
range for tritium (up to 3 Bq/L)

100

10

1

0.1
2011

2012

2013

2014

2015

2016

2017
115

FIGURE 3 / 14C ACTIVITY FOR AQUATIC PLANTS AND SEDIMENTS UPSTREAM AND DOWNSTREAM FROM THE BRENNILIS
SITE OVER THE 2012 - 2017 SITE (Bq/kg of carbon)

Bq/kg of carbon
1000

Downstream sediments

900

Upstream sediments

800

Downstream aquatic plants
Upstream aquatic plants

700

Current background radiation
range for carbon-14(approx. 227 Bq/kg of C)

600
500
400
300
200
2011

2012

2013

2014

2015

2016

2017

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /3.3. INDUSTRIAL SITES
Malvési site
Since 1959, the Orano plant at Malvési, just
3 km to the north of the town of Narbonne (Audedépartement, see figure 1), has purified uranium
concentrates from mines ("yellow cake") andconverted uranium into UF4. The conversion plantcurrently produces approximately 10,000 tons/
year. The effluents discharged during the uranium
purification process are treated and subsequently
routed to settling and evaporation basins locatedon the site. In addition to the uranium conversion
plant, the Orano site at Malvési is home to old
effluent basins (B1/B2), currently dedicated tostoring historical waste (ECRIN nuclear facility).

Discharges and monitoring plans
Discharges from the Malvési plant only containuranium radionuclides. The liquid effluentsdischarged only contain rainwater and industrial
water via the Tauran canal, which runs alongside
the Malvési site. The Tauran canal runs to
the Robine canal, which crosses the town ofNarbonne before reaching Bages-Sigean lake.
0.2 kg of uranium was discharged in 2016, whichis equivalent to 0.005 GBq of natural uranium.
Uranium discharges into the atmosphere were
halved between 2008 and 2009 and have remained
fairly constant since that time despite fluctuations
from year to year. (see figure 2). 24 kg of uranium
was discharged into the atmosphere in 2016 by thedifferent plant workshops, which is equivalent to
0.6 GBq of natural uranium.

FIGURE 1 / LOCATION OF ORANO'S SITE IN THE AUDE DÉPARTEMENT

116/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
MALVÉSI SITE

FIGURE 2 / TIMELINE FOR RECURRENT ATMOSPHERIC URANIUM DISCHARGES FROM THE MALVÉSI PLANT (GBq/year)

GBq/year
3
2.5
2
1.5
1
0.5
0

2007 2008 2009 2010

2011

The ECRIN nuclear plant also discharges
radionuclides in addition to the effluentsdischarged from plant operations. Small quantitiesof dust are released and suspended in the air due
to wind. They then diffuse, despite the covers fitted
on basins B1/B2 since 2007. Rainwater is collectedfrom the nuclear facility and sent to evaporation
basins or discharged into the Tauran canal, after
processing. The ECRIN facility is mainly likely torelease thorium-230, which is a natural decay
product for uranium-238, and plutonium, an
artificial radionuclide, to a lesser extent.
Finally, a tank of uranyl nitrate at the Malvési
workshops leaked on July 2016. ASN classified
this incident at level 1 on the INES scale (which
has 7 levels), and the leak had no significant
consequences on site personnel or the immediate
environment.

2012

2013

2014

2015

2016

The uranium conversion plant at Malvési
must comply with the rules applicable toEnvironmentally-Classified Sites (ICPE) andwith the provisions of the prefectoral order onmonitoring the environment. ECRIN nuclear facility
monitoring is defined by ASN decisions from a
regulatory viewpoint and is also part of the plant's
monitoring plan. Orano takes aquatic samples
from the Tauran canal on a periodic basis, both
upstream and downstream from the discharge
point. Additional samples are also taken farther
downstream, in the town of Narbonne (Robine
canal) up to the Bages-Sigean lake. The uranium
concentration in the ground water samples taken
near to the site is also measured both in theimmediate vicinity of the site and in a local wellapproximately one kilometre from the site. The
operator also analyses local farming output (fruitand vegetables). In the Malvési environment, IRSN
prefers to measure uranium in surface water (theTauran canal) and terrestrial plants (tree leaves,grass and wheat).

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /117

The impact of the Malvési site on its immediate
environment and public exposure

respectively. The highest uranium-238 activity
levels (over 100 Bq/kg) were recorded to the eastof the site at Livière-Haute, under the prevailingwinds from the Orano site. Activity levels above
10 Bq/kg are occasionally measured at othersampling points, under the prevailing winds tothe east (Tauran) or under secondary winds to thewest of the site (Almérats Hauts and Échine d’Âne).
This configuration means that the activity levels
detected in terrestrial plants reflect the impact (tovarying degrees depending on the sampling site)of the uranium discharged from the Orano site
at Malvési, when compared with measurementsfor plant samples taken in areas unaffected bydischarges from the nuclear industry (0.1-1 Bq/
kg dry).

The impact of the Malvési site is most visible in theterrestrial and aquatic environment for uranium
isotopes (234U, 235U and 238U). In fact, uranium
discharges from the conversion process increase
the uranium activity of atmospheric dust at local
level. This dust then settles on terrestrial plants
and surface water, as well as aquatic plants.
Cypress leaf samples have been taken to the north(in the Œillal village), and south east (Tauran) of
the Orano site (figure 3) since 2011. The samplingsite used in the south (Livière-Basse) between
2011 and 2013 was moved to the east of the site
(Livière-Haute) from 2014. Samples of otherplant matrices (pine needles and grasslands)
were also taken to the west (Almérats Hauts andÉchine d’Âne) and to the east of the site (Tauran),

FIGURE 3 / URANIUM-238 ACTIVITY BY MASS IN PLANT SAMPLES TAKEN IN THE TERRESTRIAL ENVIRONMENT AROUNDTHE ORANO SITE AT MALVÉSI BETWEEN 2011 AND 2017 (Bq/kg fresh)

118
Bq/kg fresh
1000

100

10
Echine d'Âne (grass)
Les Almérats Hauts (pin needles)
Livière-Basse (cypress leaves)
L'Oeillal (cypress leaves)
Tauran (grass)
Tauran (cypress leaves)Livière-Haute (cypress leaves)

1

0.1
Nov
2010

Apr
2012

Aug
2013

Dec
2014

May
2016

Sep
2017

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
MALVÉSI SITE

Uranium-238 activities measured in wheat stalksamples collected from around the eastern edgeof the Malvési site are relatively high (mean value:
3.0 Bq/kg over the 2014-2017 period) and similar tothe values recorded over the previous period (meanvalue: 3.2 Bq/kg for the 2011-2014 period) (figure 4).
Although the measurements recorded since 2010
are lower than those recorded over the previous
three years, they remain well above the values
measured by IRSN in areas unaffected by nuclear
discharges (activity between 0.011 and 0.17 Bq/kg).

On this basis, uranium-238 levels in plants overthe 2014-2017 period are generally similar tolevels during the previous period (2011-2014),
demonstrating that atmospheric uranium-238
activity was similar over the two periods, with amean value of 30 µBq/m3 of air. This mean value
was established using measurements taken
during the 2009-2010 period using a high-flow
sampler installed by IRSN. This mean can becompared with the uranium activity observed in
France in areas unaffected by fuel cycle facilities:
approx. 0.2 µBq/m3 of air.

FIGURE 4 / URANIUM-238 AND THORIUM-230 ACTIVITY BY MASS FOR WHEAT EAR SAMPLES TAKEN TO THE EAST OF THE
ORANO SITE AT MALVÉSI BETWEEN 2007 AND 2017 (Bq/kg dry)

Bq/kg of dried material
100

10

119

1

0.1
U
Th

238

2007

2009

2011

2013

2015

2017

2019

© DR

0.01
2005

230

Aerial view of the Malvési site
RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /mean uranium-238 activity of 0.02 Bq/L) (figure 5).
Figure 6 clearly shows how the mean value has
dropped substantially since the early years of the
21st century.

The concentration by volume of uranium in thesurface water samples taken upstream fromthe discharge points (Tauran canal) is below thedecision threshold (0.5 µg/L) 63% of the time.
Downstream from the discharge point, the mean
concentration by volume of uranium fell over time,
dropping from 4.0 µg/L between 2011 and 2014 to
1.7 µg/L between 2011 and 2017 (equivalent to

In addition, the mean concentration by volume inwater samples taken downstream remains below
the WHO's guide value (30 µg/L).

FIGURE 5 / URANIUM CONTENT OF TAURAN CANAL RIVER WATER UPSTREAM AND DOWNSTREAM FROM THE MALVÉSISITE DISCHARGE POINTS BETWEEN 2011 AND 2017 (µg/L)

µg/L
25
20
15
10
5

Decision thresholds

Upstream fromdischarge points

Downstream, but nearto discharge points

Jul-17Jan-17

Apr-17

Jul-16Oct-16

Apr-16Oct-15Jan-16

Jul-15Jan-15

Apr-15Oct-14Jul-14Apr-14Jan-14Jul-13Oct-13Apr-13Oct-12

Jan-13

Jul-12

Apr-12

Feb-12Oct-11

0Jul-11120

Downstream, at a distancefrom discharge points

FIGURE 6 / TIMELINE FOR RECURRENT URANIUM CONCENTRATIONS BY VOLUME IN TAURAN CANAL RIVER WATER
BETWEEN 1997 AND 2017 (µg/L)µg/L or Bq/L
100

10

1

0.1

0.01
1990

1995

2000

Mean annual uranium concentration (µg/L)

2005

2010

2015

2020

Gross annual alpha index (Bq/L)/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
MALVÉSI SITE

In addition, according to the analyses of groundwater samples taken on the premises of local
residents, the concentration of uranium byvolume varies between sampling points (figure 7).
However, the uranium concentration for any given
sampling location is fairly constant over time.
The mean 238U concentration represents 2.5 µg/L,
which is equivalent to a mean activity for thisradionuclide of 0.031 Bq/L (1), although the sourceof the uranium may remain uncertain (natural or
due to the site).

According to measurements for discharges andenvironmental activity, uranium isotopes are
the main cause of potential exposure for local
residents to discharges from the site. Residents inan area affected by atmospheric discharges to theeast of the plant would absorb an effective doseby inhaling uranium dust equal to 2.0 μSv/year.
This figure is similar to the values calculated by
the operator assuming that residents inhale dustat the edge of the site: 1.7-19 μSv/year. According
to the various food surveys carried out in France,
the wheat and other cereal by-products eaten by
consumers are rarely grown locally. In addition,these wheat plots are owned by Orano and used
for sowing. Despite this, eating one kg of wheatgrown at the edge of the site would involve a doseof 0.01 μSv/kg. In the same way, local residents do
not regularly drink Tauran canal water. However,if they did (e.g. to fill a water bottle), drinking 1 L
of it would lead to an extremely low uranium doseof 0.002 μSv/L.

Other radionuclides have been detected in theimmediate environment of Malvési, in addition
to uranium, however, in far smaller quantities.
These radionuclides, which include thorium-230
and plutonium-239+240, are released by the
ECRIN nuclear facility. On this basis, 230Th activity
recorded in wheat samples taken from the edgeof the site has decreased considerably since since2007 (see figure 4). 230Th activity in wheat (0.1 Bq/kg) since 2010 has remained within the data
bracket established by IRSN in areas unaffectedby discharges (between 0.009 and 0.2 Bq/kg).

121

FIGURE 7 / URANIUM CONCENTRATION BY VOLUME MEASURED IN THE WATER SAMPLES TAKEN FROM FIVE WELLS NEAR
TO THE ORANO PLANT AT MALVÉSI (µg/L)

µg/L
15

10

Decision threshold

Well 1

Well 2

Well 3Well 4Jul-17

Apr-17Jan-17Oct-16

Jul-16

Apr-16

Jan-16Oct-15

Jul-15

Apr-15Jan-15Oct-14Jul-14Apr-14Jan-14Oct-13

Jul-13Apr-13Jan-13

Jul-120

Oct-125Well 5

1. The order of 11 January 2007, on reference limits for raw water quality and water intended for human consumption, does not define the maximum
value for drinking water for alpha-emitting radionuclides such as uranium, but does however state that a specific radionuclide analysis is necessary
if gross a activity exceeds 0.10 Bq/L.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Tricastin site

Radioactive discharges at the Tricastin site

The Tricastin site is located in the Rhône valley
between Bollène and Pierrelatte, near to the EDF
NPP, and is home to several uranium enrichment
and conversion sites (see figure 1). Orano also
operates in the sector of uranium chemistry(mainly uranium defluoridation and denitration),
dismantles former enrichment plants basedon gaseous diffusion and maintains uraniumtransport containers.

Although a high percentage of the industrial
activity at the site involves uranium, artificial
radionuclides, fission or activation products,
are discharged by the Tricastin site facilities(see figures 2 and 3). Discharge levels are fairly
constant since 2010. Carbon-14 and tritium
are the main radionuclides in atmosphericdischarges, at similar quantities (1.7 and 1.3 GBq/
year respectively in 2015). Uranium activities
discharged into the air, for all isotopes, areapproximately 100 times lower (0.04 GBq/year,
2015 data) and are mainly discharged from theconversion unit. Transuranic elements (mainly
plutonium isotopes) and fission products represent
0.0002 and 0.005 GBq/year respectively (2015data). As the prevailing winds in the Rhône valley(80% N-NE and 15% S-SW) disperse discharges
to the north or (predominantly) to the south of thesite, this is the main area affected by atmosphericdischarges from the Tricastin site.

SET (Société d’Enrichissement du Tricastin)enriches uranium using centrifugal techniques at
the Georges Besse II plants, while the EURODIF
gaseous diffusion enrichment plant was shut
down in June 2012. Finally, SOCATRI is responsible
for treating effluents containing uranium, and fortreating, storing and disposing of radioactive andconventional waste.

122

In 2017, seven basic nuclear facilities (INB) andone secret basic nuclear facility (INBS) existed
at the Tricastin site. The site is also home to two
SEVESO-classified environmentally-classified(ICPE) sites.

After activity levels have been checked andtreated, process effluents are routed to the
Donzère-Mondragon canal, to the east of the site.
In 2015, liquid radioactive discharges from thesite mainly comprised uranium isotopes, of whichapprox. 4.4 GBq/year are discharged into thecanal each year. Most of the uranium discharged

FIGURE 1 / LOCATION OF AREVA'S SITE AT TRICASTIN/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
TRICASTIN SITE

FIGURE 2 / TIMELINE FOR RECURRENT ATMOSPHERIC DISCHARGES FROM ORANO'S SITE AT TRICASTIN OVER THE
2009-2016 PERIOD (GBq/year)

GBq/year
100
10Uranium

1

Transuranic elements

0.1

Other fission andactivation products

0.01

Tritium
0.001

Carbon-14

0.0001
2008 2009 2010 2011 2012 2013 2014 2015 2016

FIGURE 3 / TIMELINE FOR RECURRENT LIQUID DISCHARGES FROM ORANO'S SITE AT TRICASTIN OVER THE
2009-2016 PERIOD (GBq/year)

123
GBq/year100
Uranium

10

Transuranic elements
Other fission and activation
products

1

Tritium

0.1

Carbon-14

0.01
2008 2009 2010 2011 2012 2013 2014 2015 2016

comes from the INBS. The aqueous effluentsdischarged from the Orano site at Tricastin also
include artificial radionuclides such as carbon-14(0.3 GBq/year), tritium (0.4 GBq/year), otherfission products (0.23 GBq/year) and transuranicelements (0.08 GBq/year).
Two events at Orano's facilities in Tricastin were
declared by the operator and led to low level
discharges into both the atmosphere and theTechnetium-99

Donzère-Mondragon canal in August 2015 and
September 2016 respectively. The consequencesof these discharges cannot be detected inuranium measurements as part of monitoring,
mainly because the quantities involved are notlarge enough. For example, if a facility normallydischarges 1.7 kg of uranium into the atmosphereeach year, 22.8 g of this uranium cannot be
detected in the environment.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Monitoring the immediate environment of
Orano's site at Tricastin
Orano is supported by a terrestrial and aquatic
sampling network for monitoring radioactivity inthe immediate environment of the Tricastin site:
the Environmental Monitoring Network (Réseau deSurveillance de l’Environnement - RSE). Surface
water samples from the Donzère-Mondragon
canal are taken upstream and downstream fromthe discharge points in order to measure theconcentration by volume of uranium and tritium.
Uranium levels are also monitored in La Gaffière,a river which crosses the site and joins Trop-Longlake to the south of the site. Finally, Orano canaccess a network of piezometers to sample groundwater and detect any effects downstream fromthe site. The terrestrial component is monitored
based on a network of samplers located at points
potentially affected by atmospheric discharges
from the site. Grass and farming output aresampled at these locations, primarily for uranium
and tritium measurements.
124

IRSN also takes samples from the main rivers
mentioned above in order to detect any effects of
the Tricastin site on the uranium concentration ofwater, aquatic plants and sediments. Transuranicelements are also measured in sediments. In theterrestrial component, IRSN monitors activity
by taking plant and food samples at various
locations, in view of measuring uranium, tritiumand carbon-14. In addition, since 2014, IRSN
has taken aerosol samples and uranium isotope
measurements to the south east of the site, tocomplement the atmospheric measurements
taken since 2011.
The impact of the Tricastin site and public
exposure
Uranium isotopes

According to aerosol measurements taken by
IRSN between April 2014 and November 2017,mean uranium-238 activity represents 1.1 µBq/m3
of air, which is very similar to the value recorded
between January 2012 and August 2013 (0.9 µBq/
m3 of air). This concentration by volume, which ishigher than the uranium activity level measured
in areas unaffected by discharges from fuel cycle
units (0.2 µBq/m3 of air), and the proportion of
uranium-235 in the air, reflect the local effects ofuranium discharges from the Orano facilities at
Tricastin in the atmosphere. In addition, activity
levels by volume considerably exceeded meanvalues (i.e. more than 10 µBq/m3 of air) on two
occasions (April 2014 and May 2016), although thesource of the extra activity was not clearly identified(figure 4). It is also important to remember thatthe incidental discharge of depleted uranium fromfacility "W" (October 2013) led to ambient 238U
activity of more than 100 µBq/m3 of air.

FIGURE 4 / 238U ACTIVITY MEASURED IN AMBIENT AIR TO THE SOUTH OF ORANO'S SITE AT TRICASTIN SINCE 2012(µBq/m3 of air)µBq/year
1000

Incidental discharge fromfacility "W" - October 2013

100

10

1

0.

0.01
Feb-11

Jul-12

Nov-13Apr-15/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

Aug-16

Dec-17

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
TRICASTIN SITE

Living near to the sampler or at a similar distancefrom the site under the prevailing winds would leadto a dose after inhaling uranium dust of 0.06 μSv/
year; this estimate is very similar to that for theprevious period: 0.05 µSv/year.

Uranium-238 activity in the tree leaf samples
taken in the same area is higher (mean value:
2 Bq/kg) and varies between species. All of thesemeasurements reflect the impact of ambienturanium activities and therefore site discharges
on plants. Uranium-236, an artificial uranium
isotope, measurements in these matrices also
confirm these conclusions.

This ambient activity leads to uranium-238
concentrations in plants, and particularly in thegrass samples taken by Orano as part of regulatory
monitoring. The activity levels measured are fairly
stable and remain between 0.32 and 0.52 Bq/kg
dry on average, depending on the sampling site(table 1). If we compare these figures with the
2011-2014 period, a slight increase in uranium
activity in this matrix becomes apparent.

On the other hand, uranium-238 activity by massin wheat samples taken to the south of the site
in 2016 is surprisingly low (0.01 Bq/kg) comparedwith previous values, and is at the lower end of
the bracket for IRSN data for areas unaffected byfuel cycle facilities (activity levels between 0.011
and 0.17 Bq/kg).

TABLEAU 1 / MEAN URANIUM-238 ACTIVITY BY MASS IN GRASS SAMPLES TAKEN FROM THE ENVIRONMENTAL
MONITORING NETWORK DURING THE 2015-2017 AND 2011-2014 PERIODS (Bq/kg dry)

2015-2017
Uranium-238 (Bq/kg)

2011-2014*
Uranium-238 (Bq/kg)

ID1 - Faveyrolles

0.35

0.14

ID2 - Prés Guérinés

0.50

0.20

ID3 - Bollène-la-Croisière

0.52

0.24

ID4 - Lapalud

0.32

0.11

© AREVA* The activity levels provided for 2011-2014 from the RNM database were incorrect. The data shown here were calculated using the U concentrations
by mass measured during this period.

Aerial view of the Tricastin site
RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /125

A slightly higher mean concentration was recorded
at Gaffière, downstream from the site (1.8 µg/L,
which gives a mean uranium-238 activity of
0.02 Bq/L) when compared with upstream activity(1.1 µg/L on average) (see figure 5). Considering allof the surface water samples analysed, the TropLong lake samples contain the highest uranium
levels by far (2.9 µg/L on average for the 20152017 period, corresponding to mean uranium-238
activity of 0.03 Bq/L), although the concentration
by volume decreased over the 2011-2014 period(3.6 µg/L on average, over this period).
A higher mean uranium isotope activity wasrecorded in Gaffière sediments downstream
from the Orano site (mean uranium-238 activityof 26 Bq/kg in sediments) when compared with

upstream activity (mean uranium-238 activity of
9.1 Bq/kg in sediments (see table 1). Uranium-238
activity in aquatic plants is more homogeneousthan in sediments and no uranium contamination
was found in this matrix downstream from thesite (see tableau 2). Based on these observations,
we can conclude that the Gaffière sediments andsurface water are contaminated by uranium fromthe site. However, sediment contamination levels
downstream from the site are very low comparedwith mean uranium-238 activity in sediments
in France measured by IRSN, which represents
40 Bq/kg dry. Local residents do not drink Gaffière
river or Trop-Long lake water. However, if theydid (e.g. to fill a water bottle), drinking 1 L of it
would lead to an extremely low uranium dose of
0.003 μSv/year.

FIGURE 5 / URANIUM CONCENTRATION BY VOLUME MEASURED IN THE SURFACE WATER SAMPLES TAKEN FROMIMMEDIATE ENVIRONMENT OF THE ORANO SITE AT TRICASTIN SINCE 2012 (µg/L)

µg/L
126

5

4

3

2

1

0
Oct-12Oct-13ES6 Mayre Girarde
ES5 Mayre GirardeOct-14
ES8 Channel downstream
from the discharge point
ES7 Channel upstream
form the discharge point

Oct-15Oct-16

ES3 Gaffière,
downstream from the site
ES1 Gaffière,
upstream from the site

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

Oct-17Trop-Long lake

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
TRICASTIN SITE

According to samples and measurements forDonzère-Mondragon canal water, no significant
difference exists between the uranium
concentration downstream and upstream of thedischarge point (1.15 and 1.18 μg/L on average,
respectively). The same is true for sediment andaquatic plant samples taken downstream fromthe discharge point in the Donzère-Mondragon
canal, which are not contaminated by uranium ortransuranic elements (tables 2 and 3).

If we compare figures for surface water andsediment water samples taken in the immediate
vicinity of the Orano site in Tricastin, it becomesapparent that the mean concentration of uranium
by volume is globally constant at approx. 1.2 μg/L
(see figure 6). Uranium contamination of sedimentwater at a few points, mainly to the south of thesite, has persisted since the study conducted by
IRSN in 2010, in the same way as at Mas de Flore,
where the mean concentration is stable (12 µg/L).

TABLE 2 / URANIUM, PLUTONIUM AND AMERICIUM (241Am) ISOTOPE ACTIVITY BY MASS IN SEDIMENT SAMPLES TAKEN IN
THE AQUATIC ENVIRONMENT AROUND THE ORANO SITE AT TRICASTIN BETWEEN 2015 AND 2017 (Bq/kg dry)

Uranium-234(Bq/kg dry)

Uranium-235(Bq/kg dry)

Uranium-238(Bq/kg dry)Plutonium (239+240) Américium-241(Bq/kg dry)
(Bq/kg dry)Donzère-Mondragon canal,
upstream from discharges

18

0.8

17

0.10

0.05

Donzère-Mondragon canal,
downstream fromdischarges

15

0.6

15

0.05

0.05

Gaffière, upstream fromdischarges

9.4

0.4

9.1

0.09

< 0.05Gaffière, downstream fromdischarges

27

1.3

26

0.12

0.18

Lauzon

6.2

0.4

6.6

< 0.050.06

TABLE 3 / URANIUM ISOTOPE ACTIVITY BY MASS IN AQUATIC PLANT SAMPLES TAKEN IN THE AQUATIC ENVIRONMENTAROUND THE ORANO SITE AT TRICASTIN BETWEEN 2015 AND 2017 (Bq/kg dry)

Uranium-234 (Bq/kg)

Uranium-235 (Bq/kg)

Uranium-238 (Bq/kg)

Donzère canal - Upstream fromthe NPP

1.0

0.04

1.0

Donzère canal - Downstream fromthe NPP

2.1

0.1

2.0

Gaffière - Upstream from the NPP

1.2

0.05

1.1

Gaffière - Downstream from the NPP

1.1

0.05

1.0

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /127

FIGURE 6 / MAP SHOWING THE MEAN URANIUM CONCENTRATION BY VOLUME MEASURED IN THE GROUND SURFACEWATER SAMPLES COLLECTED USING THE DIFFERENT PIEZOMETERS IN THE IMMEDIATE ENVIRONMENT OF THE ORANO
SITE AT TRICASTIN BETWEEN 2015 AND 2017 (µg/L)

128

Tritium and carbon-14

Carbon-14 activity in fish captured in the Rhône
river at Mornas in 2015 and 2016 (86 and 89 Bq/kg
fresh respectively) exceeds background radiationin the aquatic environment (approx. 20 to 25 Bq/kg
fresh), as recorded upstream of NPPs. Reminder:
fish and mollusc samples in the Rhône river are
affected by the carbon-14 discharged from NPPs
located on the river, and 14C activity increases
downstream, reaching peak values of approx. 150- 170 Bq/kg fresh (see. figure 5 in chapter 3.1). On
this basis, fish measurements based on samples
from Mornas cannot be used to differentiate
between carbon-14 from the Tricastin nuclear site,
particularly as discharges from Orano's facility at
Tricastin containing this radionuclide (0.35 GBq/
year in 2016) are much lower than those for the
Tricastin NPP (40.6 GBq/year).

In the terrestrial component, the carbon-14
contamination of plants is extremely discreet andonly affects the immediate site environment. On
this basis, it can only be detected using a very
sensitive indicator: specific activity. This indicator
represented 269 Bq/kg C on average in 20142016 in the grass sample affected by discharges,
which is slightly above the expected value in areas
unaffected by discharges (approx. 230 Bq/kg C).
While we cannot identify the percentage of thisadded activity discharged by Orano, we can takenote that this activity (1.43 GBq/year) is 200 times
less than that of the nearby EDF NPP (413 GBq/
year).
With tritium, the probable predominance of EDF
NPP discharges over environmental activities iseven clearer. Mean tritium activity measurements
for Donzère-Mondragon canal water samples/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
TRICASTIN SITE

FIGURE 7 / TRITIUM ACTIVITY BY VOLUME MEASURED IN DONZÈRE-MONDRAGON CANAL RIVER WATER SAMPLESDOWNSTREAM FROM THE DISCHARGE POINTS AT ORANO'S SITE AT TRICANSTIN BETWEEN 2011 AND 2017 (Bq/L)

Bg/L
20
18
16
14
12
10
8
6
4
2
0
Feb-11

Feb-12

Feb-13

Feb-14

Decision thresholds

Feb-15

Feb-16

IRSN

Feb-17

Feb-18Orano
129

taken by Orano and IRSN between 2015 and 2017
are very similar: 6.3 and 6.7 Bq/L respectively(see figure 7). These values are also close to
the synthetic values recently calculated by
IRSN for this part of the Rhône river (4.7 Bq/L
downstream from Tricastin on average). These
activities are mainly attributable to discharges
from the EDF NPP (see chapter on EDF NPPs).
Tritium discharges from the Orano site (0.3 GBq/
year in 2016) are indeed very low compared with
discharges from the adjacent EDF NPP (42,000 GBq
in 2016). In addition, the NPPs located upstream
also discharge this radionuclide, which transfers
easily and can be measured in water. Tritium
activity in food is generally low: mean values of
5.7 and 3.5 Bq/L were detected in goat's milk from
Lamotte-du-Rhône and Mondragon respectively
and 3.3 Bq/L of combustion water in Bollène-laCroisière lettuce. Tritium activity levels in foodcorrespond to those expected in an environment
which is relatively little or not affected by local
discharges.

Conclusions
The impact of the Orano site at Tricastin can bedetected using environmental measurements, but
is low and mainly comprises ambient uranium,
contaminated terrestrial plants near to the site
and the Gaffière river. According to ambient
measurements, local residents could inhale a doseof approximately 0.06 µSv/year. This dose is similar
to, although lower than that modelled by Oranoon the basis of the activities discharged in 2016
(0.13 μSv/year). According to these calculations,this dose inherent to inhaling uranium would
represent almost 60% of the total dose likely to beabsorbed due to discharges from Orano facilties.
The impact of atmospheric carbon-14 discharged
from the Orano site cannot be differentiated inenvironmental measurements due to the effluentsdischarged from the EDF NPP located on the site.
The Orano effluents may rank second in terms of
its contribution to the total dose.
The tritium activity levels measured in DonzèreMondragon canal water samples, and carbon-14
activity levels measured in fish from the same
canal, are mainly attributable to liquid effluentsdischarged by EDF, from the Tricastin NPP, as wellas NPP located farther downstream.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Romans-sur-Isère site
The FRAMATOME site at Romans-sur-Isère in the
Isère valley is home to two basic nuclear facilities(figure 1). The first facility (INB63) is specialised
in producing fuel elements for research reactors.
The second facility (INB98) produces nuclear fuels
used in pressurised water reactors. This INB
transformed 620 tonnes of enriched uranium into
fuel assemblies in 2016.
Discharges and monitoring plans
Aqueous effluents which potentially containuranium (such as process water, soil washingwater, washing effluents, etc.) are directed toa water treatment plant known as Neptune.
After the water has been treated, the mainradionuclides discharged into the Isère include
uranium isotopes, and, to a lesser extent, fission
products and transuranic elements (figure 2).
These radionuclides are also discharged into
the atmosphere via the plant stacks (figure 3).

Levels of uranium isotope activity discharged haveprogressively decreased since 2008. The sudden
decrease in gaseous discharges containing
uranium isotopes since 2015 is the outcome of thetemporary shutdown of the recycling workshop,
which has been progressively restarted since 2017.
The monitoring plan implemented by FRAMATOME
aims to measure these radionuclides in the
different matrices of the terrestrial and aquatic
environment. On this basis, in the aquaticcomponent, surface water, sediment, moss, reed
and fish samples are taken from the Isère river,both upstream and downstream of discharge
points (figure 1). In the terrestrial component,
plant (tree leaves, grass, terrestrial mosses) andwheat (wheat) samples are taken in areas affectedby atmospheric discharges from the site (S and Nof the site) and areas unaffected by discharges.
In addition, samples (aerosols and tree leaves)and measurements are also taken at the site, in
all four directions, to assess the consequences ofatmospheric discharges near to sites.

130

FIGURE 1 / MAP SHOWING THE LOCATIONS OF SAMPLING POINTS IN THE IMMEDIATE ENVIRONMENT OF THE ROMANS-SURISÈRE PLANT/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
ROMANS-SUR-ISÈRE SITE

FIGURE 2 / TIMELINE FOR RECURRENT LIQUID DISCHARGES FROM FRAMATOME'S FACILITY AT ROMANS-SUR-ISÈRE
(GBq/year)

GBq/year
10
1
0.1
0.01

Uranium isotopes

0.001

Transuranic elements(decision thresholds)

0.0001
2004

Fission products(decision thresholds)
2008

2012

2016

FIGURE 3 / TIMELINE FOR RECURRENT ATMOSPHERIC DISCHARGES FROM FRAMATOME'S FACILITY AT ROMANS-SURISÈRE (GBq/year)

GBq/year
0.1

0.01

0.001
Uranium isotopes
Transuranic elements(decision thresholds)

0.00010.00001
2004

Fission products(decision thresholds)
2008

2012

2016

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /131

Ambient uranium isotopes discharged lead to anincrease in atmospheric aerosol activity levels.
On this basis, the mean uranium isotope activity
measured in aerosol samples taken at the site is
between 0.19 and 0.20 µBq/m3 and between 0.86
and 1.10 µBq/m3 for uranium-235 and uranium-238
respectively (table 1). The decrease in meanambient activity by volume compared with theprevious study period (2011-2014: 1.5 - 2.1 µBq/m3
for uranium-238) correlates to the annual
decrease in total effluents discharged (figure 3).
These values must be compared with the uranium
activity levels recorded in France in areas
unaffected by fuel cycle facilities: approx. 0.2 µBq/
m3 of uranium-238.

132

The concentrations measured in tree leaf
samples collected off-site are lower than onsite and vary between 0.6 and 1.8 µg/kg dry.
The mean uranium concentration in the otherplant samples taken in the immediate environment
around the site are slightly higher (table 2). On
this basis, on average, uranium concentrations
by mass in grass samples are higher to the northand south (11.5 and 12 µg/kg respectively) whencompared with measurement results to the east
and west (4.7 and 5.2 µg/kg respectively).
No increase in uranium concentration was detectedin Isère water analyses taken downstream fromthe discharge point compared with upstream
sample results. In fact, weighted concentrations
are similar both upstream and downstream(1.69 and 1.74 μg/L respectively). Mean weighted
uranium concentrations in ground water samples
are similar (0.40 - 1.06 μg/L). Variations areundoubtedly due to the characteristics of theaquifers.

These atmospheric aerosols contaminated bysite effluents settle on the tree leaves, leading todetectable levels of uranium activity. The highest
uranium concentration by mass is measured inside
the site, in the south part, and a mean concentrationof 47 µg/kg dry was recorded (figure 4). The meanuranium concentration by mass is lower in otherparts of the site, e.g. 17 µg/kg to the east of the site.
Although the reduction in activity detected since2012 is far less sudden, this decrease is due to the
reduction in effluents discharged as the recycling
unit has been shut down.

TABLE 1 / MEAN ACTIVITY LEVELS FOR URANIUM ISOTOPES IN AEROSOLS SAMPLES TAKEN AT FRAMATOME'S SITE AT
ROMANS-SUR-ISÈRE BETWEEN 2015 AND 2017 (µBq/m3)

U (µBq/m3)

234

East

< 14

U (µBq/m3)

U (µBq/m3)

235

U (µBq/m3)

236

0.20

238

0.86

< 0.22

North

< 13

0.19

< 0.22

0.88

West

< 13

0.19

< 0.22

1.10

South

< 12

0.19

< 0.21

1.00

TABLE 2 / WEIGHTED URANIUM CONCENTRATION IN PLANT SAMPLES TAKEN IN THE IMMEDIATE ENVIRONMENT OF
FRAMATOME'S SITE AT ROMANS-SUR-ISÈRE (µg/kg dry)

Location of sampling
pointsGrassTerrestrial mosses
Wheat

North

East

South

West

Distance from the site (m)

200

200

750

1200

Uranium (µg/kg dry)

11.5

4.7

12

5.2

Distance from the site (m)

750

1000

1250

Uranium (µg/kg dry)

114

156

145

Distance from the site (m)

200

2000

750

Uranium (µg/kg dry)

2.7

2

< DT

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
ROMANS-SUR-ISÈRE SITE

FIGURE 4 / WEIGHTED URANIUM CONCENTRATION IN PINE NEEDLE SAMPLES TAKEN AT FRAMATOME'S SITE AT
ROMANS-SUR-ISÈRE, BETWEEN 2011 AND 2017µg/kg dry
1000

100

10

133
1
Jan-2011

Jan-2012

Jan-2013
East

Jan-2014
North

According to the results of uranium isotope
analyses in sample matrices from the Isèreriver, no additional uranium isotopes are present
downstream from the discharge point comparedwith upstream samples (table 3). Uranium-238
activity levels measured in reeds, sediments
and fish are similar upstream and downstream(uranium-238 in sediments: 5.7 and 5.3 Bq/kg
fresh respectively). Furthermore, no uranium-236,
an artificial uranium isotope, was detected as
per the results of analyses on samples from theaquatic environment.

Jan-2015

West

Jan-2016

Jan-2017

South

According to the levels of environmental activity
measured, uranium isotopes are the main causeof potential exposure for local residents toatmospheric discharges from the site. Residents
in an area affected by atmospheric discharges
from the plant would absorb a maximum doseby inhaling uranium dust equal to 0.15 μSv/year.
This dose is below the estimated value fromthe previous study period (2011-2014: 0.5 µSv/
year), as uranium discharges have decreased
significantly, and the proportion of uranium-234 in
the air, based on more precise estimates, is lower(4 µBq/m3 of air).

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /TABLE 3 / MEAN URANIUM ISOTOPE ACTIVITY MEASURED IN SAMPLES TAKEN IN THE ISÈRE RIVER UPSTREAM AND
DOWNSTREAM OF THE DISCHARGE POINT AT FRAMATOME'S SITE AT ROMANS-SUR-ISÈRE

Reeds(Bq/kg fresh)

Aquatic
mosses(Bq/kg fresh)

Sediment(Bq/kg fresh)

134

Discharges
250 m upstream

Discharges 2.5 km
downstream

Discharges 6 km
downstream

Discharges 9 km
downstream

Upstream from
Pizançon dam

Pizançon dam

Romans sur-Isère
town centre

Downstream fromthe Romans-surIsère wastewater
treatment plantBeaumontMonteux dam

234

U< 0.11< 0.11< 0.11235

U0.0001±0.00003

0.00016±0.00004

0.00007±0.00002

236

U< 0.0011< 0.0012< 0.0011

238

U

0.0011±0.0003

0.0014±0.0003

0.007±0.001

234

U

2.9±0.6

1.8±0.4

235

U

0.4±0.1

0.20±0.04

236

U< 0.012< 0.018238

U

7.7±0.2

3.3±0.7

234

U

< 28

< 30

< 28

235

U

0.3±0.05

0.3±0.06

0.4±0.08

236

U

< 0.3

< 0.4

< 0.3

238

U

5.3±1.1

5.7±1.1

6.7±1.3

234

U< 0.11< 0.09< 0.08235

U0.00004±0.00001

0.0002±0.00004

0.00009±0.00002

236

U< 0.001< 0.001< 0.0008

238

U

0.001±0.003

0.004±0.0009

0.002±0.0005© Framatome

Fish(Bq/kg fresh)

Discharges
1.5 km upstream

Aerial view of the Romans-sur-Isère site

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITE

La Hague site

Discharged effluentsThe facilities at the Orano Cycle site (formerly
the AREVA NC site) at La Hague are used for the
first stage in processing spent fuels post-nuclear
reactor operations. The site is adjacent to theradioactive waste storage facility on the Channel(CSM) run by ANDRA. This storage facility collected
almost 530,000 m3 of highly and weakly radioactive
waste between 1969 and 1994 (see figure 1). The
CSM no longer receives waste and is currently
monitored.

Figure 2 shows the activities of the mainradionuclides discharged in gaseous effluentsfrom the Orano Cycle site at La Hague. Annual
activity levels for discharges have remained fairly
constant over time since the late 1990's. Krypton-85
is the main contributor by far, followed by tritiumand carbon-14. Iodine-129 ranks 4th and is theprincipal component of iodine discharges. Muchlower amounts of other β−γ emitting radionuclides
are found in discharges, particularly including
ruthenium-106 and antimony-125, preventing
quantification. The values shown in figures 2
and 3 for β−γ and α emitters are total decisionthresholds.

Given that these two sites are next to each other,monitoring data is combined into one single
chapter as part of this radiological report.

FIGURE 1 / AERIAL VIEW OF THE ORANO CYCLE SITE AT LA HAGUE AND ANDRA CSM

135

Orano Cycle site

© ANDRACSM site

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 2 / OVERVIEW OF ATMOSPHERIC DISCHARGES FROM ORANO'S FACILITY AT LA HAGUE (TBq/year)

TBq/year
1,000,000
100,000
10,000
1000
100
10
1
0.1
0.01
0.001
0.00001
0.000001
0.0000001
1996

1998

2000

2002

2004

2006

2008

2010

2012

2014

2016

2014

2016

Kr
H
C
Iodines ( I > 90%)
Other artificial beta-gamma emitters (decision thresholds)
Artificial alpha emitters (decision thresholds)
85

136

3

14

129

FIGURE 3 / OVERVIEW OF LIQUID DISCHARGES FROM ORANO'S FACILITY AT LA HAGUE (TBq/year)

TBq/year
100,000
10,000
1000
100
10
1
0.1
0.01
1996

1998

2000

2002

2004

2006

2008

2010

2012

14
106
H
C
Iodines
Ru 90Sr 137Cs 134Cs
Other beta-gamma emitters (decision thresholds)
Alpha emitters (decision thresholds)

3/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 201760

Co

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITE

FIGURE 4 / RAINWATER AND WASTEWATER DISCHARGES FROM ORANO'S SITE AT LA HAGUE

137

Tritium is the main radionuclide discharged inliquid effluents by far, followed by carbon-14 andiodine isotopes, particularly iodine-129 to a lesser
extent. The respective proportions are similar
to those detected for gaseous discharges (seefigure 3). Liquid effluents are discharged at sea,
via a duct which discharges approximately 5 km
offshore from Goury port.

Drainage from the liquid effluents discharged
from the Channel centre, which are currently
covered and planted, are collected and routed to
the Orano site for discharge at sea. The activity
levels in question are insignificant compared withthose recorded in Orano discharges. Tritium is themain radionuclide discharged in liquid effluents(2.1 GBq in 2016).

Rainwater and wastewater are discharged into
three streams based on their sources: les Combes,
St-Hélène and les Moulinets.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Monitoring plans for the immediate
environment of the La Hague site

radionuclides discharged by the facilities and thedifferent matrices potentially affected.

Details of the regulatory monitoring plan
implemented by Orano in the immediate environmentof the La Hague site and IRSN's monitoring plan canbe found in Tables 1 and 2. The monitoring plan isparticularly large in scope due to the number of

Figure 5 shows the locations of monitoring
points, where terrestrial, continental aquatic andatmospheric samples are taken. Figure 6 showsdetails of the locations of marine sampling sites.

TABLE 1 / TERRESTRIAL ENVIRONMENTAL MONITORING PLANS FOR THE LA HAGUE SITE, DRAFTED BY ORANO AND BY IRSN

Environment monitored ortype of testing

Orano

IRSN

Soil air• 5 sampling points; gross alpha and beta
activity measurements with a daily filter• γ spectrometry if gross β activity > 2 mBq/m3• Alpha spectrometry for total monthly value
for the filter, Iodines with a weekly cartridge,
weekly 3H, bimonthly 14C, monthly 85Kr

• 1 station; gross α and β and γ spectrometry
measurements with a weekly filter, onemonthly Pu measurement with a weekly
filter (1st period), iodines with a weekly
cartridge, bimonthly 3H

Dosimeter• 11 fence locations, monthly measurementsRain• 2 samplers for weekly free tritium
measurements• gross α and β and γ spectrometry if
the α or β count is significant

Ground water• 53 samplers, including around a dozen
off-site; monthly gross α and β, andfree tritium measurements-

Drinking water• 12 samplers; monthly gross α and β,
and free tritium measurements-

Stream and spring water• 7 samplers for 6-monthly or weekly gross α
and β, free tritium and γ spectrometry
measurements• Monthly 90Sr and γ spectrometry
measurements for 4 springs• 6 annual to quarterly sampling points; grossα, gross β, γ spectrometry and free tritium
measurementsSoils• 7 sampling points; quarterly γ spectrometry
measurements

-

Grass

• 10 points; monthly or quarterly γ
spectrometry bound tritium, 14C, and 129I
measurements; annual α spectrometry• 1 monthly sampling point; 14C, bound andfree tritium and γ spectrometry
measurementsMilk• 5 points; monthly γ spectrometry 90Sr, 129I, 14C
and free tritium measurements• 3 quarterly sampling points; 90Sr, 129I, 14C, freetritium and γ spectrometry measurementsMeat• 2 to 3 annual samples; γ spectrometry, αspectrometry, free and bound tritium, 14C,
and 129I measurements and 90Sr
measurements for one sample.

• 1 annual sample; bound 3H, 14C,
γ spectrometry and 90Sr measurements

Other food (vegetables,
eggs, honey, etc.)• 1 annual cereal sampling run;• 10 to 12 annual samples; annual γ
α spectrometry (Pu/Am), 90Sr;
spectrometry, α spectrometry, bound tritium,14
γ spectrometry, 14C, and boundC, and 129I measurements (Pu, 244Cm) and90
spectrometry measurements.
Sr measurements.

Aquatic plants• 3 sampling points used to collect 12 annual
samples; γ spectrometry and bound tritium
measurements

Sediments/beach sand• 26 points: 10 off-shore and 13 low-tidesampling points; quarterly α and γ
spectrometry measurements

138• 1 sampler, monthly free tritium
measurements• 10 annual to quarterly sampling points;
α spectrometry (Pu/Am and Cm for3 samples), 90Sr, γ spectrometry
measurements/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITETABLE 2 / MARINE ENVIRONMENTAL MONITORING PLANS FOR THE LA HAGUE SITE, DRAFTED BY ORANO AND BY IRSN

Environment
monitored or type of
testing

Orano

IRSN

Seawater• 5 points: 2 on the coast, 3 offshore; daily 129I andfree tritium measurements at Anse des• 1 sampling points; quarterly free tritium
Moulinets; monthly or quarterly 90Sr andmeasurements
α spectrometry measurementsAlgae• 6 sampling points used to collect 24 annual
samples; α and γ spectrometry, 129I, 14C
measurements• 3 quarterly sampling points; α spectrometry(Pu/Am/ Cm), 90Sr and γ spectrometry
measurements

Fish• 3 sampling points used to collect 24 annual
samples; α and γ spectrometry, 129I and 14C
measurements• 3 annual sampling points; α spectrometry (Pu/Am), 90Sr and γ spectrometry measurements

Molluscs• 5 to 6 sampling points used to collect 40 to 50
annual samples; α and γ spectrometry, 129I and14
C measurements• 3 quarterly to 6-monthly sampling points;
α spectrometry (Pu/Am/ Cm) and γ
spectrometry measurements

Shellfish• 3 sampling points used to collect 12 annual
samples; γ spectrometry, 129I and 14C
measurements-

FIGURE 5 / MAP SHOWING THE LOCATION OF THE LA HAGUE SITE, AND THE MUNICIPALITIES AND SAMPLERS USED FOR
TERRESTRIAL AND ATMOSPHERIC SAMPLING

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /139

Due to the strong ocean currents near to thedischarge channel at La Hague, the impact ofOrano discharges at sea can be detected beyond
the immediate environment of the site and theChannel in general. The measurements taken
by EDF near to coastal NPP (Flamanville, Penly,

Paluel et Gravelines) and by IRSN can also be used
to characterise these discharges. Figure 6 shows
the locations of marine sampling points near to
EDF's nuclear powerplants.

FIGURE 6 / MAP SHOWING THE LOCATIONS OF THE MARINE SAMPLERS AROUND THE LA HAGUE SITE

140

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITE

FOCUS ARTICLE
IRSN'S OMONVILLE-LA-PETITE SAMPLER

Since 1994, IRSN has accessed a test zone at
Omonville-la-Petite, to the north of the Orano siteat La Hague. This technical zone is located under
the prevailing winds and is home to various
measuring instruments, which IRSN uses to monitor atmospheric discharges from the La Hague
facility and run studies, particularly focusing on the behaviour of tritium in the air and inecosystems.
In 2017, IRSN decided to combine the different measuring systems and other equipment used at
Omonville-la-Petite for the purposes of regular monitoring:• Téléray sensor (proportional counter) and gamma spectrometry system• tritium bubbler• passive tritium trap;• OPERA-AIR 80 aersol sampler;• rainwater collector.
FIGURE A / INSTRUMENTATION INSTALLED AT THE IRSN SAMPLER AT OMONVILLE-LA-PETITE141

The sampling station in IRSN's new OPERA-AIR 80 network has been installed at Omonvillesince 2014 and can be used to filter particles (aerosols) by taking in ambient air at a flow rate of 80
m3/h and trapping the gaseous iodine in a specific channel (3 m3/h) using a sampling systemcomprising a specific cartridge. The filter and cartridge are replaced on a weekly basis and sent to
the laboratories at Vésinet for analysis.
Figure B shows particulate ambient iodine-129 activity by volume, which is one of the only
artificial radionuclides to still be regularly detected by IRSN at this station. Beryllium-7 and lead210 are the other two radionuclides systematically measured by gamma spectrometry. Both arenatural in origin. This figure also shows the link between the presence of iodine-129 in the air andthe increased dose rate attributable to La Hague effluents (see focus article on krypton-85 on page146). Finally, the particulate iodine-129 measurement illustrates the efforts made by IRSN tocontinue to improve metrological performances after the acquisition of sensors with an anticosmic system in 2016 and the switch to 24-hour counting for aerosol filters. Efforts are still being
made to reduce decision thresholds by using more compact filters, after a series of conclusive tests
launched since 1 January 2018.
●●●

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /●●●

FIGURE B / PARTICULATE IODINE-129 ACTIVITY BY VOLUME FOR THE IRSN SAMPLER ATOMONVILLE-LA-PETITE

120

100

100
10

80
60

1

40

Dose rate (nSv/h)

Activity by volume (µBq/m3)

140

0.1
20
0.01
27/12/14
24/01/15
21/02/15
21/03/15
18/04/15
16/05/15
13/06/15
11/07/15
08/08/15
05/09/15
03/10/15
31/10/15
28/11/15
26/12/15
23/01/16
20/02/16
19/03/16
16/04/16
14/05/16
11/06/16
09/07/16
06/08/16
03/09/16
01/10/16
29/10/16
26/11/16
24/12/16
21/01/17
18/02/17
18/03/17
15/04/17
13/05/17
10/06/17
08/07/17
05/08/17
02/09/17
30/09/17
28/10/17
25/11/17
23/12/17
20/01/18
17/02/18

0

I

129

Dose rate

The following figure shows particulate and gaseous iodine-129 activity by volume for the
Omonville sampler. It would appear that iodine-129 activity by volume mainly comprises gaseousiodine trapped in activated carbon cartridges with other iodine isotopes discharged from the La
Hague facilities (iodine-131 and iodine-133).
FIGURE C / PARTICULATE AND GASEOUS IODINE-129 ACTIVITY BY VOLUME FOR THE IRSN SAMPLER ATOMONVILLE-LA-PETITE

100

Activity by volume (µBq/m3)

10

1

0.1

0.01
27/12/14
24/01/15
21/02/15
21/03/15
18/04/15
16/05/15
13/06/15
11/07/15
08/08/15
05/09/15
03/10/15
31/10/15
28/11/15
26/12/15
23/01/16
20/02/16
19/03/16
16/04/16
14/05/16
11/06/16
09/07/16
06/08/16
03/09/16
01/10/16
29/10/16
26/11/16
24/12/16
21/01/17
18/02/17
18/03/17
15/04/17
13/05/17
10/06/17
08/07/17
05/08/17
02/09/17
30/09/17
28/10/17
25/11/17
23/12/17
20/01/18
17/02/18

142

I Decision thresholds

129

Particulate 129I

Decision thresholds for particulate 129I

Gaseous 129I

Decision thresholds for gaseous 129I●●●

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITE●●●

IRSN uses various sampling systems to monitor tritium discharges in the atmosphere from thefacilities at La Hague in addition to monitoring dose rate and aerosols. Discharges have beenmonitored with a bubbler set up at Omonville since 2015. The bubbler traps ambient tritium inthe form of water vapour (HTO) and aquatic tritium as a gas (HT) prior to analysis by liquid
scintillation. A rainwater collector was added to the system in 2017, and is used to collect wet
deposits.
Combining these different units at the same sampling station means that measurements can becompared, in addition to monitoring activity levels in the different atmospheric components.
Figure D shows the relationship between tritium (HTO) measurements in ambient water vapour
and in rainwater. This figure also shows the low activity levels currently recorded in the atmosphere,
and the measuring equipment required to detect significant tritium values (< 5 Bq/L).
FIGURE D / AMBIENT HTO TRITIUM ACTIVITY MEASURED IN AIR AND RAINWATER AT THE IRSNSAMPLING STATION AT OMONVILLE-LA-PETITE

Bq/m 3
0.35

Bq/L
35

0.3

30

0.25

25

0.2

20

0.15

15

0.1

10

0.05

5

143

0
0
6
5
5
7
5
5
6
6
6
5
7
7
7
1
1
1
1
1
1
1
1
1
1
1
1
1
r - un r - un r - un cccpppnJa
Ap
J
J
J
Se
Se
Se
De
De
De
Ma
Ma
Ambient 3H - HTO

Decision thresholds (ambient 3H - HTO)

Rainwater 3H

Decision thresholds (rainwater 3H)

IRSN developed a "passive" system able to trap atmospheric tritium as HTO using absorbent
material (a molecular sieve) exposed to the environment, with a special geometric format(see focus article on passive traps; pp. 14-15) to complete its panel of ambient tritium sampling
resources. After a specific sampling period, the sieve is processed to desorb the trapped waterprior to counting the tritium by liquid scintillation analysis.
This system has been tested at the Omonville station since 2017 to complement the bubbler.

●●●

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /●●●Figure E compares the ambient tritium (HTO) activities recorded using the two samplingtechniques. Activity measurements are in the same range, indicating that results are reliable. It isalso worth taking note that the passive trap samples, when used with suitable metrologicaldevices, systematically give values above the decision threshold for the period, unlike the bubbler.
FIGURE E / AMBIENT HTO TRITIUM ACTIVITY MEASURED AT THE IRSN SAMPLER (bubbler and passivetrap) AT OMONVILLE-LA-PETITE

Bq/m 3
0.25

0.2

0.15

0.1

0.05
144
0
Jan-17

Feb-17

Apr-17

Bubbler HTO H
3

May-17

Jul-17

Sep-17

Decision thresholds

Oct-17

Passive trap HTO 3H

Sampling station and shelter forthe 85Kr measuring system
H bubbler shelter

3

OPERA-AIR 80 m3/h sampler

Passive3
H trapRain gauge
Gaseousiodine sampler

Dec-17

Dose ratemeasuring sensor/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITE

The impact of the La Hague site on its immediate
environment and associated public exposure
The main radionuclides in the liquid and gaseousdischarges from the facilities on the La Haguesite are also those most frequently measured in
the environment, with the highest activity levels.
These radionuclides include krypton-85 in theair, carbon-14 and tritium in all components andiodine-129 in terrestrial and marine components.
Krypton-85

Krypton-85 is a noble gas and disperses in the
air without settling on the ground. Krypton-85
discharges have no effect on the terrestrial
components and food in particular.
This radionuclide is regularly measured at the fivevillage samplers located around the La Hague site:
Beaumont-Hague, Digulleville, Gréville-Hague,
Herqueville and Jobourg.

Herqueville (see figure 7). This noble gas will only
lead to external exposure for local inhabitants.
Estimated effective doses due to this activity range
from 1.6 μSv/year at Jobourg, through 2.7 μSv/
year at Beaumont-Hague and up to 5.4 μSv/year
at Herqueville. These doses match those assessedby Orano based on discharge data from 2016:
1.2 μSv/year per adult living in Goury and 8.1 μSv/
year per person living in the Digulleville canton.
Krypton-85 bursts lead to regular, but transient,increases in the equivalent dose rate for ambient
gamma, however the levels reached can be high.
The extra dose due to these bursts can be calculated
thanks to the Omonville-la-Petite samplingstation, where IRSN has installed a Téléray sensor
combined with a gamma spectrometer. This dose
reached approx. 3.3 μSv/year in 2017 (see focus
article on Detecting bursts of 85Kr; p. 146), which
corroborates estimates based on ambient 85Kr
activity measurements near to the site.

Ambient activities by volume fluctuate between afew dozen and several thousand Bq/m3, with meanvalues calculated over the last three years, from 2015
to 2017, representing approx. 200 Bq/m3 at Jobourgand Gréville-Hague and up to 680 Bq/m3 around

145

FIGURE 7 / QUARTERLY MEAN VALUES FOR AMBIENT KRYPTON-85 ACTIVITY BY VOLUME MEASURED AT THE FIVEVILLAGE SAMPLERS LOCATED NEAR TO THE LA HAGUE SITE (Bq/m3) SINCE SEPTEMBER 2009

Bq/m 3
2,000
1,800
1,600
1,400
1,200
1,000
800
600
400
200
0
Sep-09Sep-10

Sep-11

Beaumont-Hague

Sep-12DigullevilleSep-13

Sep-14

Gréville-Hague

Sep-15

Sep-16HerquevilleSep-17

Jobourg

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /IRSN equipment at the Omonville-La-Petite
sampler regularly detects increases in the equivalentdose rate expressed in nanoSievert per hour
(1 nSv/h = 0.001 μSv/h). The Téléray sensor(proportional counter) can issue one measurement
every 10 minutes, and detect increases of over
100 nSv/h (figure A) during these episodes.

© IRSN

FOCUS ARTICLE
USING THE TELERAY NETWORK TO DETECT
BURSTS OF KRYPTON-85

Téléray sensor (on the left, in the foreground), at the’Omonville-la-Petite sampling site

FIGURE A / DOSE RATE (nSv/h) MEASURED USING THE TÉLÉRAY NETWORK SENSOR AT OMONVILLE-LAPETITE

300

nSv/h

250

146

200
150
100
50
0
2012

2013

2014

2015
2016
Local background radiation

2017

These increases are sometimes caused by natural phenomena with the particulate daughter
products of radon, however they are generally caused by krypton-85 discharged from Orano's
plant at La Hague.
A gamma spectrometry sensor has been installed with the Téléray sensor since October 2016. The
krypton peak from industrial discharges can be clearly identified at 514 keV (figure B).
FIGURE B / SPECTRUM FOR THE GAMMA SPECTROMETRY SENSOR DURING A KRYPTON-85 BURST– Omonville–la-Petite sampling station (the number of hits depends on energy levels)

Spectra can be processed in order to differentiate between artificial increases and natural increases
by calculating an indicator for the presence of artificial radionuclides, and isolating the radionuclides
causing these increases, e.g. by extracting the number of hits attributed to krypton-85.
●●●/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITE●●●

At the Omonville-la-Petite sampling station, the presence of artificial radionuclides correlates
strongly with the identification of krypton-85 (figure C).

Artiﬁcial radionuclide indicator

FIGURE C / CORRELATION BETWEEN THE INDICATOR FOR THE PRESENCE OF ARTIFICIALRADIONUCLIDES AND THE NUMBER OF HITS ATTRIBUTED TO KRYPTON-85
140
120
100
80
60
40
20
0

0

5

10
15
20
25
30
Number of hits for krypton-85

35

40

FIGURE D / IDENTIFICATION OF VALUES FOR A KRYPTON-85 BURST– Omonville–la-Petite sampling station

147
140
120
100
80
60
40
20
0
11/2016

12/2016
02/2017
03/2017
Number of hits for krypton-85

05/2017
07/201708/2017
Artificial radionuclide indicator

10/2017

The dose added due to krypton-85 discharges can be determined after identifying significant
results from the discharge of artificial radionuclides (figure D), and removing their reference
background radiation value. The total value can be used to calculated an additional dose of
3.3 µSv for the year 2017. The graphic shown in figure E gives monthly variations in thisadditional dose, with a maximum value of 1.8 µSv recorded in the month of December 2016 alone
at the Omonville-la-Petite sampling station.

Adjusted dose µSv

FIGURE E / MONTHLY ADDITIONAL DOSE DUE TO KRYPTON-85 FROM NOVEMBER 2016 TO SEPTEMBER
2017 – Omonville-la-Petite sampling station (µSv/mois)
2.0
1.8
1.6
1.4
1.2
1.0
0.8
0.6
0.4
0.2
0.0

6
7
7
7
7
7
7
7
17
17
17
17
16
17
Nov- Dec-1 Jan- Feb- Mar-1 Apr-1 May- Jun- Jul-1 Aug-1 Sep-1 Oct-1 Nov- Dec-1

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Tritium

Most of the tritium discharged from Orano's plantin La Hague is trapped as tritiated water and thenreleased to sea. A very small fraction of the tritium
is discharged as gas. These gaseous discharges
only have a moderate effect on the atmosphere.

148

Due to the decision thresholds used by Orano forroutine monitoring (approx. 0.4 Bq/m3, i.e. 40 times
ambient background tritium radiation from either
natural sources or nuclear testing), measurementsby Orano can only rarely be used to quantify total
tritium activity (HTO+HT) in the air as per samples
from the 5 samplers located in the villages near tothe site. The highest number of significant values(1)(only 3% of values exceeded the DT of 0.4 Bq/m3) was recorded at the Herqueville sampler tothe south east of the plant between 2015 and 2017.
On the other hand, it is regularly measured in the
rainwater collected at the 3 samplers installedat Omonville-la-Petite for Orano, Digullevillefor ANDRA and Gréville-Hague for IRSN
(see figure 8). Activity levels per volume canoccasionally exceed 30 Bq/L for the two samplers
most exposed to the prevailing winds (Digullevilleand Omonville-la-Petite).
IRSN has run a bubbler to monitor atmospherictritium at Omonville-la-Petite since 2015, tocomplement monitoring by Orano. Thanks tothis system and the more advanced measuringsystems used for expertise (see focus article

on the "Omonville-la-Petite samplers"; p. 141),
ambient tritium activity can be measured,particularly in the form of water vapour (HTO) andtritiated hydrogen (HT) (see figure 9). Since 2017,
IRSN has also installed its rainwater collector at
this sampling station to complement the existingmeasuring systems (bubblers, aerosol samplers,
Téléray sensors and spectrometers). Mean
ambient tritium values (HTO and HT) measured
at this location between 2015 and 2017 reach 0.07
Bq/m3 and 0.14 Bq/m3 respectively. Mean tritium
activity in rainwater samples at Omonville-laPetite in 2017 represented 7.1 Bq/L. This figure
corroborates the ambient measurement recordedfor HTO.
At Omonville-la-Petite, ambient tritium levels
will lead to an extremely low internal dose due toexposure by inhaling (estimated effective dose:less than 0.01 µSv/year), however tritium in HTO
form will also lead to transcutaneous external
exposure. The estimated effective dose is equal tothe calculated inhaled dose. The total atmospherictritium dose is therefore less than 0.02 µSv/year.
This dose is approximately equal to the figures
calculated by Orano based on discharge data from2016: 0.04 μSv/year per adult living in Goury and0.1 μSv/year per person living in the Digullevillecanton. The differences are mainly due to thelocations of the samples assessed depending on
distance from the discharge point and prevailingwind direction.

1. In this document, a "significant value" is defined as a measurement which is above the decision threshold (DT). The definition applies throughout
this document.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITE

FIGURE 8 /TRITIUM (HTO) ACTIVITY BY VOLUME MEASURED IN RAINWATER IN THE IMMEDIATE VICINITY OF THE
LA HAGUE SITE (Bq/L)

Bq/L
100

Omonville-la-Petite (Orano)
Decision thresholds

90

Significant values

80
70
60
50
40
30
20
10
0
Jan-09Jan-10

Bq/L
100

Jan-11

Jan-12

Jan-13Jan-14Jan-15Jan-16

Jan-17Jan-18Digulleville (ANDRA)
Decision thresholds

90

149

Significant values

80
70
60
50
40
30
20
10
0
Jan-09Jan-10

Bq/L
30

Jan-11

Jan-12

Jan-13Jan-14Jan-15Jan-16

Jan-17Jan-18Jan-17Jan-18

Gréville-Hague (IRSN)
Decision thresholds

Significant values

25
20
15
10
5
0
Jan-09Jan-10Jan-11

Jan-12

Jan-13Jan-14Jan-15Jan-16RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 9 / AMBIENT TRITIUM (HT and HTO) ACTIVITY BY VOLUME MEASURED AT THE IRSN SAMPLER AT OMONVILLE-LAPETITE SINCE 2015 (Bq/m3)

Bq/m 3
1.4
1.2
1
0.8
0.6
0.4
0.2
0

Ja
150

6
7
5
7
7
6
6
6
5
7
5
5
5
n-1 pr-1 un-1 ep-1 ec-1 ar-1 un-1 ep-1 ec-1 ar-1 Jun 1 ep-1 ec-1
A
J
J
S
S
D
S
D
D
M
M
H - HTO

3

Decision thresholds (3H - HTO)

The low bound tritium activity levels by massmeasured in the grass samples are attributable
to these atmospheric activities. Mean values forthe 2015 - 2017 period range from 1.1 to 3.5 Bq/
kg fresh (see figure 10), depending on the sampler,which is slightly above local backgrond radiation.
The highest activity levels were recorded near tothe site in the municipality of Digulleville, under
the prevailing winds north east of the site.
The geographic distribution of the activities
measured is as expected based on the prevailingwinds at the site (see figure 21).
Activity levels by mass measurements for boundtritium (OBT) in leaf vegetables (leaks, cauliflowers,
parsley, etc.) represent between 0.5 and 2.2 Bq/
kg fresh, which is above background radiationlevels (mean value: 1.1 Bq/kg fresh). Free tritium(HTO) measurements were only obtained for two
cauliflower samples. Significant values reaching
between 2 and 8 times background radiation wereH - HT

3

Decision thresholds (3H - HT)recorded for both samples. Results were similar
in root vegetables (carrots and potatoes), with amean value of 1.2 Bq/kg fresh for bound tritium
and 5.4 Bq/kg fresh for free tritium.
Free tritium (HTO) activity by volume in milk
is generally below the decision threshold (<4.5 Bq/L). Between 2015 and 2017, the highest
number of significant values (21% of values) wasrecorded for milk from Digulleville, with peak
activity of 10 Bq/L. Bound tritium activity levels
by mass quantified in meat can be differentiatedfrom background radiation thanks to mean values
over the study period of 5.3 Bq/kg fresh for poultry,
2.1 Bq/kg fresh for sheep and 3.6 Bq/kg fresh forwild rabbits.
Mean activity by mass for honey and eggs are atsimilar levels (4.9 and 1.7 Bq/kg fresh respectively).
These values are similar to those recorded in
2011-2014.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITE

FIGURE 10 / MEAN TRITIUM ACTIVITY BY MASS FOR THE 2015-2017 PERIOD IN GRASS SAMPLES COLLECTED AT THE 10
SAMPLERS NEAR TO LA HAGUE (Bq/kg fresh) AND TIMELINE FOR RECURRENT ACTIVITY LEVELS MEASURED AT TWO OF
THESE SAMPLERS SINCE JANUARY 2009 (Bq/kg fresh)151

H (OBT) - Bq/kg fresh
20

H (OBT) - Bq/kg fresh
20

18

18

16

16

14

14

12

12

10

10

8

8

6

6

4

4

2
0
Jan-09Digulleville - Pont Durand (A5)3Calais farm (A12)3

2Jan-10Jan-11

Jan-12

Jan-13Jan-14Jan-15Jan-16

Jan-17Jan-18The terrain and narrow configuration of the
Cotentin peninsula are home to small coastal
rivers, which all run to the Channel. Tritium
activity levels by volume were measured in water
samples taken in all streams in the immediate
environment around the site (see figure 11). Only 3of these samples regularly include tritium activity
levels in excess of 10 Bq/L: Moulinets stream(recboc spring), Sainte-Hélène and Grand Bel withmean activities by volume of 18 Bq/L, 21 Bq/L and
319 Bq/L respectively, calculated by IRSN over the
2015-2017 period.

0
Jan-09Jan-10Jan-11

Jan-12

Jan-13Jan-14Jan-15Jan-16

Jan-17Jan-18The Sainte-Hélène steam and its tributary,
the Grand Bel, carry rainwater and drainage
water from the area to the east of the Orano La
Hague site and the ANDRA site, after storage ina storm retention basin (see figure 4). Tritiumcontamination is still present further to historicalpollution from the 1970's.
The Moulinets stream collects rainwater fromthe area west of the Orano site and wastewater.
Finally, the Combes stream collects rainwaterfrom the area north of the site.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 11 / FREE TRITIUM (HTO) ACTIVITY BY VOLUME IN RIVER WATER SAMPLES COLLECTED AT 6 IRSN MONITORING
POINTS NEAR TO LA HAGUE (Bq/L) SINCE JANUARY 2009 AND LOCATION OF THE DIFFERENT SPRINGS

Bq/L
10,000

1000

100

10

1
Jan-09 Jan-10

Jan-11

Combes stream
Moulinet stream, Recboc springJan-12 Jan-13 Jan-14 Jan-15 Jan-16 Jan-17 Jan-18
Landes stream
Le Grand Bel stream

Moulinets stream, Le Batardeau
Sainte Hélène stream

152

Thanks to the improvements in metrological
performance for the systems used by the operator
over the 2015-2018 period, tritium (HTO) activity byvolume in drinking water has been characterised
in more detail. Significant tritium activity can still
be detected at the 12 samplers monitored by Oranoaround the La Hague site. Activity levels by volume
for the closest Hameau Fabien borehole to the site,
located in the municipality of Beaumont-Hague,
are between 7 and 17 Bq/L, with a mean activity
by volume of 9.8 Bq/L. Ignoring this borehole, theactivity levels measured are mainly below 10 Bq/L,
if they are significant at all. Drinking 2 L of water
daily from the Hameau Fabien borehole would leadto an effective dose of 0.13 µSv/year.

The ground water under the La Hague site, andspecifically under the CSM, has high tritiumcontamination levels, and can peak at an activity
by volume of 100,000 Bq/L based on data recorded
since 2014 using the most affected piezometer.
The ground water downstream from the CSM
is affected by historical tritium contamination
due to an incident on a storage unit in 1976. The
radionuclides are currently in the decay phase(see figure 12). This ground water is not used forany purpose.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
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LA HAGUE SITE

FIGURE 12 / TOTAL TRITIUM ACTIVITY BY VOLUME IN GROUND WATER SAMPLES COLLECTED NORTH EAST OF AND ABOVE
THE CSM SITE USING PIEZOMETER P0131 (Bq/L) SINCE JANUARY 2009

Bq/L
250,000

200,000

150,000

100,000

50,0000
Jan-09

May-10

Sep-11

Feb-13Jun-14

Nov-15Mar-17Ground water - Piezometer PO131 (ANDRA)

Contamination by tritiated liquid effluentsdischarged by the La Hague site, as well as the
British Sellafield plant, to a lesser extent, is clearlymeasurable throughout the Channel.
Mean tritium activity by volume in seawaterover the 2015 - 2017 period (see figure 13) isapproximately 12 Bq/L near to La Hague (compare
this value with natural background radiation of
approx. 0.1 - 0.2 Bq/L). This figure progressively
decreases with distance. Note: these mean values
mask significant variations within periods of justa few hours (see the focus article in the IRSN
radiological report from 2012).
Tritium activity in marine organisms, plants
and animals is in equilibrium with that of water,
therefore activities by mass are similar. Mean
activity by mass in fish captured on the west coast of
the Cotentin peninsula represents 3.7 Bq/kg freshfor bound tritium (OBT) and 6.8 Bq/kg fresh forfree tritium (HTO). In terms of molluscs, the twoSaint-Jacques samples taken on the north coastof the Cotentin peninsula exceed backgroundradiation; mean activity by mass is equal to

3 Bq/kg fresh for bound tritium and 6.7 Bq/kg freshfor free tritium. The two limpet samples taken nearto Herquemoulin record similar levels, althoughmean activity by volume for free tritium is slightly
higher (10.3 Bq/kg fresh). These activity levels
are similar to and corroborate sea water data, as
tritium is at equilibrium between seawater andfish.
The potential dose absorbed due to tritium
discharged by the site by eating local food(vegetables, fish, meat, etc.) is extremely low. Thisdose is estimated at less than 0.01 µSv/year for an
adult eating items grown near to the La Hague site,on the basis of the mean activity levels measured
in food during the study period (2015-2017). A
diet (see table 5) corresponding to that of people
living in the north of the Cotentin peninsula, witha fisherman at the head of the household, wasassumed. This diet is representative of an ordinary
diet with fairly high fish contributions. Diet dataand self-sufficiency data were taken from the
CREDOC survey(2). This dose is insignificant
compared with those absorbed for krypton-85
discharged in effluents and described above.

2. Consumption Planning Department (Département Prospective de la consommation) (1998) Enquiry on food consumption in the north of the
Cotentin peninsula on behalf of COGEMA CREDOC.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /153

FIGURE 13 / MEAN FREE TRITIUM ACTIVITY MEASURED IN SEA WATER AROUND THE COTENTIN PENINSULA OVER THE
2015-2018 PERIOD (Bq/L)© J.-M. Taillat/Areva

154

La Hague site as viewed from Anse des Moulinets/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITE

Carbon-14

than 0.03 Bq/m3 (< DT) and 2.2 Bq/m3. Mean values
calculated over the last three years (2015 - 2017)
remain between the background level for thisradionuclide (approx. 0.05 Bq/m3) at Digullevilleand Beaumont-Hague, and 0.08 Bq/m3 at Jobourg.

The effects of liquid and gaseous effluentscontaining carbon-14 (CO2) can be detected inmost environmental components.
Ambient carbon-14 is regularly measured at thefive village samplers located around the site (seefigure 14). Ambient activity by volume measured
on a bimonthly basis (for activity measured in theterrestrial food chain), fluctuates between less

The dose absorbed by inhaling carbon-14 (as CO2)
by inhabitants of the municipality of Jobourg,
where mean activity by volume is the highest, isvery low (this dose peaks at 0.002 µSv/year).

FIGURE 14 / AMBIENT CARBON-14 ACTIVITY BY VOLUME MEASURED AT THE FIVE VILLAGE SAMPLERS LOCATED NEAR TO
THE LA HAGUE SITE (Bq/m3) SINCE JANUAR 2009

AS1 - Gréville-Hague
C (Bq/m 3)

14

Decision thresholds

AS2 - DigullevilleSignificant values

C (Bq/m 3)

14

1

1

0.1

0.1

0.01
Jan-09Jan-10Jan-11

Jan-12

Jan-13Jan-14Jan-15Jan-16

Jan-17Jan-180.01
Jan-09Decision thresholds

155

Jan-10Jan-11

Jan-12AS3 - Beaumont-Hague
C (Bq/m 3)

14

Decision thresholds

C (Bq/m 3)

14

1

0.1

0.1

Jan-10Jan-11

Jan-12

Jan-13Jan-14Jan-15Jan-16

Jan-13Jan-14Jan-15Jan-16

Jan-17Jan-18

AS4 - HerquevilleSignificant values

1

0.01
Jan-09Significant values

Jan-17Jan-180.01
Jan-09Jan-10Decision thresholds

Jan-11

Jan-12

Jan-13Significant values

Jan-14Jan-15Jan-16

Jan-17Jan-18AS5 - Jobourg
C (Bq/m 3)

14

Decision thresholds

Significant values

1

0.1

0.01
Jan-09Jan-10Jan-11

Jan-12

Jan-13Jan-14Jan-15Jan-16

Jan-17Jan-18RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /The impact of carbon-14 discharges is easier
to detect in food, particularly in sea food(fish, molluscs and shellfish) due to activity
by mass measurements fluctuating between
background radiation levels (approx. 20 Bq/kg
fresh) and 3 to 4 times this value (see figures
15 to 17). Mean activity levels by mass calculated
between 2015 and 2017 are between 33 Bq/kg
fresh for fish and 53 Bq/kg fresh for shellfish.
Due to variation in activity by mass, it is impossible
to differentiate between sea food from the different
sampling areas near to the site (west, north andeast of the Cotentin peninsula). However, specificmeasurements taken on limpet samples collectedon the Cotentin coast demonstrate that the
impact of effluents discharged from La Hague issubstantially higher near to the plant discharge
points (near the discharge channel at Goury andAnse des Moulinets) than to the east, towards
Cherbourg, or further south towards BarnevilleCarteret. This impact is also detectable, to asmaller degree, along the entire French coast of
the Channel up to Dunkirk (see. figure 18).

FIGURE 15 / CARBON-14 ACTIVITY BY MASS IN FISH CAPTURED NEAR TO THE LA HAGUE SITE SINCE JANUARY 2009 (Bq/kg fresh)

Bq/kg fresh
120
100
80
60
40
20
0
Jan-09 Jan-10 Jan-11 Jan-12 Jan-13 Jan-14 Jan-15 Jan-16 Jan-17 Jan-18
East Cotentin
North CotentinWest Cotentin
Range for natural background radiation and nuclear weapons tests© IRSN156

Fish sampling (plaice)/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITE

FIGURE 16 / CARBON-14 ACTIVITY BY MASS IN SHELLFISH CAPTURED NEAR TO THE LA HAGUE SITE SINCE JANUARY
2009 (Bq/kg fresh)

Bq/kg fresh
120
100
80
60
40
20
0
Jan-09 Jan-10 Jan-11 Jan-12 Jan-13 Jan-14 Jan-15 Jan-16 Jan-17 Jan-18
Lobsters, west Cotentin

Crabs, north Cotentin

Crabs, west Cotentin

Range for natural background radiation and nuclear weapons tests
157

FIGURE 17 / CARBON-14 ACTIVITY BY MASS IN MOLLUSCS CAPTURED NEAR TO THE LA HAGUE SITE SINCE JANUARY 2009
(Bq/kg fresh)

Bq/kg fresh
120
100
80
60
40
20
0
Jan-09 Jan-10 Jan-11 Jan-12 Jan-13 Jan-14 Jan-15 Jan-16 Jan-17 Jan-18
St-Jacques, north Cotentin

Oysters, east Cotentin

Oysters, west Cotentin

Range for natural background radiation and nuclear weapons tests

Note: Orano has only taken oyster samples since 2014 due to a lack of mussels.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 18 / MEAN CARBON-14 ACTIVITY LEVELS IN LIMPETS CAPTURED NEAR TO THE LA HAGUE SITE BETWEEN 2015
AND 2017 (Bq/kg fresh)

158

Carbon-14 activity in the terrestrial component
around La Hague can also be differentiated fromthe "background radiation" for this radionuclide(see chapter 2), but to a lesser extent. Activity byvolume measured in milk (see figure 19), rarely
exceeds 40 Bq/L. Mean values calculated between
2015 et 2017 range from 19 Bq/L at Jobourg(Hameau Ricard) to 28 Bq/L at Herqueville(Hameau de l’église), where most activity isnatural (approx. 15 Bq/L).

The geographic distribution of activity measured ingrass samples (see figure 20) is fairly consistent
with the expected configuration based on theprevailing winds (see figure 21) and with distance
between the sampling site and the facility.
The areas affected by atmospheric discharges
from La Hague can be determined on this basis.
The prevailing winds are west and south west.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
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LA HAGUE SITE

FIGURE 19 / CARBON-14 ACTIVITY BY VOLUME IN MILK SAMPLED NEAR TO THE LA HAGUE SITE SINCE JANUARY 2009
(Bq/L)
Bq/L 70
60
50
40
30
20
10
0
Jan-09Jan-10Jan-11

Beaumont - Hague(Rue de Beaumont)Jan-12

Beaumont - Hague(Es Galle village)

Jan-13Jan-14Herqueville(Eglise village)

Jan-15
Jobourg(Ricard village)

Jan-16

Jan-17Jan-18Digulleville(Rantot farm)

Range for natural background radiation and nuclear weapons tests

FIGURE 20 / CARBON-14 ACTIVITY BY MASS IN GRASS SAMPLES TAKEN NEAR TO THE LA HAGUE (Bq/kg dry)(3)Mean values for the 2015-2017 period for ten samplers. The highest activity levels were recorded near to the site, under the prevailingwinds east/north east of the site.

3. Since 2014, ASN has preferred for results relating to non-edible matrices to be given in Bq/kg dry to improve the harmonisation of data uploaded
to the RNM database.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /159

FIGURE 21 / WIND DIRECTIONS (La Hague)

340
320
300

280

360

11 %
10 %
9%
8%
7%
6%
5%
4%
3%
2%
1%
0%

20
40
60

80

260

100

240

120
220

140
200

180

160

% of time

160

Mean values measured in leaf vegetables and root
vegetables between 2015 and 2017 (see figure 22)
represent 17 and 27 Bq/kg fresh respectively,
which is 2 to 3 times the value of backgroundradiation (7 Bq/kg fresh for leaf vegetables and
10 Bq/kg fresh for root vegetables). Carbon-14
measurements during this period, in meat(poultry and sheep) and eggs (see figure 23)
remain within the usual range in France and canmostly be attributed to natural sources (approx.
35 Bq/kg fresh for eggs, 55 Bq/kg fresh for poultry
and 65 Bq/kg fresh for sheep). Only wild rabbits
exceeded background radiation for this type offood on one occasion (approx. 50 Bq/kg fresh).
Mean activity by mass calculated for this productrepresented 46 Bq/kg fresh between 2015 and2017. Activity by mass measurements for fruit(blackberries) are similar to background radiation(14 Bq/kg fresh), and the mean value calculated
over the study period reached 15 Bq/kg fresh.

The mean activity by mass of the two honeysamples taken in 2015 and 2016 reached
73 Bq/kg fresh. This is also true for thyme,
for which a mean activity by mass for thetwo samples represents 133 Bq/kg fresh.
Both of these foods concentrate radioactivity.
The dose potentially absorbed by eating local
food (milk, vegetables, fish, meat, honey, etc.)
contaminated by carbon-14 due to effluentsdischarged from the La Hague site is estimatedat 0.4 µSv/year for an adult eating items grownnear to the La Hague site, on the basis of themean activity levels measured in food during
the study period (2015-2017). A diet (see table 5)
corresponding to that of people living in the northof the Cotentin peninsula, with a fisherman at thehead of the household, was assumed. Diet dataand self-sufficiency rates were taken from the
CREDOC survey carried out in the region in 1998.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITE

FIGURE 22 / CARBON-14 ACTIVITY BY MASS MEASURED FOR A FEW LEAF VEGETABLES SAMPLED NEAR TO THE LA
HAGUE SITE SINCE JANUARY 2009 (Bq/kg fresh)

Bq/kg fresh
80
70
60
50
40
30
20
10
0
Jan-09 Jan-10 Jan-11 Jan-12 Jan-13 Jan-14 Jan-15 Jan-16 Jan-17 Jan-18
Leaf vegetables (cauliflower, leaks, parsley)
Root vegetables (carrots, potatoes)

Mushrooms
Blackberries

Range for natural background radiation andnuclear weapons tests

FIGURE 23 / CARBON-14 ACTIVITY BY MASS MEASURED IN ANIMAL-BASED FOOD SAMPLES TAKEN NEAR TO THE LA
HAGUE SITE SINCE JANUARY 2009 (Bq/kg fresh)

Bq/kg fresh
80
70
60
50
40
30
20
10
0
Jan-09 Jan-10 Jan-11 Jan-12 Jan-13 Jan-14 Jan-15 Jan-16 Jan-17 Jan-18
RabbitMuttonCocks, hens, chickens

Eggs

Range for natural background radiation and nuclear weapons tests

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /161

than 0.5 µBq/m3 (DT) and 27 µBq/m3 for iodine-129
measured in particulate form and between
13 µBq/m3 (DT) and 390 µBq/m3 for iodine-129
measured in gaseous form. On this basis,
iodine-129 is mainly discharged as a gas and themean value calculated between 2015 and 2017 at
Omonville-la-Petite represents 48 µBq/m3.

Iodine-129

Iodine-129 is mainly discharged at sea after mixing
with tritiated water.
Very little iodine-129 is discharged in gaseous form
(6.1 MBq in 2016) as this radionuclide is absorbed
by iodine filters installed on discharge stacks prior
to discharge. For this reason and due to the decisionthresholds used by Orano for routine monitoring(approx. 0.008 Bq/m3), ambient iodine-129 is nevermeasured at the five village samplers located in themunicipalities around the site.

Due to the very low ambient levels of iodine-129
at Omonville-la-Petite, the dose absorbed by local
residents by inhaling is extremely low (estimatedeffective dose: 0.04 µSv/year). This dose is lessthan that calculated by Orano based on discharge
data from 2016: 0.9 μSv/year per adult living in the
Digulleville canton.

IRSN has run a new higher-flow aerosol sampler
compared with the previous sampler fitted at
Beaumont-Hague (80 m3/h) at Omonville-la-Petite
since 2015, to complement monitoring by Orano.
Thanks to this system and the more advanced
measuring systems used for expertise, ambient
iodine-129 activity can be measured. Ambient
activity levels by volume fluctuate between less

162

Mean activity levels by mass measured in grasssamples(4) between 2015 and 2017 range between
less than 0.4 and 4.4 Bq/kg dry (see figure 24).
The geographic distribution of iodine-129 activity
in grass samples is similar to that of carbon-14
or tritium.

FIGURE 24 / MEAN IODINE-129 ACTIVITY BY MASS IN GRASS SAMPLES TAKEN NEAR TO THE LA HAGUE SITE (Bq/kg dry)
BETWEEN 2015 AND 2017
Mean values for the 2015-2017 period for ten samplers.

<0.4
2.8
<0.8

2.8
4.1

1.2
2.1

0.8
1.3

Orano site
La Hague
Sampling points<0.5

Activity by mass of Iodine-129 in grass(source: RGE-BDTOPO@ & BDCARTO@ by IGN - 2015 ed.)Iodine-129 value (Bq/kg dry)Grass (10 sampling points)

4. Since 2014, ASN has preferred for results relating to non-edible matrices to be given in Bq/kg dry to improve the harmonisation of data uploaded
to the RNM database.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITE

Iodine-129 is detected in less than 10% of milk
samples taken at farms in the municipalities ofBeaumont-Hague, Herqueville and Jobourg (fora decision threshold of approx. 0.02 Bq/L (seefigure 25). The peak value measured in thesemunicipalities reached 0.06 Bq/L. 34% of milk
samples taken at the farm to the north east of theDigulleville site, where grass samples record thehighest iodine-129 activity levels by mass, gavesignificant measurements(5) between 0.02 and0.07 Bq/L. Activity levels generally corroborate
those measured in grass samples, which would
appear to indicate that some of the animal feed isgrown locally.
Iodine-129 was not detected in any of the analyses
conducted on cabbages, carrots, potatoes orleaks (DT < 0.1 Bq/kg fresh). On the other hand,
iodine-129 was systematically detected in parsley,
thyme and mushroom samples (with mean resultsof 0.4, 1.8 and 0.06 Bq/kg fresh respectively).

Activity could not be quantified in some meats(cock, rabbit and sheep), which could imply amore distant source of majority feed. However, asignificant iodine-129 measurement was recorded
for the two egg samples analysed between
2015 and 2017: 0.1 Bq/kg fresh); iodine is easilytransferred to eggs
Iodine-129 has also been detected in aquatic plant
samples taken from rivers to the north of the site:
Landes, Combes and Sainte-Hélène (figure 26).
However, no iodine-129 has been detectedin water samples. Iodine-129 is occasionallydetected in sediments (e.g. in samples taken nearto the Moulinets dam), however the concentrations
measured are near to the decision threshold insuch circumstances (and less than 2 Bq/kg dry).

163
FIGURE 25 / IODINE-129 ACTIVITY BY VOLUME MEASURED IN MILK SAMPLED NEAR TO THE LA HAGUE SITE SINCEJANUARY 2009 (Bq/L)

Bq/L
0.12
0.10
0.08
0.06
0.04
0.02
0
Jan-09 Jan-10 Jan-11 Jan-12 Jan-13 Jan-14 Jan-15 Jan-16 Jan-17 Jan-18
Decision thresholds(all sites)

Beaumont - Hague(rue de Beaumont)

Beaumont - Hague(Es Galle village)

Herqueville(Eglise village)

Jobourg(Ricard village)

Digulleville(Rantot farm)

5. In this document, a "significant value" is defined as a measurement which is above the decision threshold (DT).

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 26 / IODINE-129 ACTIVITY BY MASS MEASURED IN AQUATIC PLANT SAMPLES TAKEN IN RIVERS NEAR TO
THE LA HAGUE SITE (Bq/kg fresh)

Bq/kg fresh
3.5
3.0
2.5
2.0
1.5
1.0
0.5
0

09
20

an

J
164

10
20

an

J

11
20

J

an

12
20

J

an

2
01
-2

c
De

3
01
-2

c
De

Omonville-la-Petite, La Sainte-Hélène
Omonville-la-Petite, Les Landes

The highest iodine-129 activity levels in a marine
environment are found in algae, which concentrate
the radioelement. On this basis, algae can be used
as a bio-indicator for the impact of iodine-129
effluents discharged from the La Hague plant,
outside of the immediate environment of thesite. Figure 27 shows changes in the geographic
distribution of mean activity levels by massmeasured between 2015 and 2017 in algae
sampled along the Cotentin coast. These figurescorroborate limpet data.

4
01
-2

c
De

5
01
-2

c
De

6
01
-2

c
De

7
01
-2

c
De

Omonville-la-Petite, Les Combes
Decision thresholds (for 3 samplers)

Seawater is only slightly contaminated by thisradionuclide: over the 2015-2018 period, it was
only detected four times (near to Goury port
(Auderville) and Anse des Moulinets (Herqueville))
at concentrations of less than 10 mBq/L.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITE

FIGURE 27 / IODINE-129 ACTIVITY BY MASS MEASURED IN LIMPET (Bq/kg fresh) AND ALGAE (Bq/kg dry) SAMPLES TAKEN
NEAR TO LA HAGUE - MEAN VALUES FOR THE 2015-2017 PERIOD FOR 12 SAMPLERS AND RECURRENT LIMPET VALUESSINCE 2009

Bq/kg fresh
3
2.5
2
1.5
1
0.5
0
Jan-09 Jan-10 Jan-11 Jan-12 Jan-13 Jan-14 Jan-15 Jan-16 Jan-17 Jan-18
Anse des Moulinets

Anse Saint-Martin Goury Herquemoulin
Decision thresholds (all sites)

Elcagrain

Bq/kg fresh
3

165

2.5
2
1.5
1
0.5
0
Jan-09 Jan-10 Jan-11 Jan-12 Jan-13 Jan-14 Jan-15 Jan-16 Jan-17 Jan-18
Anse du Brick
Barfleur
Querqueville
Decision thresholds (all sites)

UrvilleBq/kg fresh
3
2.5
2
1.5
1
0.5
0
Jan-09 Jan-10 Jan-11 Jan-12 Jan-13 Jan-14 Jan-15 Jan-16 Jan-17 Jan-18
Siouville Barneville Granville
Decision thresholds (all sites)
RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 28 / MEAN IODINE-129 ACTIVITY FOR LIMPETS AND ALGAE

0.5

Orano site
La Hague

0.4

0.2

0.2

0.2

0.3

0.2

1.0

0.5

Sampling points

0.2

166

(source: RGE-BDTOPO@ & BDCARTO@ by IGN - 2015 ed.)

0.5

Mean iodine-129 activity by mass for limpets and algae
Iodine-129 value, limpets (Bq/kg fresh)
Iodine-129 value, algae (Bq/kg dry)
Limpets (12 sampling points)
Algae (12 sampling points)

Iodine-129 contamination is higher in sea foodthan in terrestrial food produce. Contamination ismore evenly spread in shellfish and molluscs thanin fish (see figures 29 and 30). In fact, between
2015 and 2017, between 63% and 89% of themeasurements recorded for fish were below thedecision threshold Activities by mass measured
range from 0.05 Bq/kg fresh on the east coast to
0.46 Bq/kg fresh on the west coast of the Channel.
The highest iodine-129 activity levels by mass
are recorded for lobsters captured on the west
coast for shellfish (between 0.2 and 2.1 Bq/kg
fresh). Crabs are also regularly contaminated,with activity levels by mass between 0.06 and 0.34
Bq/kg fresh. The highest levels were recorded inlimpets captured near to the discharge channel formolluscs. Contamination levels drop progressively
with distance. Mean activity levels by massmeasured in limpet samples captured near to thedischarge channel range between 0.4 and 1 Bq/
kg fresh (see figure 27). Mean iodine-129 activity
levels by mass calculated between 2015 and 2017
represent 0.4 Bq/kg fresh for shellfish and 0.5 Bq/
kg fresh for molluscs.
The potential dose absorbed by eating local foodcontaminated by iodine-129 discharged by the
La Hague plant is estimated at 0.2 μSv/year. Thisdose was assessed for an adult. Only the sea foodcomponents of the diet were considered (seetable 5, for residents of north Cotentin peninsula,with a fisherman at the head of the household),given that most of the activity levels measured
in almost all terrestrial food are insignificant
therefore a mean value cannot be calculated.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITE

FIGURE 29 / IODINE-129 ACTIVITY BY MASS MEASURED IN FISH CAPTURED NEAR TO THE LA HAGUE SITE (Bq/kg fresh)

Bq/kg fresh
0.8
0.7
0.6
0.5
0.4
0.3
0.2
0.1
0
Jan-09 Jan-10 Jan-11 Jan-12 Jan-13 Jan-14 Jan-15 Jan-16 Jan-17 Jan-18
Est Cotentin
North CotentinWest Cotentin
Decision thresholds (all sources)
167

FIGURE 30 / IODINE-129 ACTIVITY BY MASS MEASURED IN SHELLFISH AND MOLLUSC SAMPLES (excluding limpets)
TAKEN NEAR TO THE LA HAGUE SITE (Bq/kg fresh)

Bq/kg fresh
2.5
2.0
1.5
1.0
0.5
0
Jan-09 Jan-10 Jan-11 Jan-12 Jan-13 Jan-14 Jan-15 Jan-16 Jan-17 Jan-18
Lobsters, West Cotentin
Crabs, North Cotentin
Crabs, West Cotentin
St-Jacques, North Cotentin
Decision thresholds (all species)

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Plutonium 238, 239+240 and americium-241
Depending on the activity levels discharged, theimpact of the actinides discharged by the La Haguesite into the terrestrial environment cannot be
differentiated from residual atmospheric fallout asplutonium and americium are mainly discharged inliquid effluents via the coastal discharge channel.
In addition, discharges only affect the continental
aquatic environment to a limited extent. Despite
this, sediment samples taken from Sainte-Hélène
steam and the Moulinets basin are contaminated
due to old pollution from La Hague operations andthe ANDRA storage facility. Liquid effluents fromthese two sites are not generally discharged via
the Sainte-Hélène stream and Moulinets basin.

168

ANDRA collected two water samples fromthe Sainte-Hélène spring in June 2017, atmonitoring points R6 and R6-10 (Hameau laFosse). Analyses on these samples detected
plutonium contamination. The activity by volume
for the sample taken at point R6 represented
0.008 Bq/L for 239+240Pu and 0.0047 Bq/L for 238Pu
and 0.0011 Bq/L for 239+240Pu for the sample taken
at point R6-10. Both of these samples were
contaminated by 241Am (0.00036 Bq/L for point R6
and 0.00042 Bq/L for point R6-10), but also by ararer radionuclide: silver-108m. This radionuclide
was probably released by the ANDRA site.
On the other hand, the impact of liquid discharges
in the marine environment is far clearer. 239+240Pu
and 238Pu isotopes are regularly measured inmolluscs, the most sensitive matrix (see figures 31
and 32). Significant activity levels by mass wererecorded for all of the measurements taken on
Saint-Jacques molluscs captured off the northcoast of the Cotentin peninsula between 2015 and2017, for 238Pu and 239+240Pu. These measurements
fell in the 0.007 - 0.03 Bq/kg fresh and 0.02 0.06 Bq/kg fresh brackets respectively.

For oysters collected on the east and west coastsof the Cotentin peninsula, 40% of values are below
the decision threshold for the 239+240Pu (< 0.005 Bq/
kg fresh) measurement. The maximum activity bymass measured reached 0.01 Bq/kg fresh. Only
20% of 238Pu measurement results are significant
for oysters, with a peak measurement of 0.01 Bq/kg
fresh. Finally, between 60 and 80% of 238Pu values
are significant for limpets (except limpet samples
taken at Urvillle: only 30% of measurements are
significant). When measuring 239+240Pu, over 90%
of results were significant for most monitoring
points, except Urville where only 70% exceed thedecision threshold. Figure 33 shows mean activity
by mass calculated for the 2015-2017 period. The
geographic distribution of actinide contaminationin limpets is lower than iodine-129 contamination.
Shellfish (crabs and oysters) are not contaminatedby these radionuclides.
All 239+240Pu measurements for fish samples
between 2015 and 2017 are below the decisionthreshold (< 0.0025 Bq/kg fresh), except one
sample taken on the east coast in 2016, wherean activity by mass of 0.0003 Bq/kg fresh wasmeasured.
Americium-241 was measured in a Saint-Jacquessample in 2017 (0.19 Bq/kg fresh) and in a limpet
sample from Granville in 2016 (0.09 Bq/kg fresh).
The potential dose absorbed by eating local foodcontaminated by plutonium isotopes (239, 240 and238) discharged by the La Hague plant is estimatedat 0.02 μSv/year. This dose was assessed for an
adult. Only mollusc type sea food components ofthe diet were considered (see table 5, for residents
of north Cotentin peninsula, with a fisherman at
the head of the household), given that only theseproducts are regularly contaminated over time.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITE

FIGURE 31 / PLUTONIUM-239+240 ACTIVITY BY MASS MEASURED IN MOLLUSCS CAPTURED NEAR TO THE LA HAGUE SITE
(Bq/kg fresh)

Bq/kg fresh
0.16
0.14
0.12
0.10
0.08
0.06
0.04
0.02
0
Jan-09 Jan-10 Jan-11 Jan-12 Jan-13 Jan-14 Jan-15 Jan-16 Jan-17 Jan-18
St-Jacques,North Cotentin

Oysters,
Oysters,
East Cotentin West Cotentin

Decision thresholds(all species)

169
FIGURE 32 / PLUTONIUM-238 ACTIVITY BY MASS MEASURED IN MOLLUSCS CAPTURED NEAR TO THE LA HAGUE SITE (Bq/kg fresh)

Bq/kg fresh
0.07
0.06
0.05
0.04
0.03
0.02
0.01
0
Jan-09 Jan-10 Jan-11 Jan-12 Jan-13 Jan-14 Jan-15 Jan-16 Jan-17 Jan-18
St-Jacques,North Cotentin

Oysters,
East Cotentin

Oysters,
West Cotentin

Decision thresholds(all species)

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 33 / MEAN 239+240PU AND 238PU ACTIVITY BY MASS MEASURED IN LIMPET SAMPLES TAKEN NEAR TO THE LA
HAGUE SITE (Bq/kg fresh)
Mean values for the 2015-2017 period for 6 samplers.

0.012
0.008

Orano site
La Hague

0.012<0.008

0.017
0.010

0.018
0.009

0.013

0.018

170

0.007

Sampling points(source: RGE-BDTOPO@ & BDCARTO@ by IGN - 2015 ed.)0.020

Mean plutonium (239+240)Pu and 238Pu activity
Plutonium-239+240 value (Bq/kg fresh)
Plutonium-238 value (Bq/kg fresh)
Limpets (6 sampling points)

Finally, the impact of discharges from La Hague
can also be detected in sediments and algae. Mean
activity by mass in ocean sediments over this same
period (see table 3), ranges from 0.31 Bq/kg dry
at Barfleur to 1.1 Bq/kg dry in Cherbourg bay for
239+240
Pu and from 0.15 to 0.46 Bq/kg dry for 238Pu.
With the exception of Barfleur, 241Am issystematically quantified in ocean sediments.
The maximum mean activity by mass measured
reached 2.9 Bq/kg dry in Cherbourg bay. 244Cm
is also occasionally measured in sediments(10% of results exceed the decision threshold).
Significant measurements range from 0.14 Bq/

kg dry in Cherbourg bay to 0.82 Bq/kg dry at AnseSaint-Martin. The highest values were recorded
for samples from Cherbourg bay due to the finer
sediments in the bay. The radionuclides can fix tothese sediments more effectively. As was the casefor sea food, the mean isotopic ratio between 238Pu
and 239+240Pu calculated based on activity levels forthe different sediment samples is equal to 0.43,
and provides proof of an industrial source.
Activity measured over the 2015-2017 period inalgae ranges from 0.048 (< DT) to 0.49 Bq/kg dryfor 239+240Pu and from 0.042 (< DT) to 0.3 Bq/kg dryfor 238Pu.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITETABLE 3 / MEAN ACTIVITIES BY MASS MEASURED IN OCEAN SEDIMENTS COLLECTED NEAR TO THE LA HAGUE SITE (Bq/kg
dry)

Mean activities by mass (Bq/kg dry)

Sampling site

Pu

Pu

238

239+240

Am

241

Anse des Moulinets

0.15

0.33

0.58

Elcagrain

0.21

0.51

0.92

Anse St-Martin

0.39

0.95

2.02

Grande Rade de Cherbourg

0.46

1.06

2.86

Sciotot

0.18

0.44

0.77

Anse du Brick (Cap Lévi D1)

0.39

1.01

1.97

Anse du Brick (Cap Lévi D2)

0.32

0.65

1.41

Barfleur

0.15

0.31

0.40

Ruthenium-106, cobalt-60, caesium-137 andstrontium-90
Up until around 2005, ruthenium-106, cobalt-60
and even caesium-137 activity levels, mainly
measured in algae, molluscs and shellfish, wereaffected by liquid discharges from the La Hague
plant, not only in the marine environment (northcoasts of the Cotentin peninsula), but along theentire French coast of the Channel(6).
Most of these radionuclides can no longer be
detected as part of Orano's monitoring programme
since liquid discharges containing specificradionuclides have been reduced (from 2007).
Ruthenium-106
106
Ru is no longer detected in sediments due to thedecrease in quantities discharged and the relative
short half life of this radionuclide. 106Ru has only
been detected in 20 to 40% of limpet samples
captured in Elcagrain bay, Anse des Moulinets andSiouville since 2015. Despite this, the activity bymass measurements were all close to the decisionthreshold (and between 0.9 and 2.3 Bq/kg fresh).
Ruthenium-106 was also detected in a sample ofSaint-Jacques molluscs in 2017 (0.9 Bq/kg fresh).

Two grass samples taken at Pont Durand in Marchand April 2016 were contaminated with 106Ru.
Activity by mass measurements represented 14
and 6 Bq/kg dry).

Cobalt-60

Cobalt-60 is only occasionally detectable in sea
food due to a progressive decrease in discharges
containing this radionuclide. Cobalt-60 was
only measured twice in 2015 in a spider crab
sample and in a limpet sample from the Ansedes Moulinets (activity by mass of 0.30 Bq/kg
and 0.19 Bq/kg respectively) and once in 2017, ina Saint-Jacques sample (0.15 Bq/kg fresh) as partof the monitoring programme for the 2015-2017
period.
According to the studies conducted by IRSN, at
the request of EDF, cobalt-60 is detected lessfrequently in sea food off the coast of Normandy(see table 4).
Cobalt-60 is still regularly detected in sediment
samples taken from Cherbourg bay (1.9 Bq/kg dry)
Levels decrease with distance (0.65 Bq/kg dry at
Anse Saint-Martin and < DT towards the monitoring
points located after the tip, heading along thecoast towards the east (Elcalgrain and Anse desMoulinets). This decrease is also apparent on theeast coast of the Cotentin peninsula, with a mean
activity by mass of 0.6 Bq/kg dry at Anse du Brick(monitoring point SD16) and < DT at Barfleur.
Finally, the activity levels measured at the different
sampling points range from 0.18 (< DT) to 1.39 Bq/
kg dry in algae.

6. Ruthenium-106 activity levels are attributed to discharges from La Hague as the NPPs do not release this radionuclide; cobalt-60 and caesium-137
activities are mainly attributable to discharges from Hague, which are 1000 to 10,000 times higher than NPP discharges. This difference is currently
smaller.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /171

TABLEAU 4 / COBALT-60 AND RUTHENIUM-106 ACTIVITY BY MASS MEASURED IN MOLLUSCS COLLECTED IN THE
CHANNEL AND ANALYSED IN STUDIES ENTRUSTED TO IRSN BY EDF FOCUSING ON NPPS (Bq/kg fresh)
The ratio indicates the number of times the radionuclide was measured over the number of measurements (all other results are below
the decision threshold).

EDF NPPIsotope

2006

2007

2008

2009

2010

2011

2012

2013

2014

0.04-0.14
5/6

0.03-0.7
7/8

0.06-0.11 0.02-0.05 0.03-0.06 0.03-0.07
5/7
2/8
5/8
5/8

0.0170.029
5/8

0.2
2/9

0.023-0.03 0.27-0.60
2/6
2/6

0.6-0.8
3/8

0.3-0.4
3/7

0.15
1/8

Co

0.03
2/5

0.04-0.08
2/7

0.03
1/7

0.02-0.06 0.02-0.03
4/5
2/6

Ru

-

-

0.08
1/7

0.12
1/5

Co

0.023
1/7

0.03-0.15
5/6

0.03
1/7

Ru

0.3
1/7

0.26-0.6
3/6

-

Co

0.019-0.04
3/9

Ru

60

Flamanville
106

60

Paluel
106

60

Penly
106

Co

60

Gravelines
106

Ru

0.027
1/6

0.2-0.3
3/4-

0.18-0.27 0.12-0.16
2/8
3/8

2016

0.015-0.03
3/7

0.0090.041
3/7

0.11-0.23 0.19-0.28
3/7
2/7

-

0.03
1/6

0.02
1/6

0.0230.071
3/6

0.043
1/6

0.042
1/6

-

-

-

-

-

-

-

0.11
1/5

0.02
1/7

0.01-0.03
2/7

0.03
1/6

-

0.012
1/6

0.013
1/6

0.021
1/6

-

-

-

-

-

-

-

-

0.05
1/2

0.02
1/3

0.01-0.04
4/6

0.033
1/4

-

0.012
1/2

-

-

-

-

-

-

0.04-0.05 0.04-0.05 0.02-0.06 0.02-0.03 0.02-0.03
3/5
3/4
3/5
5/6
2/4
0.15
1/5

0.25
1/8

2015

0.16
1/6

-

172
Caesium-137

In a terrestrial environment, it would appear that
residual contamination can be detected in thearea to the north west of the La Hague site. In
fact, as shown by soil analyses near to the Landes
stream in 2016 and 2017, (see chapter 5.4, focus
article on the Landes stream) mean activities bymass measured in this area exceed backgroundradiation levels for this radionuclide due to fallout
from nuclear tests and the Chernobyl accident.
This contamination was originally airborne andwas released in past events, particularly thedischarge incidents recorded from 1974. At thistime, concrete blocks containing waste stored
at off-site areas in the north west disseminatedcaesium-137 in the region.
This contamination can also be detected, to alesser extent, at Orano's regular grass monitoring
points to the north west of the site: mainly
monitoring point A15 near to where the Landes
stream comes out, and moving farther away fromthe site towards the north, at point A6 (Acres) andpoint B18 (Hameau Ricard). Activity levels by mass
for the grass samples collected at these threepoints almost always, or regularly, exceed local
background radiation levels for this type of matrix(< 0.4 Bq/kg dry at Flamanville). The same cannot
be said for other monitoring points (see figure 34).
However, grass sample measurements are low
enough to prevent a transfer of the radionuclides
to cow's milk. In fact, all of the results for thistype of matrix are below the decision threshold(< 0.04 Bq/L).
Mushrooms are the only terrestrial food withsignificant results, with a mean activity by massmeasured between 2015 and 2017 of 0.2 Bq/kg
fresh, which is equal to background radiationlevels for this type of food.
Caesium-137 is also discharged by the La
Hague plant in liquid effluents. The annual
activity discharged (660 GBq/year for 2016) is
progressively decreasing (see figure 35). In termsof sea food, caesium-137 activity by mass in fish
captured along the Cotentin coast is relatively
stable on the west and east coast and has been
gradually decreasing on the north coast since 2015(see figure 35). Activity levels measured between
2015 and 2017 range from 0.05 to 0.25 Bq/kg fresh,with a mean value of 0.09 Bq/kg fresh. Results
for this radionuclide are similar to backgroundradiation in sea fish (0.08 Bq/kg fresh).

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITE

The only food with activity by mass measurements
which exceed background radiation is fish,
based on caesium-137 measurements.

The dose absorbed by individuals who regularly
eat this fish from La Hague is extremely low,depending on the selected scenario (less than
0.001 µSv/year).

FIGURE 34 / CAESIUM-137 ACTIVITY BY MASS IN GRASS SAMPLES TAKEN NEAR TO THE LA HAGUE SITE (Bq/kg dry)
BETWEEN 2015 AND 2017

Bq/kg dry
5
4.5
4
3.5
3
2.5
2
1.5
1
0.5
0

Jan-15 Apr-15 Jul-15 Oct-15 Feb-16 May-16 Aug-16 Dec-16 Mar-17 Jun-17 Sep-17

Calais farm (A12) (decision thresholds)
North-west (A15)North-west (decision thresholds)
Les Acres (A9)Les Acres (A9) (decision thresholds)

Monts Eperons (A3) (decision thresholds)
Pont Durant (A5) (decision thresholds)
Ricard village (B18)
Ricard village (decision thresholds)

Range for natural background radiation and nuclear weapons tests

FIGURE 35 / CAESIUM-137 ACTIVITY BY MASS MEASURED IN FISH CAPTURED IN THE CHANNEL NEAR TO THE LA HAGUESITE (Bq/kg fresh) BETWEEN 2015 AND 2017

Bq/kg fresh
0.45
0.40
0.35
0.30
0.25
0.20
0.15
0.10
0.05
0
Jan-09 Jan-10 Jan-11 Jan-12 Jan-13 Jan-14 Jan-15 Jan-16 Jan-17 Jan-18
East Cotentin

North CotentinWest Cotentin

Decision thresholds (all sources)

Range for natural background radiation and nuclear weapons tests

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /173

Strontium-90

Strontium-90 is one of the main radionuclides
remaining from fallout from atmospheric nuclear
testing. This radionuclide can also be found in liquid
effluent discharges from the La Hague plant and ispart of the fission products discharged at sea.

174

In an aquatic continental environment, strontium-90
activity by volume in rivers near to the La Hague
plant is approximately at background radiationlevels due to the leaching of soils contaminatedby atmospheric fallout from nuclear tests, that is< 10 mBq/L. Only the contamination of the Landes
stream, which runs to the north west of the La
Hague site, exceeds background radiation levels.
Activity levels measured between 2015 and 2017at the point where the Landes stream discharges
range from 0.6 to 1.4 Bq/L. (see figure 36). These
concentrations must be compared with thestrontium-90 content of the ground water feeding
this stream due to an incident in the 1980's whenconcrete pits used to store waste on the surface
deteriorated and leaked content. The waste hassince been recovered.

Over 97% of values are significant (7) for the cow's
milk samples from the five farms located in themunicipalities of Beaumont-Hague, Digulleville,
Herqueville and Jobourg (see figure 37). The
highest mean activity by volume recorded over the2015 - 2017 period (0.07 Bq/L) was measured for
the Beaumont-Hague farm. Strontium-90 levels
at other farms are at local background levels(0.036 Bq/L); mean activity levels by volume range
between 0.035 and 0.037 Bq/L.
Any one individual drinking cow's milk and dairy
products from the municipality of BeaumontHague would absorb a dose of 0.05 µSv/year,
depending on the selected scenario. The mean
activity by volume for milk samples taken at thetwo farms located in the municipality of BeaumontHague was used for these calculations. This dose
drops to 0.02 µSv/year if the mean activity byvolume calculated using all of the milk samples
from the farms located in the area around the site
is assumed(8).

7. In this document, a "significant value" is defined as a measurement which is above the decision threshold (DT).
8. The annual ration of milk and dairy products consumed locally in the selected scenario represents 10.2 kg/year and 8 L/year of milk.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITE

FIGURE 36 / STRONTIUM-90 ACTIVITY BY VOLUME IN STREAM WATER SAMPLES TAKEN NEAR TO THE LA HAGUE SITE
(Bq/L)(IRSN data)

Bq/L
3
2.5
2
1.5
1
0.5
0
Jan-09 Jan-10 Jan-11 Jan-12 Jan-13 Jan-14 Jan-15 Jan-16 Jan-17 Jan-18
Landes stream spring
Moulinets stream,
Le Batardeau
Sainte-Hélène stream

Landes stream
Moulinets stream,
Recboc spring

Combes stream
Le Grand Bel stream(decision thresholds)

175
FIGURE 37 / STRONTIUM-90 ACTIVITY BY VOLUME MEASURED IN MILK SAMPLED NEAR TO THE LA HAGUE SITE SINCEJANUARY 2009 (Bq/L)

Bq/L
0.2
0.18
0.16
0.14
0.12
0.1
0.08
0.06
0.04
0.02
0
Jan-09 Jan-10 Jan-11 Jan-12 Jan-13 Jan-14 Jan-15 Jan-16 Jan-17
Beaumont - Hague(rue de Beaumont)
Beaumont - Hague(Ès Galle village)

Digulleville(Rantot farm)
Herqueville(Église village)

Jobourg(Ricard village)
Decision thresholds(all farms)

Range for natural background radiation and nuclear weapons tests

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Summary of dose evaluations
Excluding tritium, since the dose absorbed byinhaling or ingestion is extremely low despite thelarge quantities discharged into the environment,
krypton-85, carbon-14 and iodine-129 are themain three radionuclides discharged at the La
Hague site in liquid or gaseous effluents, andrepresent the primary contributions to the dose
reaching local residents.
If we consider a reference group, virtually
spread around the site, breathing air containinga mean activity measurement by volume of eachradionuclide as measured at various points aroundthe site and eating local food(9) according to theselected mean scenario for an individual living in
north Cotentin, with a fisherman at the head of
the household, approx. 80% of the total effective
dose is contributed by krypton-85 due to theinherent external exposure. On a subsidiary basis,carbon-14 contributes 10% of the dose, mainly
due to residents eating local food, and iodine-129
contributes 7%, exclusively due to eating local
food. The remaining 5% of the total dose iscontributed by tritium, followed by strontium-90
and plutonium (238+239+240) on a 50/50 basis.
Caesium-137 input is extremely low.

FIGURE 38 / DISTRIBUTION OF THE DOSE BASED ON THE RADIONUCLIDE MEASURED IN THE ENVIRONMENT FOR A
REFERENCE GROUP VIRTUALLY SPREAD AROUND THE AREA

Average scenario(family with a fisherman at its head)
176

85.2% food and drink
14.8% inhaling
99.9% food and drink
0.1% inhaling

Kr

85

7%

5%

C

14

I

129

10 %

Others radionuclides(3H, Pu, 137Cs, 90Sr)

78 %100% external exposure

Contribution by other radionuclides (radionuclides)
H

3

10 %
<0%

Pu (238+239+240)
137

10 %

90

Cs

Sr

80 %

9. The mean activity of each radionuclide is calculated based on all food samples taken near to the site.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITE

The scenario adopted when assessing thedoses absorbed by the population as part of theradiological report for the 2015-2017 period tends
to represent an average diet for people living in thenorth of the Cotentin peninsula. Two diets were
proposed in 1999 as part of the study carried out
by the GRNC (Groupe Radioécologie Nord Cotentin- North Cotentin peninsula radioecology group) inorder to assess more worst-case dose scenarios.
The first diet represents a fisherman living in
the Huquets area at Jobourg and who regularlyeats sea food, and the second diet represents a
farmer living at Pont Durand near to Digulleville,

eating a high percentage of roof vegetables anddairy products. Levels of self-sufficiency are
identical for both diets. The quantities of local foodeaten each year, based on this self-sufficiency
ratio, are shown in table 5.
Large differences can arise for the quantity ofsome products eaten based on the selected diet.
This is particularly true for sea food for fisherman
and dairy products for farmers. The effective doseis then calculated based on the amount of local
food eaten and will necessarily vary (see figure 39).

TABLE 5 / QUANTITY OF LOCAL FOOD EATEN

Food

Fisherman in the Huquets
zone

Average scenario in theradiological report: a person
living in the north of theFarmer living at Pont Durand
Cotentin peninsula with afisherman at the head of thefamily177

Food ration (kg/year or l/year for milk and water)
Shellfish

32.3

6.9

1.8

Molluscs

23.3

5.3

2.7

Fish

35.5

12.2

5.9

Milk

75.6

184.1

8.0

Dairy produce

9.9

23.4

10.2*

Lamb and mutton

1.1

1.1

0.6

Poultry

10.8

15.1

3.2

Rabbit

2.0

2.8

0.9

Eggs

9.6

20

3.9

Leaf vegetables

14.4

33

2.0

Root vegetables

78.6

159

21.2

Jams

3.4

8.4

0.5

Fruit

2.9

Honey

0.2

Water

720

* Including yoghurt and fresh cheese, cow's cheese and animal fat (butter).

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 39 / ASSESSMENT OF THE DOSES ABSORBED BY PEOPLE LIVING NEAR TO THE LA HAGUE SITE FOR EACH
RADIONUCLIDE DETECTED IN THE ENVIRONMENT AS PER VARIOUS SCENARIOSµSv/year
4.5
4
3.5
3
2.5
2
1.5
1
0.5
0

Kr

C

85

14

I

H

129

3

Pu

238+239+240

137

Cs

90

µSv/year
0.25
178

0.2
0.15
0.1
0.05
0

H

3

Pu

238+239+240

137

Cs

Average scenario from the radiological report
Fishermen from the Huquets area (Jobourg)
Farmers living at Pont Durand (Digulleville)/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

90

Sr

Sr

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
LA HAGUE SITE

The doses calculated based on these three
scenarios are between 4 µSv/year for the mean
scenario adopted for the radiological report and8 µSv/year for the farmer at Digulleville.
These estimates are based on mean activity levels
calculated based on the results of measurements
obtained during environmental monitoring andare fully consistent with those obtained by Oranofor the year 2016 on the basis of actual discharge
data. In fact, Orano estimated the effective dose
potentially absorbed by a fisherman at Goury at
5 µSv/year and the dose potentially absorbed bya farmer at Digulleville at 13 μSv/year.

Overview
The activities measured in the La Hague
environment between 2015 and 2017 match those
expected based on authorised discharge levels.
These measurements also follow on from datafrom previous years. Krypton-85, carbon-14,
iodine-129 and tritium are the radionuclides
most regularly measured in the environment,
as expected based on their dominant compositionin effluents discharged.

© E. Larrayadieu/Interlinks Image/Areva

179

Water samples taken near to the La Hague site

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Aube storage facility and Morvilliers
storage facility
The Aube storage facility (CSA) is located in themunicipalities of Soulaines-Dhuys, Ville-aux-Boisand Epothémont in the Aube department, andhas been operated by ANDRA (INB no. 149) since
January 1992. The CSA is the second surface
storage facility in France for radioactive waste withweak and moderate activity and a short half life
(WMA-SL). The CSA took over from the Channel
storage facility. This storage facility is authorisedfor up to 1 million packages of radioactive waste.
33% of this authorised storage capacity had beenreached by late 2017.

180

Most waste with a WMA-SL configuration is
generated from small items of equipment
contaminated during maintenance operations(gloves, clothing, tools, etc.) and the operationof French nuclear facilities (treating liquidand gaseous effluents). WMA-SL waste is also
generated by research laboratories, hospitals,
universities, etc. or by decommissioning or
purification operations.

Waste is conditioned in concrete or metal packages(drums, caissons) before being stored at the CSA
on the surface in reinforced concrete structureswith open tops. Waste is stored under portable
metal rail-fitted frames which protect from rain.
Once full, the structures are sealed with a concreteslab and an impermeable coating is added.
A waste conditioning workshop is available at the
CSA. This workshop comprises an injection unit
used to block and contain specific large waste
items supplied by the producers without a coatingin mortar, and a compacting unit used to reducethe volume of compactable waste.
The Cires Industrial combination and storage facility(Centre industriel de regroupement, d’entreposage
et de stockage) is located just a few kilometers fromthe CSA in the municipalities of Morvilliers and La
Chaise. This facility is environmentally-classified(ICPE) and has been dedicated to storing very low
activity (VLA) waste since 2003. This storage facility
is authorised for up to 650,000 m3 of radioactive
waste. 54.2% of this maximum authorised capacity
had been reached in 2017.

FIGURE 1 / MAP SHOWING THE LOCATIONS OF THE AUBE AND CIRES STOCKAGE FACILITIESCSA siteRoad networks, hydrographics and site boundaries
Departmental road
Permanent river or stream
Seasonal river or stream
Site boundary

CIRES site

Municipal borderLand use
Construction or building
Anthropic surface (Structure)
Anthropic surface (Industry or shops)

Toponymy: hydrographic
network

ForestRiver, stream or lake
Other(source: RGE-BDTOPO@ & BDCARTO@ by IGN - 2015 ed.)/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
AUBE STORAGE FACILITY AND MORVILLIERS STORAGE FACILITY

FIGURE 2 / AUBE STORAGE FACILITY (CSA)181

FIGURE 3 / THE INDUSTRIAL COMBINATION AND STORAGE FACILTY (Cires)

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /VLA waste mainly comprises gravel, earth, scrap
metal, etc. with very low contamination levels.
This waste is generated when decommissioningor operating nuclear facilities or traditional
industrial sites using materials which arenaturally radioactive. This waste can also be
generated when treating or renovating old sites
contaminated by radioactivity.
Cires includes a VLA waste treatment building
used to reduce the volume of compactable waste.
VLA waste is stored at Cires in cells in clay units.
Once these cells are full, they are sealed with acoating, which mainly comprises a high density
polyethylene membrane and an outer envelopeof natural clays. These operations are carried out
under portable roofs, which protect from rain.

182

Cires has also proposed combination and storage
solutions for radioactive waste since 2012.
The waste combined at the facility is collectedfrom approximately 1,000 non-electronuclear
producers spread throughout France (hospitals,
pharmaceutical laboratories, individuals, etc.).
A very wide range of types of waste is handled:
gloves, plastics, solvents, blouses, lightning
arresters, smoke detectors, etc. Most of thiswaste is VLA or WMA-SL and storage options
are available. Some of this waste has a weak ormoderate activity level and a long life; no storage
solutions are currently available for such waste
and it is stored at the site. Since 2016, Cires has
also run a facility specifically dedicated to sorting
and treating this waste from non-electronuclear
activities and combined at the site.

Radioactive discharges
Radioactive discharges from the CSA

Waste conditioning operations lead to radioactive
gaseous effluents, which are discharged via
the stack in the waste conditioning workshop.
These effluents are routed at source by nuclear
ventilation systems. Very high efficiency (VHE)
filters are fitted in ventilation ducts to purify any
dust or aerosols in the effluents, as necessary.
Tritium, radioactive iodine isotopes and carbon-14
are not filtered and are therefore likely to bedischarged into the atmosphere.
Gaseous elements, dust and aerosols aremonitored prior to discharge to the atmosphere.
The aim of this process is to quantify the elements
discharged to the environment; continuous
samples are taken for this purpose, withsubsequent laboratory measurements. The flowrate for the air discharged is also measured.
A representative portion of the air discharged issampled in the ventilation duct and trapped using
filters (dust - gross alpha/beta activities and alphaand beta-gamma emitters), activated carbon
cartridges (used to trap iodines -125I, 129I and 131I)
and bubblers (trapping 3H and 14C).
These sorted discharges are subject to maximum
discharge levels as defined by order. Annual tritium
discharges since 2006 have varied between 0.082
and 7.3 GBq (see figure 4). Tritium is the mostfrequently measured radionuclide in gaseousdischarges from the CSA.
The liquid effluents produced in the facilities
and likely to be contaminated are collected inseveral tanks at the site and then tested (tritium,
carbon-14, alpha, beta and gamma emitters),
before potential discharge into the storm retention
basin via a specific network; the storm retention
basin is the only discharge point for liquid effluentsfrom CSA into the natural environment, specificallythe Noues d’Amance stream. Annual discharges
have varied between 0.2 and 5.3 MBq over the last
decade for tritium, the most frequently measured
radionuclide in liquid discharges from the CSA.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
AUBE STORAGE FACILITY AND MORVILLIERS STORAGE FACILITY

Radioactive waste from the Cires site

Gases are discharged from Cires due to VLA waste
treatment operations (compacting) and the sorting
and treatment of waste from non-electronuclear
operations. A continuous air sampling systemfitted at the discharge point for the ventilation/
filtration system is used to test the air discharged(atmospheric tritium, iodines (125I, 129I and 131I),
carbon-14 and gross alpha and beta activity levels
are measured) from each of the two discharge
points.

Liquid effluents from Cires likely to containradiological contamination are considered asliquid waste and collected + stored in tanks prior
to recycling and elimination via an authorised
external treatment unit. These effluents are nottherefore discharged into the environment. Other
liquid effluents (rainwater, household effluents,etc.) are collected, treated if necessary (settling,
oil removal) and then routed to the Loriguettestream to the north of the site and to the Courgain
stream to the south of the site via basins.

These sorted discharges are subject to maximum
discharge levels as defined by prefectoral order.
Annual discharges have varied between 32 and300 MBq over the last decade for tritium, the mostfrequently measured radionuclide in gaseousdischarges from Cires.

FIGURE 4 / VARIATION IN LIQUID AND GASEOUS TRITIUM DISCHARGES FROM THE CSA BETWEEN 2006 AND 2017 (GBq/year)

GBq/year

183

10

1

0.1

0.01

0.001

0.0001

2006

2007

2008

2009

2010

Gaseous tritium discharges
Liquid tritium discharges

2011

2012

2013

2014

2015

2016

2017

Gaseous carbon-14 discharges
Liquid carbon-14 discharges

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Radiological monitoring of the site environment
Monitoring the CSA

184

The operator monitors radioactivity in theatmosphere by measuring ambient gamma
radiation directly, and with differed measurements
based on daily atmospheric dust samples (gamma
spectrometry, gross alpha and beta activity
measurements), and periodic air (atmosphericcarbon-14 and tritium measurements), halogen
gas (iodine-125, 129 and 131 measurements)
and rainwater (gross alpha and beta, carbon-14
and tritium activity measurements) samples
collected via monitoring stations located as per
the prevailing winds. Two monthly samples andone quarterly plant sample are taken in theterrestrial component, as well as two monthly
milk samples. An annual sampling run is alsoorganised for mushrooms, the main farming
output and topsoil, particularly in areas under theprevailing winds. Gross alpha and beta activities
are also generally measured in terrestrial water
samples, and gamma spectrometry is performed.
Carbon-14 measurements are also organised eachquarter, and tritium measurements and alpha
spectrometry are performed annually, particularly
aiming to measure transuranic elements andcomplement the above analyses.

Ground water under the CSA is tested on a monthly
basis using 9 piezometers mainly installed inside
the CSA, and at 13 other locations on a quarterly
basis. Tritium and gross alpha and beta activities
are measured using these samples.
Monitoring the Cires site

The Cires monitoring programme is defined in aprefectoral order on site activities. A continuous
air sampling system is fitted in the administrativebuilding and can be used to check the impact ofdischarges routed from the treatment building anddischarges diffused by the facility (storage cells,etc.). The same measurements are taken at thissampler as those taken at the treatment building
discharge point. Cires can also access ambient
gamma radiation measuring systems (passive
dosimeters).
Water and sediment samples are taken fromstreams (Courgain and Loriguette steams).
Gross alpha and gross beta and tritium activity ismeasured for water samples. alpha and gamma
spectrometry is performed on sediments.
Barrémien and Aptien ground water is monitored
on a 6-monthly basis for radiological purposes.

Occasional surface water and sediment samples(weekly, monthly and quarterly) are taken in theaquatic component, more specifically in the Noues
d’Amance stream, upstream and downstream
from the discharge point, and in the Voire river,downstream from the CSA discharge point. Tritiumand gross alpha and beta activities are measured inwater and sediment (in water) samples. Alpha andgamma spectrometry is also used to complement
these results on a regular basis (downstream
from the discharge point). Annual fish samples
and 6-monthly aquatic plant samples are taken
in Noues d’Amance. Analysis results for aquatic
flora and fauna are similar to those for water andsediment samples.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
AUBE STORAGE FACILITY AND MORVILLIERS STORAGE FACILITY

The impact of the ANDRA Cires and CSA sites on
their immediate environments
Atmospheric carbon-14 levels are monitored by a
bubbler. The decision thresholds for the methods
used are close to atmospheric backgroundradiation levels. Gaseous iodine-125, 129 and
131 are monitored by taking air samples via
a cartridge and by monitoring atmosphericaerosols. No radionuclides were detected in theimmediate environment of the storage facilities
run by ANDRA between 2015 and 2017. Tritium
has been detected in the air as HT or HTO since
May 2014 (see figure 5). Decision thresholds are
between 10 and 20 times background radiationlevels for atmospheric tritium, therefore theseanalyses do not decisively indicate if ANDRA
discharges potentially affect the area. On the other
hand, in terms of the rainwater samples collected
between January 2015 and December 2017, whichwere all found to have activity levels below thedecision threshold of approx. 2 Bq/L and therefore
within the current background range, no visible
contamination occurred during rainfall.

This lack of contamination by tritiated atmosphericdischarges was confirmed by measuring results
for this radionuclide in grass and soil samples
taken during the 2015-2017 period. Bound tritium
activity levels for these results are either below
the decision threshold, or between 0.2 and 1.7
Bq/kg fresh, i.e. within the current background
range. In addition, according to measurement
results for grassland samples, carbon-14 activity
varies extensively. Measurement uncertainty of
up to 60% of results must also be considered.
Contamination from ANDRA facilities cannot be
concluded based on these uncertain results. Allother measurements taken in the immediate
environment of these two storage facilities areeither natural radioactivity (40K, 7Be, etc.) or
residual fallout from the Chernobyl accident or
the testing of nuclear weapons (137Cs).

185

FIGURE 5 / AMBIENT TRITIUM ACTIVITY BY VOLUME NEAR TO THE CSA AND CIRES FACILITIES BETWEEN JULY 2011 AND
DECEMBER 2017 (Bq/m3)

Bq/m 3
0.8
0.7
0.6
0.5
0.4
0.3
0.2
0.1
0
Jun-11 Dec-11 Jun-12 Dec-12 Jun-13 Dec-13 Jun-14 Dec-14 Jun-15 Dec-15 Jun-16 Dec-16 Jun-17
Tritium in HT form

Decision thresholds
Tritium in HTO form

Total tritium

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Tritium has not been detected as part of rivermonitoring (see figure 6) since August 2014 inmeasurements taken in stream water, upstream
from Cires (Chantecocq stream), between Cires
and the CSA (Courgain stream, Loriguette stream)and downstream from the CSA (Noues d’Amancein particular).

Measurements taken using sediment, fish andaquatic plant (ranunculus) samples failed to reveal
any contamination of the aquatic environment bydischarges from facilities operated by ANDRA.

FIGURE 6 / TRITIUM ACTIVITY BY VOLUME MEASURED IN SURFACE WATER SAMPLES TAKEN NEAR TO THE CSA AND
ANDRA CIRES FACILITIES BETWEEN JULY 2011 AND DECEMBER AND 2017 (Bq/L)

Bq/L
6

5

4
186
3

2

1

0
Jul-11 Jan-12 Jul-12 Jan-13 Jul-13 Jan-14 Jul-14 Jan-15 Jul-15 Jan-16 Jul-16 Jan-17 Jul-17
Decision thresholds
Chantecocq stream - upstream from the CIRES site

Courgain stream - downstream from the CIRES site

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Industrial sites / 3.3
AUBE STORAGE FACILITY AND MORVILLIERS STORAGE FACILITY

Ground water near to these two facilities ismonitored for radiological purposes using two
piezometers installed both on- and off-site. The
tritium activities found in water samples taken
at specific locations in 2015 were several times
greater than background radiation, and peaked at
3.8 Bq/L (see figure 7).

Tritium was only detected once after January
2016 in ground water, with an activity level close
to background radiation (2.1 Bq/L), using a
piezometer located near to the storage facility.
Measurements for beta and alpha emitters failed
to reveal contamination by discharges from
ANDRA facilities.

FIGURE 7 / TRITIUM ACTIVITY BY VOLUME MEASURED IN GROUND WATER SAMPLES TAKEN USING PIEZOMETERS AT THE
CSA AND ANDRA CIRES FACILITIES BETWEEN JULY 2011 AND DECEMBER 2017 FOR ALL PIEZOMETERS (Bq/L)

Bq/L
9
8
7
6
187

5
4
3
2
1
0
Jul-11 Jan-12 Jul-12 Jan-13 Jul-13 Jan-14 Jul-14 Jan-15 Jul-15 Jan-16 Jul-16 Jan-17 Jul-17
Decision thresholds

Measurement

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /3.4. RESEARCH SITES• the Gammatec facility (INB 170) operated by
STERIS: this site houses gamma irradiators forthe purposes of research and development.

Marcoule site
Discharges and monitoring plans
The Marcoule (Gard) site is home to around twenty
facilities, including five basic nuclear facilities(INB):• the Phénix reactor (INB 71) operated by CEA: afast neutron reactor, shut down in 2009;• the Atalante facility (INB 148) operated by CEA:
this facility can be used for fundamental andradiochemical research on highly radioactive
elements;• the Melox facility (INB 151) operated by
Orano Cycle: this facility was constructed torecycle plutonium from French PWR nuclear
powerplants. Morax is currently the only French
plant producing MOX fuel;188• the Centraco facility (INB 160) operated by
Socodei: this facility was commissioned in 2000,
and processes weakly radioactive effluents andwaste aiming to reduce volumes before sending
the former to ANDRA facilities for storage.

The site is also home to a secret basic nuclear
facility (INBS) operated by CEA. The mainunits at this INBS have been shut down anddecommissioning is in progress:• the Célestin 1 & 2 reactors were definitively shut
down towards the end of 2009;• The Tritium workshop at Marcoule (ATM) was
definitively shut down in June 2012.
The radioactive liquid effluents produced at thesite are transferred to the liquid effluent treatment
station (STEL) operated by CEA. The CENTRACOINB is equipped with its own treatment unit for
liquid effluents and subsequently discharges
them. The details of discharges cannot beprovided for each facility. Gaseous discharges are
distributed between the different site facilities(Atalante, Phenix, Centraco and Melox) and eachfacility holds its own discharge authorisation.
Table 1 provides details of liquid and gaseousdischarges.

FIGURE 1 / MAP SHOWING THE LOCATIONS OF CEA MONITORING POINTS (on the left) AND IRSN MONITORING POINTS(on the right) NEAR TO THE MARCOULE SITE

Marcoulesite

Marcoulesite

Marcoule
siteRoad networks, hydrographics and site boundaries Land use

CEA and IRSN sampling points (Number)
Atmosphere (10 - 3)

Fruit (1 - 1)

MotorwayConstruction or building

Rainwater (1 - 1)

Wheat (0 - 1)

National road

Anthropic surface (Structure)

Surface water (4 - 1)

Milk (1 - 1)

Railway

Anthropic surface (Industry or shops)

Drinking water (1 - 0)

Fish (1 -1)

Departmental road

Vineyards and orchards

Ground water (12 - 0)

Soil (2 - 0)

Permanent river or stream

ForestGrass (10 - 2)

Sediment (1 - 3)

Tree leaves (0 - 2)

Meat (0 - 1)

Aquatic plants (1 - 2)

Wine (0 - 1)

River, stream or lake

Seasonal river or stream

Other

Site boundary(source: RGE-BDTOPO@ & BDCARTO@ by IGN - 2015 ed.)/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
MARCOULE SITETABLE 1 / DISTRIBUTION OF DISCHARGES FROM THE DIFFERENT FACILITIES IN 2016

Gaseous effluents from CEA
Marcoule INBs
(PHENIX & ATALANTE)

2014

2015

2016

Gamma beta aerosols (MBq)

11.4

11

9.9

Alpha aerosols (MBq)

0.14

0.07

0.07

Tritium (MBq)

34.8

77.0

17.8

Halogens (MBq)

8.2

9.0

8.8

Gases excl. tritium (TBq)

46

54

52

Tritiated gaseous effluentsdischarged from INBs (TBq)

2014

2015

2016

37

21

25

Liquid effluents (INBS)*

2014

2015

2016

1.58

0.77

1.71

Alpha emitters (GBq)
Carbon-14 (GBq)

6.29

2.77

4.64

Iodines (GBq)

0.46

0.26

0.12

Tritium (TBq)

22

20.2

38.2

Other gamma beta
aerosols (GBq)

67.9

36.4

63.3

*L
 iquid effluents generated by facilities at the Marcoule site are processed at an INBS facilty (STEL), except for CENTRACO discharges.

CEA at Marcoule and IRSN have implemented
monitoring plans for all environmental components
since the site opened. CEA implements thisplan on behalf of all Marcoule site operators.
Table 2 and figure 1 provide details of thecorresponding monitoring plans. When the
Célestin reactors and the Tritium workshop wereshut down in 2009, tritium discharges from the site
dropped significantly, as shown in figure 2.

FIGURE 2 / VARIATION IN TRITIATED ATMOSPHERIC DISCHARGES FROM THE SITE

TBq/year
1000

100

10

1
1996

1999

2002

2005

2008

2011

2014

2017

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /189

TABLE 2 / CEA AND IRSN MONITORING PLANS FOR THE MARCOULE SITE (the CEA plan shown applied up to December 2016; themonitoring programme was amended on 1 January 2017 when adapting the new discharge authorisation)

Environment
monitored ortype of testing

190

CEA

IRSN

Ambient gamma
radiation• 4 sensors in the immediate environment of the
St-Étienne-des-Sorts, Bagnols-sur-Cèze, Codolet
and Caderousse sites: ambient γ dose rate
• 10 passive dosimeters at the site fence• 2 sensors in the immediate environment of
Bagnols-sur-Cèze and Orange sites: ambient γ dose
rate

Atmosphericaerosols• 4 sampling points at the St-Étienne-des-Sorts,
Bagnols-sur-Cèze, Codolet and Caderousse sites:
gross α and β activities (daily), γ spectrometry ifgross α and β > 2 mBq/m3• 1 sampling point at Codolet:
γ spectrometry (weekly)
isotopic uranium (monthly)

Ambient tritium,
carbon-14 andiodine-129• 2 sampling points at the St-Étienne-des-Sorts
and Codolet sites: ambient tritium (HTO - HT), 129I
and 14C (every 1, 8, 15 and 22 of each month)

Rainwater• 1 sampling point at Codolet:
gross α and β activities, tritium (bimonthly)
and gross α and β activities for TSS (monthly)

Ground water• 10 sampling points on the site or at the site fence:
tritium, gross α and β activities,• 7 sampling points on the Codolet grasslands:
tritium, gross α and β activities

Surface water• 2 sampling points upstream and downstream fromthe site: gross α and β activities with a filtrate,
gross β activity for filtration residue, tritium(weekly), γ spectrometry at the downstream point(monthly)• 1 sampling point at Codolet lake: tritium, gross α
and β activities, γ spectrometry (monthly)

Sediments• 1 sampling point downstream from the site: gross α • 2 sampling points upstream and downstream fromand β activities, γ spectrometry, 90Sr (monthly) andthe site: γ and α spectrometry, 90Sr (6-monthly)γ spectrometry (annual)Fish• 1 sampling point downstream from the site:
gross β activity, γ spectrometry, 90Sr (monthly), 14C
and 3H (annual)• 1 sampling point downstream from the site: γ and α
spectrometry, 90Sr (annual)

Aquatic plants• 1 sampling point downstream from the site:
gross β activity, γ spectrometry, 90Sr (monthly), 14C
and 3H (annual)• 2 sampling points upstream and downstream fromthe site: γ spectrometry, organically-bound tritium, αspectrometry (6-monthly)Soils• 2 sampling points to the north and south of the site:
γ spectrometry (annual)

Grass• 10 sampling points around the site: gross β activity,
γ spectrometry (monthly) free tritium,
α spectrometry (rotate between 3 to 4 points eachmonth), 14C (quarterly rotation between 2 points)• 1 sampling point at Codolet:
tritium (monthly)• 1 sampling point at Codolet lake:
tritium (6-monthly)• 2 sampling points at St-Etienne-des-Sorts andCodolet: γ spectrometry, free tritium, α spectrometry,90
Sr (annual)

Tree leaves• 3 sampling points at St-Etienne-des-Sorts, Codolet
and Caderousse: free and organically-bound tritium(annual)Fruit andvegetables• 1 leaf vegetable sampling point to the south-west of
the site: γ spectrometry, free and organically-boundtritium (annual)• Annual sampling runs for the main farming outputs,
particularly to the north south of the site:• 1 root vegetable sampling point to the south east of
gross β activity, γ spectrometry, 90Sr, 14C and HTO
the site: γ and α spectrometry (annual)(annual)• 1 sampling point to the south-east of the site:
γ spectrometry, free and organically-bound tritium(annual)Wheat• 1 sampling point to the south of the site:
γ spectrometry, organically-bound tritium,
α spectrometry, 90Sr (annual)Meat• 1 sampling point to the south of the site:
γ spectrometry, organically-bound tritium (annual)Wine• 1 sampling point to the south of the site:
γ spectrometry, free tritium (annual)Milk• 1 sampling point at Le Pontet: gross β activity,
γ spectrometry, HTO (monthly)

Drinking water• 4 sampling points at the Caderousse, Codolet,
St-Étienne-des-Sorts and Bagnols-sur-Cèze sites:
gross β activity, tritium (monthly), andα spectrometry (6-monthly)• 2 sampling points to the south and south-west of thesite: γ spectrometry, free tritium, 129I (quarterly)/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
MARCOULE SITE

The impact of the Marcoule facility on its
immediate environment
Tritium

Tritium is the dominant radionuclide in atmosphericand liquid discharges from Marcoule, and is also
the most frequently measured and most abundantisotope in the different environmental components
around the site.
Tritium can be found in two forms in the air:
tritiated water vapour (HTO) and gas (HT and othertritiated gaseous organic compounds). Ambient
activity levels for these 2 forms are measured
using bubblers on a weekly basis at 2 samplingstations: Saint-Étienne-des-Sorts to the north andCodolet to the south of the site. Figure 3 shows theresults for both sampling stations.

Tritiated water vapour is the dominant form.
Despite this, 78% of the HTO measurements
acquired at the two samplers are below
the decision threshold. At the Codolet site,
activity levels measured over the 20152017 period vary from less than 0.09 Bq/m3
to 0.42 Bq/m3 for vapour tritium (HTO) and from
0.12 Bq/m3 to 0.16 Bq/m3 for gas tritium (HT).
Similar values were recorded at Saint-Étiennedes-Sorts: from 0.08 Bq/m3 to 0.40 Bq/m3 forvapour tritium (HTO) and from 0.16 Bq/m3 to0.27 Bq/m3 for gas tritium (HT). In general, therange of activity is smaller than that recorded overthe previous period (2011-2014). This is due to theprogressive decrease in discharges since the Tritium
workshop was shut down in 2012. This decrease
can also be considered as part of a dominant trend
since the Célestin reactors were shut down in 2009.

FIGURE 3 / AMBIENT TRITIUM ACTIVITY LEVELS IN THE FORM OF WATER VAPOUR (HTO) AND AS A GAS(HT and other tritiated gaseous organic compounds) MEASURED IN THE IMMEDIATE ENVIRONMENT OF THE MARCOULE
SITE ON A WEEKLY BASIS

Bq/m 3

191

HTO: tritiated water vapour

3.5
3.0
2.5
2.0
1.5
1.0
0.5
0.0
Jan-12

Jan-13Jan-14

Decision thresholds
Bq/m 3
3.5

Jan-15
CodoletJan-16

Jan-17Jan-18Saint-Étienne-des-Sorts

HT: gaseous tritium

3.0
2.5
2.0
1.5
1.0
0.5
0.0
Jan-12

Jan-13Jan-14
Decision thresholds

Jan-15
CodoletJan-16
Jan-17Jan-18Saint-Étienne-des-Sorts

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 4 /TRITIUM ACTIVITY MEASURED IN RAINWATER (Bq/L)

Bq/L
160
140
120
100
80
60
40
20
0
Dec-08 Dec-09 Dec-10 Dec-11 Dec-12 Dec-13 Dec-14 Dec-15 Dec-16 Dec-17
Decision thresholds

However, significant ambient tritium activity levels
detected in the area around the Marcoule siteremain well above background radiation levels forthis radionuclide (approx. 0.01 Bq/m3 for HTO).
192

The range of activity levels measured for tritium inrainwater samples at Codolet is also decreasing,in line with ambient tritium activity levels andreduced discharges. The range runs from 2.5
Bq/L measured in June 2015 to a peak of 30.6 Bq/L
measured in December 2015 (see figure 4). Thesefigures an be compared with current backgroundradiation levels, which are between less than 1 and3 Bq/L of rainwater.

Rainwater

Grass measurements for samples taken near tothe site are based on the atmospheric activity data
provided above. Indeed, tritium in free water in grass(HTO) reflects the ambient tritium concentration a
few hours prior to taking the sample. Concentration
measurements vary between 2.2 Bq/kg fresh and56.9 Bq/kg fresh (see figure 5) for the period inquestion. On the other hand, according to figure 6,
tritium activity in milk is lower (ranging from lessthan 2.6 to 3.4 Bq/L over the 2015-2017 period), andremains within the background radiation range.
This is due to the fact that the milk samples weretaken at Pontet at a distance from the site and outof the prevailing winds, and that local feed is nottherefore strongly contaminated.

FIGURE 5 / FREE TRITIUM ACTIVITY MEASURED IN GRASS SAMPLES (Bq / kg fresh of HTO) NEAR TO THE CEA SITE AT
MARCOULE

Bq/kg fresh
100
90
80
70
60
50
40
30
20
10
0
May-09

May-10May-11 May-12 May-13 May-14 May-15
Decision thresholds
Grass/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

May-16May-17

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
MARCOULE SITE

Note: over the previous period (2011-2014), freetritium activity levels in milk were mostly above
background radiation levels. This variation was
once again due to the reduction in discharge
levels in recent years. Activity levels measured
in fruit, which range from 2.9 to 9.2 Bq/kg fresh(see figure 7), and wine (8 Bq/L), reflect the limited
tritium contamination of these food items.

(5.2 - 55.4 Bq/kg dry) to match the measurements
for the grass samples, atmospheric water vapour
and rainwater.

Finally, organically bound tritium activity intree leaves collected in the municipalities ofCaderousse and Codolet varies extensively

Over the 2015-2017 period, the highest
measurement was recorded in February 2015 at
piezometer F215 and reached 68 Bq/L.

The impact of tritium discharges from the site canalso be detected in ground water. In general, tritium
activity in ground water samples decreased for all
piezometers installed at the site (see figure 8).

FIGURE 6 / FREE TRITIUM ACTIVITY MEASURED IN MILK (Bq/L) NEAR TO THE CEA SITE AT MARCOULE

Bq/L
16
14
12
10

193

8
6
4
2
0
Jan-09 Jan-10

Jan-11

Jan-12

Jan-13Jan-14

Decision thresholds

Jan-15Jan-16

Jan-17Jan-18Milk

FIGURE 7 / FREE TRITIUM ACTIVITY MEASURED IN FRUIT TAKEN FROM TREES NEAR TO THE CEA SITE AT MARCOULE (Bqof tritium/kg fresh)

Bq/kg fresh
100
90
80
70
60
50
40
30
20
10
0
Dec-11

Dec-12

Dec-13
Dec-14
Dec-15
Decision thresholds
Tree fruitDec-16

Dec-17RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 8 / ACTIVITY LEVELS IN GROUND WATER SAMPLES (Bq/L) COLLECTED AT THE SITE (top graphic) AND TO THE
SOUTH OF THE SITE (bottom graphic)

Bq/L
160
140
120
100
80
60
40
20
0
Jan-09

May-10

Sep-11

Feb-13Sampling points (piezometers):

F211

Jun-14F215

Nov-15F285

P13Mar-17
P15

Bq/L
140
120
100
80
60
40
20
0
Jan-09

May-10

Sep-11

Feb-13Jun-14

Sampling points (piezometers):

P12

Nov-15Mar-17

P53

© CEA

194

160

Aerial view of the Marcoule site
/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
MARCOULE SITE

Tritium contamination was also detected via
the radiological monitoring of surface water,
particularly at the Codolet lake to the south of thesite. Variation in tritium activity at Codelet lake,as shown in figure 9, matches variation in groundwater measurements (see figure 8). Mean tritium
activity for the lake dropped from 67.5 Bq/L for the
2011-2014 period, to 24.6 Bq/L for the 2015-2017
period.

According to regular analyses, low activity was
detected in Rhône river water, mainly due to theother nuclear facilities in the Rhône valley (NPPdischarges represent a total of approx. 95% oftritium discharges) (see figure 10). Tritium activity
downstream from the site represents 6.3 Bq/L on
average over the 2015-2017 period, but ranges
between 3.1 Bq/L and 11.1 Bq/L.

FIGURE 9 /TRITIUM ACTIVITY MEASURED IN WATER SAMPLES TAKEN FROM CODOLET LAKE TO THE SOUTH OF THE CEA
SITE AT MARCOULE (Bq/L)

Bq/L
180
160
140
120
100
80

195

60
40
20
0
Jan-09

May-10

Sep-11

Feb-13Jun-14

Nov-15Mar-17

FIGURE 10 / TRITIUM ACTIVITY FOR RHÔNE WATER SAMPLES TAKEN UPSTREAM (Bollène municipality) AND
DOWNSTREAM (Beaucaire municipality) FROM THE MARCOULE SITE

Bq/L
16
14
12
10
8
6
4
2
0
Dec-08Jun-10Dec-11

Downstream decisionthresholds

Jun-13

Dec-14

Upstream Rhône riverwater (Bollène)

Jun-16

Jan-17

Downstream Rhône riverwater (Beaucaire)

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Tritium is the only radionuclide detected indrinking water supply for the municipality ofCaderousse. Most measurements are below thedetection threshold, with a peak value of 5.8 Bq/L
reached in 2016.

versus current background radiation levels,
due to site discharges. In terms of food,this additional specific activity corresponds
to an additional activity by mass of around
0.2 Bq/kg fresh for a lettuce or 0.5 Bq/kg freshfor fruit or 0.5 Bq/L for milk. These additional
activity levels by mass cannot be differentiatedfrom background radiation, in theory. On thisbasis, significantly higher measurements acquiredby CEA as part of its monitoring programme,
particularly for fruit, could be due to technicalmeasuring uncertainties.

Carbon-14196

Although atmospheric carbon discharges releasedby the facilities at Marcoule are very minor, activity
levels in the environment due to these discharges
can be differentiated from background radiationlevels if the specific activity is measured as Bq/
kg of carbon. Figure 11 shows specific carbon-14
activity levels, as measured by IRSN since 2009
in various plants, and tree leaves in particular.
Most of these activity measurements exceed
the background radiation range (current mean
background radiation: 227 Bq/kg of C). Due to thedecrease in specific carbon-14 activity throughout
the northern hemisphere, this mean value
for background radiation represented approx.
240 Bq/kg of C in 2009 (see chapter 2).
The mean measurement acquired by IRSN
over the 2015-2017 period reflects an averageincrease of + 8 Bq/kg of C, which is + 3.5%

Carbon-14 activity measured in the aquatic
environment, particularly for fish in the Rhône
river downstream from the Marcoule site, ismainly attributable to discharges from NPPs on
the Rhône river (see chapter on NPPs).
Other radionuclides

In the terrestrial environment, only caesium-137
from fallout from the Chernobyl accident andnuclear tests can be measured at similar levels
to those detected in areas unaffected by anuclear facility, and can therefore be attributed tobackground radiation (see chapter 3.1 pp. 90-91).

FIGURE 11 / SPECIFIC CARBON-14 ACTIVITY MEASURED BY IRSN IN THE TERRESTRIAL ENVIRONMENT OF THE CEA SITE
AT MARCOULE

Bq/kg of carbon
340
320
300
280
260
240
220
200
2009

2010

2011

Specific activities measured

2012

2013

2014

Background radiation range/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

2015

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
MARCOULE SITE

Caesium-137 activity levels in sediment
samples taken downstream from the site arehigher than levels for sediment samples taken
upstream: 15.3 Bq/kg dry compared with 1.2 Bq/
kg dry (figure 12). Sediment contamination isslightly higher at Codolet. Despite this, activity
measurements correspond to backgroundradiation levels (see chapter 2: fallout fromatmospheric testing). In addition, several artificial
radionuclides can also be measured downstream:cobalt-60, strontium-90, americium-241 andplutonium-239+240, to varying degrees.

are occasionally measured in aquatic plants:
particularly caesium-137, cobalt-60, strontium-90,
americium-241 and plutonium-239+240. Table 3
can be used to compare activity levels upstream
and downstream from the site, and demonstrates
that these measurements do not indicate any site
impact at the current time. With caesium-137,
activity levels may indeed be higher downstream,
but remain within the range of variation inbackground radiation from residual fallout.
In terms of fish, with the exception of one
single sample containing quantifiable tracesof caesium-137, no artificial radionuclide was
detected between 2015 and 2017.

Aquatic plant and fish samples are taken in
the Rhône upstream and downstream fromthe site. A few traces of artificial radionuclides

FIGURE 12 / ACTIVITY BY MASS FOR THE MAIN RADIONUCLIDES OF INTEREST IN THE SEDIMENT SAMPLES TAKEN IN THE
RHÔNE RIVER UPSTREAM AND DOWNSTREAM FROM THE CEA SITE AT MARCOULE

Bq/kg dry downstream
1000

197

100
10
1
0.1
0.01
Jan-09

May-10

Caesium-137

Caesium-137 at Codolet

Sep-11

Feb-13Jun-14

Nov-15Mar-17

Americim-241

Plutonium-239+240

Sep-13Jan-16Strontium-90

Bq/kg dry upstream
1000
100
10
1
0.1
0.01
Jan-09Mar-10May-11

Decision thresholds

Jul-12

Americium-241

Nov-14

Caesium-137

Mar-17

Plutonium-239+240

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /TABLE 3 / ACTIVITY MEASURED IN AQUATIC PLANT SAMPLES TAKEN UPSTREAM AND DOWNSTREAM OF THE CEA SITE AT
MARCOULE (Bq/kg fresh)

Min. and max. value upstream fromSaint-Étienne-des-Sorts

Min. and max. value downstream from
CodoletH

0.34 – 0.65

0.38 – 3.43

Cs

0.32 – 0.35

0.17 – 0.22

Co

< DT

0.08

Radionuclide
3

137
60

Sr

0.54

0.15 – 0.30

Am

0.007

0.009 – 0.018

90

241

Pu

238

Pu

239+240

< DT

< DT

0.006 – 0.008

0.010 – 0.065

Conclusions

198

In general, tritium activity levels have decreased
in all environmental components near to the
Marcoule site, due to the substantial reduction indischarges as the Célestin reactors and the Tritium
workshop have been shut down, and this feature
characterises the radiological changes recorded in
the immediate environment of the site over recent
years. Due to this decrease, over the 2015-2017
period, the number of significant measurements(results above the decision threshold) is far
lower than in previous periods (22% for ambient
HTO measurements) and mean values(1) which
could be used to estimate the doses potentiallyreaching local residents cannot be determined.
In the previous Radiological report for the 2011-2014
period, the dose inherent to tritiated discharges
from the facility had been estimated at 0.28
µSv/year; the current value would be far lower.

According to the specific carbon-14 activity
measured by IRSN around the site and theexposure scenarios described in chapter 8 of theappendices, the dose absorbed due to carbon-14
is approx. 0.07 µSv/year.
Discharge levels for other radionuclides are too
low for the inherent activity in the environment tobe detectable. However, in an aquatic environment,
and particularly in sediments, residual activity
from past site discharges is still detectable.

1. Mean values are only calculated if at least 50% of measurements are significant (> DT) (see chapter 8 of the appendices).

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
VALDUC SITE

Valduc site
Discharges and monitoring plans
The Valduc facility is dedicated to technologicalresearch and development for the nuclear
materials required to ensure a dissuasive French
nuclear force. The fast neutron reactor, Rachel,was particularly installed at Valduc in 1957, and led
to the first ever criticality studies in France. Since
this time, specialists at the site also maintain anddecommission nuclear units. The site is located ina rural area, surrounded by forests and farming

land in the municipality of Salives, 45 km to thenorth west of Dijon in the Côte-d’Or department(figure 1). Site facilities mainly discharge gaseous
tritium into the atmosphere. Discharges havedecreased considerably since the 1970's and havereached stable levels since the early years of the
21st century, at around 300 TBq/year (figure 2).
CEA and IRSN have implemented a monitoringplan since the site opened, focusing on thisradionuclide (table 1), to test and estimate theimpact of site discharges on the population andthe environment.

FIGURE 1 / MAP SHOWING THE LOCATIONS OF MONITORING POINTS NEAR TO THE VALDUC SITE

199

Valduc site

Valduc site

CEA and IRSN sampling points (Number)
Atmosphere (22 - 1)
Rainwater (5 - 1)
Surface water (5 - 10)
Spring water (0 - ?)Wheat (0 - 1)
Tree leaves (0 - 3)
Grass (4 - 3)
Milk (1 - 1)
Vegetables (0 -1)
Meat (0 - 1)

Road networks, hydrographics and site boundaries
Departmental road
Permanent river or stream
Seasonal river or stream
Site boundary
Municipal border
Site boundary
Municipal borderLand use
Construction or building
Anthropic surface (Structure)
Anthropic surface (Industry or shops)
ForestRiver, stream or lake
Other(source: RGE-BDTOPO@ & BDCARTO@ by IGN - 2015 ed.)

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 2 / GASEOUS EFFLUENTS CONTAINING TRITIUM DISCHARGED INTO THE ATMOSPHERE FROM THE CEA SITE AT
VALDUC (TBq/year)

TBq/year
100,000

10,0001000

100
1969 1973 1977 1981 1985 1989 1993 1997 2001 2005 2009 2013 2017200

The impact of the Valduc facility on its
immediate environment
Tritium discharges into the immediate environment
around the Valduc site can be detected in allenvironment components, up to a few dozen
kilometres around the site. Ambient tritium issampled on a weekly basis using bubblers at 4
sampling stations located in the 4 municipalities
in the area around the site. Ambient tritium canbe found in two forms: tritiated water vapour(HTO) and gas (HT and other tritiated gaseousorganic compounds), however water vapour isthe dominant form. Figure 3 shows measurement
results, with mean and maximum values for eachsampler given in Table 2. Mean tritiated water
vapour activity measured over the 2015-2017
period for the samplers at Échalot and Salives
represents 0.6 Bq/m3. The highest values aremeasured to the north of the site, particularly inthe municipality of Échalot, where a maximum
value of 4.5 Bq/m3 of tritiated water vapour (HTO)
was reached in July 2017 and 0.9 Bq/m3 of gaseous
tritium (HT) was measured in December 2016.

According to figure 3, while activity levels vary
substantially, the ranges are fairly constant overtime, with similar mean values, matching variationin discharge levels over the last 20 years. Theseambient tritium levels are well above the current
background radiation levels for atmospherictritium in areas unaffected by a nuclear facility, i.e.
approx. 0.01 Bq/m3 of air for tritiated water vapour.
Tritium activity in rainwater can be tracked in thesame municipalities using collectors. The annual
mean figure over the period for the 4 samplers
represents 21.8 Bq/L. Note: just like ambient
activity levels (HTO and HT), the highest activity
levels are recorded at samplers to the north of thesite (table 2). The peak activity reached in rainwater
represented 151 Bq/L at the Échalot sampler on
30 January 2017 (see figure 3). These rainwatermeasurements match the above ambient data.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
VALDUC SITETABLE 1 / MONITORING PLANS FOR THE VALDUC SITE

Environment monitoredor type of testing

CEA

IRSN

Ambient gamma
radiation• 10 passive dosimeters at the edge of the site oron-site: ambient γ dose rate
• 4 passive dosimeters in the immediate
environment of Échalot, Léry, Moloy andSalives: ambient γ dose rate

Atmospheric aerosols• 3 sampling points at Échalot, Moloy and Léry
gross α and β activities (weekly)• 1 sampling point at Salives:gross α and β activities (daily)

Ambient tritium• 4 sampling points at Echalot, Moloy, Léry andSalives: ambient tritium (HTO - HT) (weekly)• 1 sampling point at Salives:ambient tritium (HTO - HT) (weekly)

Rainwater• 4 sampling points at Échalot, Moloy, Léry andSalives: tritium (weekly)• 1 sampling point at the CEA site:
gross α and β activities (monthly)• 1 sampling point at Salives:
tritium (weekly)

Milk• 1 sampling point at Salives (Larçon):tritium, γ spectrometry (monthly)• 1 sampling point at Salives (Larçon): free andorganically-bound tritium (6-monthly)• 2 sampling points to the north-west and southwest of the site: free tritium (quarterly)Grass• 4 sampling points at Échalot, Moloy,
Léry and Salives: tritium (monthly),γ spectrometry (monthly rotation between the
4 points)• 3 sampling points at Échalot, Léry and Salives:
free and organically-bound tritium (annual)

Tree leaves• 5 sampling points at Échalot, Léry, Salives,
Avot and Vernois les Vesvres: free andorganically-bound tritium (annual)

Vegetables• 1 sampling point at Salives (Larçon): free andorganically-bound tritium (annual)Meat• 1 sampling point to the north-west or southwest of the site: organically-bound tritium(annual)Wheat• 1 sample of a departmental mixture:organically-bound tritium, γ spectrometry(annual)Surface water• 9 sampling points at Étalante (2 points),
Léry (2 points), Minot, Moitron, Moloy, Orretand Salives: gross β activity, potassium, tritium(6-monthly)• 1 sampling point at Grand Etang at the CEA
site: gross α and β activities, potassium,
γ spectrometry (6-monthly)

Spring water or outlet• 5 sampling points at Échalot, Moloy, Salives,
Léry and Grand Étang at the CEA site: gross α
and β activities, tritium, γ spectrometry• 8 sampling points at Étalante (2 points),
Le Meix, Minot, Moitron, Moloy, Poiseul-laville-et-Laperrière and Salives: gross β activity,
potassium, tritium (6-monthly)

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /201

TABLE 2 / MEAN AND MAXIMUM TRITIUM ACTIVITY LEVELS IN THE FORM OF WATER VAPOUR (HTO) ESTABLISHED ON
THE BASIS OF SIGNIFICANT AMBIENT MEASUREMENTS OBTAINED ON A WEEKLY BASIS IN THE IMMEDIATEENVIRONMENT OF THE CEA SITE AT VALDUCHTO (Bq/m3)
Mean value

Maximum value

Moloy

-*

1.0

Échalot

0.7

4.5

Léry

-*

0.8

Salives

0.5

2.1* Mean values are only calculated in this radiological report if at least 50% of measurements are significant (above the decision threshold),which is not the case for ambient tritium activity measurements at the Lery and Moloy samplers (see chapter 8 in the appendices).

FIGURE 3 / AMBIENT TRITIUM ACTIVITY LEVELS IN THE FORM OF WATER VAPOUR (HTO) AND AS A GAS(HT and other tritiated gaseous organic compounds) MEASURED IN THE IMMEDIATE ENVIRONMENT OF THE CEA SITE AT
VALDUC ON A WEEKLY BASIS (Bq/m3)

Bq/m 310

HT: gaseous tritium

202
1

0.1

0.01
Dec-12Oct-13Aug-14Jun-15

Decision thresholds

Échalot

Bq/m 310

Apr-16
Salives

Feb-17

Léry

Dec-17

Moloy

HTO: tritated water vapour

1

0.1

0.01
Dec-12

Dec-13

Dec-14

Decision thresholds

Échalot

Dec-15
Salives/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

Dec-16
Léry

Moloy

Dec-17

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
VALDUC SITETABLE 3 /TRITIUM ACTIVITY IN RAINWATER (Bq/L)

Municipality
Salives
Échalot
Léry
Moloy

North
South

Mean value(Bq/L)

Maximum value(Bq/L)

24.9

126.0

28.2

151.0

14.7

45.0

14.2

56.0

Free tritium measurements (free water HTO inplants) are taken from grass samples around the
Valduc site on a monthly basis. Figure 4 highlights
the parallels between activity levels measured inrainwater and those in plants. In fact, HTO activity
levels in plants are representative of tritium
activity levels in the atmosphere over the period
preceding the sample. Variation in these activity
levels is also similar to that recorded for rainwaterand air. The mean value for the 4 samplers overthe 2015-2017 period is also very similar to themean measurement for rainwater: 23.7 Bq/kg of
fresh grass. The peak value during the study period
was measured in the municipality of Échalot:
280 Bq/kg of fresh grass.

FIGURE 4 / TRITIUM ACTIVITY MEASURED IN RAINWATER (Bq/L) AND IN GRASS SAMPLES (Bq of free tritium/kg fresh)
NEAR TO THE CEA SITE AT VALDUC

Bq/L or Bq/kg fresh

203

1000

100

10

1
Sep-08Jan-10May-11

Sep-12
Rainwater

Jan-14Apr-15Aug-16

Dec-17

Grass

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Free tritium activity levels (HTO), based on theanalysis of cow's milk samples taken aroundthe site, vary significantly, in the same way as
rainwater and grass samples. Figure 5 shows theparallels between activity levels measured in grass
and those in milk. Mean tritium activity for milk
over the period in question is equal to 11.7 Bq/L,
with a peak value of 27.2 Bq/L in a sample takenin the municipality of Salives in September 2015.
Activity in milk is very naturally lower (2 to 3 times
lower on average), than activity in grass samples.

This is due to the fact that tritium is primarilytransferred to livestock by eating food and drinking
water, as well as by inhaling and transcutaneously.
The tritium contamination of some cattle foodcomponents (feed or water) can be less than thatof local grass. Figure 6 also confirms that activity
levels are higher to the north of the site. These
tritium activity levels in milk samples collectedin the area around the Valduc site are well above
local background radiation levels, which currently
range between less than 1 Bq/L and 3 Bq/L.

FIGURE 5 / FREE TRITIUM ACTIVITY MEASURED IN MILK (Bq/L) AND GRASS SAMPLES (Bq of free tritium/kg fresh) NEAR
TO THE CEA SITE AT VALDUC

Bq/L or Bq/kg fresh
1000

204

100

10

1
Sep-08Jan-10May-11

Sep-12

Jan-14

Cow's milk

Avr-15Aug-16

Dec-17

Grass

FIGURE 6 / GEOGRAPHIC DISTRIBUTION OF MEAN TRITIUM ACTIVITY IN MILK (Bq/L) IN THE IMMEDIATE ENVIRONMENTOF THE CEA SITE AT VALDUC

Bq/L

N-NW

100

N

N-NE

NW

NE
10

W-NW

W

E-EN

E

1

E-SE

W-SW
SE

SW
S-SW

S

S-SE

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
VALDUC SITE

According to analyses of annual beef samples
taken in the municipalities around the facility,
activity ranges from 1.1 to 9.3 Bq/kg dry of meatin OBT. This activity must be divided by 3 to 4 toobtain the activity in Bq/kg fresh. This activity
range in wheat falls between 2.2 and 8.7 Bq/kg dryof wheat. Finally, according to analyses of honeysamples, tritium activity ranges between 4.2 and11.6 Bq/kg fresh. These activity levels must becompared with background radiation levels fortritium, which are currently between less than 1
and 3 Bq/kg fresh.
Figure 7 shows the results of the analysis of tree
leaves collected at increasing distances between
the Valduc site facility and the municipality ofVernois Les Vesvres. According to these results, atapproximately 20 km from the site, tritium activity
levels can still exceed over 3 times backgroundradiation for this radionuclide, confirming that
tritium discharges from the Valduc facility affectthe terrestrial environment around the site over
several tens of kilometres.

Ground water is monitored by taking samples atthe points where the Coquille, Galopine, Prélard,and Prégelan springs emerge and public supply
points: a public fountain at Minot and at Moloy,
and the washing point at Le Meix (figure 8).
Tritium activities measured range from 2.2 to67.7 Bq/L of water. The highest activity levels were
measured in samples taken at the Prégelan springat Salives and in the municipality of Le Meix withmean values of 53.9 Bq/L and 24.7 Bq/L of water
respectively. Tritium contamination of other water
sources oscillates between the decision threshold(< 5 Bq/L) and 9.3 Bq/L.

205
FIGURE 7 / ORGANICALLY-BOUND TRITIUM ACTIVITY MEASURED IN TREE LEAF SAMPLES (Bq/kg dry of leaves) BETWEEN
2012 AND 2017

Bq/kg dry
1000

100

10

1

0

5

10
15
20
Distance from the CEA site at Valduc (km)25

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 8 / TRITIUM ACTIVITY MEASURED IN GROUND WATER SAMPLES TAKEN FROM NEAR TO THE CEA SITE AT
MARCOULE (Bq/L)

Bq/L
90
80
70
60
50
40
30
20
10
0
Jan-09 Jan-10 Jan-11 Jan-12 Jan-13 Jan-14 Jan-15 Jan-16 Jan-17 Jan-18

206

Decision thresholds

Lavoir spring at Le Meix

Coquille spring

Public fountain at Minot

Public fountain at Moloy

Le Prélard spring at EtalantePrégelan spring at Salives

Galopine spring at Moitron

Two aquifers flow under the Valduc site and feed
several rivers. To the north and west, water ispart of the Seine drainage area; to the south andeast, water is part of the Saône drainage area(see figure 9). According to monitoring results,
tritium activity in the rivers draining the Valducbutte fell substantially during the 1990's andthe first decade of this century, although thedecrease slowed in recent years. This overall trend
matches variation in atmospheric discharges(see figures 10 and 11).

The Noirvau and Douix rivers join the Ignon to thesouth of the site. Mean activity levels measured
in these rivers: 116.1 Bq/L, 23.3 Bq/L and
17.4 Bq/L respectively. The La Tille river flows to
the east, with peak tritium activity of 33.5 Bq/L
and mean activity of 28.6 Bq/L of water. On thisbasis, according to monitoring results for rivers
in the area around the site, tritium contamination
is a general feature, with the exception of theSeine river (to the west of the site) for which allmeasurements were below the decision threshold

Mean activity levels at Grand Étang represent
152.3 Bq/L of water. This lake feeds the Noirvau
stream, which then joins the Douix river, as
shown in figure 9. Douix river water is therefore
less contaminated as Noirvau activity is diluted(see figure 10). On this basis, the maximum activity
levels measured in the Douix and Noirvau rivers
reached 25.8 Bq/L and 138.0 Bq/L respectively.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
VALDUC SITE

FIGURE 9 / MAP OF RIVERS IN THE IMMEDIATE ENVIRONMENT OF THE CEA SITE AT VALDUC AND THE SURFACE WATERMONITORED

Valduc site

207

FIGURE 10 / TRITIUM ACTIVITY MEASURED IN SURFACE WATER SAMPLES TAKEN FROM NEAR TO THE CEA SITE AT
VALDUC (Bq/L) IN THE SEINE DRAINAGE AREA

Bq/L
1000
800
600
400
200
0
Jan-97 Jan-99 Feb-01 Mar-03 Mar-05 Apr-07 Apr-09 May-11 Jun-13 Jun-15 Jul-17
Grand Etang at Valduc

Noirvau stream

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 11 / TRITIUM ACTIVITY MEASURED IN SURFACE WATER SAMPLES TAKEN FROM NEAR TO THE CEA SITE AT
VALDUC (Bq/L) IN THE SAÔNE DRAINAGE AREA

Bq/L
150
125
100
75
50
25
0

Jan-97 Jan-99 Feb-01 Mar-03 Mar-05 Apr-07 Apr-09 May-11 Jun-13 Jun-15

Tille stream

208

Ignon stream

Assessing mean doses based on environmental
measurements
The following types of exposure are consideredwhen calculating the dose: eating food and drinking
water, inhaling and transcutaneous transfer. Meantritium contamination was calculated for all typesof exposure considered. No other radionuclides
were taken into consideration as the impact of the
CEA site at Valduc cannot be detected in analyses
for these radionuclides.
When calculating exposure by inhaling andtranscutaneous transfer, the individual is assumed
to spend all of their time in an atmosphere with themean activity level indicated in table 2 for tritiatedwater vapour (HTO) and gaseous tritium (HT andother tritiated gaseous organic compounds); thisapplies for the two municipalities to the northof the site. The inherent dose is estimated at
0.22 µSv/year at Échalot and 0.14 µSv/year at
Salives.

Jul-17

Douix stream

In the same way as a worst-case assumption
is used when calculating the dose absorbed byinhaling or transcutaneous transfer, the impactof the presence of radionuclides in drinking wateris calculated based on the presence of tritiumin rivers and ground water. The use of springwater with activity of 53.9 Bq/L was assumed
for the municipalities of Salives and Échalot.
The inherent dose is calculated as approx.
0.7 µSv/year for the municipalities of Échalot andSalives.
A basic standard diet was assumed for France asa whole in rural areas for calculations on eating
food grown locally. A dose of approx. 0.15 µSv/
year was obtained for Échalot and 0.10 µSv/year
for residents living in Salives.
The mean total dose for tritiated discharges
from the site for these municipalities is therefore
around 1 μSv/year (see figure 12 for contributions
per type of exposure).

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
VALDUC SITE

FIGURE 12 / ESTIMATED DOSES FOR TRITIUM DISCHARGED INTO THE ATMOSPHERE FROM THE CEA SITE AT VALDUC:CONTRIBUTION TO THE TOTAL EFFECTIVE DOSE

µSv/year
1.2
1.0

0.11
0.15

0.07
0.07
0.10

0.69

0.69

0.11
0.8
0.6
0.4

Dose absorbed transcutaneously
Total dose absorbed by internal exposure for an adult

0.2

Dose absorbed by eating
0

Dose absorbed by drinking water
Échalot

Salives

209

Conclusions© IRSN

According to the results of the measurements
taken in all environmental components in theimmediate environment around the facility, only
tritium contaminates this area up to a distanceof several tens of 10 km. The activity measured
for other radionuclides is insufficient to detect
any contribution from CEA discharges. Tritium
levels in the different environmental components
are stable and generally 10 to 100 times above
background radiation. The potential effective
dose inherent to CEA discharges from Valduc
represents 1.0 μSv/year on average for an adultliving in the immediate environment of the site for
one full year, and eating local food. This estimate
is 1,000 times less than the exposure limit definedfor the public (1 mSv/year).
Taking water samples at the Coquille spring at Étalante

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Cadarache site

Radiological monitoring of the site environment

The CEA facility at Cadarache (see figure 1) was
created on 14 October 1959. This facility wasconstructed in the municipality of Saint-PaulLez-Durance in the Bouches-du-Rhône areaat the point where three other administrative
departments join up (Alpes-de-Haute-Provence,
Var and Vaucluse). This facility is home to a
research centre, experimental fuel design andproduction laboratories and development units
for the associated nuclear technologies.

The operator monitors radioactivity in theatmosphere using continuous measurements(ambient gamma radiation) or deferredmeasurements (atmospheric dust, tritium,
carbon-14, rainwater) via five samplers spread
both inside and outside of the site: Grande Bastide,
Verrerie, Cabri, Ginasservis and Saint-Paul-LezDurance.

Cadarache site operated in 2017:• 21 basic nuclear facilities (INB);• 24 environmentally-classified facilities (ICPE)
excluding INB, including 14 "nuclear" ICPE;• 12 facilities using radioactive substances subject
to authorisation under the French public healthcode; 3 of these facilities are also non-nuclear
ICPE.
210

Radioactive discharges
In addition to the noble gases (krypton, etc.)
discharged by some INB at the facility (Cabri,
Leca-Star, Phébus, etc.), tritium is the mainradionuclide discharged into the atmosphere by
the Cadarache nuclear facility (figure 2).
Since 2014, after conducting radiological tests
for each facility, liquid radioactive effluents fromthe site have been transferred to the Advanced
effluent treatment and management workshop(AGATE). This workshop can be used to reduce thevolume of waste while concentrating radioactivity.
The concentrates are then routed to the Marcoulesite for final treatment and preparation as waste
packages.
If the liquid effluents comply with transfer
standards, they will then join the industrial effluent
network prior to treatment at the purification
station (STEP-EI). These effluents are treated andthen discharged into the Durance river (table 1).
Tritium is the main radionuclide discharged inliquid effluents.

Monthly milk and plant samples are taken in theterrestrial component, under the prevailing winds.
An annual sampling run is also organised for themain farming output and topsoil. Gross alphaand beta activities are also generally measured
in terrestrial samples, and gamma spectrometryis performed. Alpha spectrometry, and tritium,
carbon-14 and strontium-90 measurements
are performed annually, particularly aiming tomeasure transuranic elements, and complement
the above analyses.
Continuous and occasional surface water
samples are taken in the aquatic component,
more specifically in the Durance river, upstream(facility pumping station) and downstream (Pont
Mirabeau sampler) from the Cadarache facility.
Samples are also taken from the discharge pipe
outlet and the village of Saint-Eucher. Tritium andgross alpha and beta activities are measured inwater samples. Alpha and gamma spectrometry
and strontium-90 measurements are occasionallyused to complement these results (particularly
downstream from the discharge point). Sediment,
aquatic plant and fish samples are taken in the
Durance river on an annual basis or more often.
Ground water under the facility is tested on amonthly basis using samples collected via 48
piezometers. Tritium and gross alpha and beta
activities are determined using these samples.
Strontium-90 and actinide activity (alpha
spectrometry) is also determined every 6 months
at some locations.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
CADARACHE SITE

© DR

FIGURE 1 / CADARACHE SITE

211

Road networks, hydrographics and site boundaries
Motorway
Departmental road
Railway
Permanent river or stream
Seasonal river or stream
Site boundary

CEA site at
Cadarache

Municipal borderLand use
Construction or building
Anthropic surface (Structure)
Anthropic surface (Industry or shops)
Vineyards and orchards
ForestRiver, stream or lake
Other(source: RGE-BDTOPO@ & BDCARTO@ by IGN - 2015 ed.)

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /The corresponding measurements for the
sub-surface of the site are not uploaded to the
RNM or used in this report, which exclusively
describes and comments on off-site data.

Punctual analyses carried out at the request of
ASN as part of inspections with environmental
sampling can be added to this monitoring plan.

FIGURE 2 / VARIATION IN LIQUID AND GASEOUS TRITIUM DISCHARGES FROM THE CEA SITE AT CADARACHE SINCE 2004
(GBq/year)

GBq/year
1000

100

10

1
212
0
2004 2005 2006 2007 2008 2009 2010 2011 2012 2013 2014 2015 2016
Gaseous discharges

Liquid discharges

TABLE 1 / OVERVIEW OF LIQUID RADIOACTIVE EFFLUENTS DISCHARGED INTO THE DURANCE RIVER BETWEEN 2009 AND
2016 (GBq/year)
Source: CEA

Parameters

Tritium

Carbon-14

Gross beta
measurement

Gross alphameasurement

Activity discharged in 2009

0.6

0.006

0.26

0.000202

Activity discharged in 2010

23.64

0.008

0.18

0.000208

Activity discharged in 2011

16.4

0.01030.201

0.000446

Activity discharged in 2012

8.1

0.00458

0.28

0.000185

Activity discharged in 2013

2.79

0.002190.29

0.000195

Activity discharged in 2014

0.44

0.00190.32

0.00018

Activity discharged in 2015

0.59

0.00190.23

0.00012

Activity discharged in 2016

0.75

0.002

0.23

0.0002/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
CADARACHE SITE

The impact of the Cadarache site on its
immediate environment
Tritium

Although atmospheric tritium is dominant ingaseous discharges, as a gas (HT) and as water
vapour (HTO), it was only measured on one occasion
between 2014 and 2017 (as HT). The measurement(0.14 Bq/m3) exceeds background radiation for thisradionuclide and reflects the temporary impact ofdischarges from the Cadarache site.
Tritium is also very occasionally (5 times between
2014 and 2017) measured in rainwater collected
near to the site. Measurements vary from 2.4
to 5 Bq/L, and are similar to or slightly above
background radiation, which ranges from lessthan 1 to 3 Bq/L).
Tritium activity levels above the decision thresholdwere only recorded for 6 out of the 350 water
samples taken between 2014 and 2017 in the
Durance river downstream from the Cadarache site
and in the canal upstream from the site (figure 3).

An activity of approx. 4 Bq/L for one single sample,
taken downstream from the site in 2014, revealedtransient and minor contamination from discharges
from the Cadarache site. Note: tritium was notdetected at any time after the decision threshold
was increased from approx. 2.2 to 4 Bq/L early in
2016, in line with the regulatory decision thresholds
established in ASN decision no. 2013-DC-0360 of
16/07/13.
Tritium measurements only exceeded the decisionthreshold for 18 of the 787 ground water samples
taken using 14 piezometers located around the
Cadarache site. The values obtained vary from
2.2 to 34 Bq/L, which is approximately equal tobackground radiation levels for this radionuclide(ranging from less than 1 to 3 Bq/L). Tritium wasmost recently detected in January 2016, before thedecision threshold was increased from approx. 2.2
to 4 Bq/L.
Finally, tritium results in vegetables and milk do
not indicate any contamination by discharges fromthe Cadarache site.
213

FIGURE 3 / DECISION THRESHOLDS AND TRITIUM ACTIVITY BY VOLUME MEASURED IN DURANCE RIVER WATER (upstream
and downstream samples combined) BETWEEN SEPTEMBER 2014 AND DECEMBER 2017 (Bq/L)

Bq/L
6
5
4
3
2
1

Se

p-1
8
No
v-1
8
Jan
-19
Ma
r-1
9
Ma
y-1
9
Jul
-19
Se
p-1
9
No
v-1
9
Jan
-20
Ma
r-2
0
Ma
y-2
0
Jul
-20
Se
p-2
0
No
v-2
0
Jan
-2
Ma 1
r-2
1
Ma
y-2
1
Jul
-21
Se
p-2
1
No
v-2
1

0

Decision thresholds

Measurements

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Carbon-14

Carbon-14 samples are taken using bubblers,
just as for atmospheric tritium. The results
obtained vary from 0.042 to 0.094 Bq/m3, with amean value of approx. 0.06 Bq/m3. All of the dataobtained using these samplers are slightly above
background radiation in France (approx. 0.05 Bq/m3), indicating the very low influence of carbon-14
discharges from the Cadarache site (figure 4).
Carbon-14 activity is also measured in fish from
Durance river, with a mean activity level of 26
Bq/kg fresh for the 2 samples analysed, which issimilar to background radiation levels for these
indicators (around 24 Bq/kg fresh; see chapter 2).
The same applies for aquatic plants, activity
levels cannot be differentiated from backgroundradiation measured at a distance from nuclear
facilities.

FIGURE 4 / AMBIENT CARBON-14 ACTIVITY BY VOLUME NEAR TO THE CADARACHE SITE BETWEEN JANUARY 2009 AND
NOVEMBER 2017 - BUBBLERS AT THE ATMOSPHERIC SAMPLERS AT GINASSERVIS (C1) AND SAINT-PAUL-LEZ-DURANCE(C4) (Bq/m3)

Bq/m 3
0.16
0.14
0.12
0.10
0.08
0.06
0.04
0.02
0

Ja
n
Ma - 0 9y
Se -09pJa 0 9n
Ma -10y
Se -10p-1
Ja 0n
Ma -11ySe -11p-1
Ja 1
n
Ma -12ySe -12p-1
Ja 2
n
Ma -13ySe -13p-1
Ja 3n
Ma -14ySe -14p-1
Ja 4n
Ma -15ySe -15p-1
Ja 5n
Ma -16ySe -16p-1
Ja 6n
Ma -17ySe -17p-1
7214

The carbon-14 activity levels measured in milk
samples are typical of residual atmosphericfallout from nuclear weapons tests. Carbon-14
activity levels measured in 2016 in vegetablesamples taken at Saint-Paul-lez-Durance andGinasservis are above background radiation forthis radionuclide. However, no details are available
as to the matrix sampled and considering thevariation in carbon content of "vegetables andfine herbs" (class used in the RNM database),no conclusion can be reached as to whether thisdifference from background radiation (6 and 16
Bq/kg fresh respectively) is due to CEA discharges
from the Cadarache site. In fact, NPPs discharge
far higher quantities of this radionuclide
comparatively speaking and contaminate theimmediate environment (5 km radius) with approx.
0.3 - 0.7 Bq/kg fresh in fruit and vegetables (seethe corresponding paragraph).

Sampler C1

Sampler C4/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
CADARACHE SITE

Other radionuclides

Traces of 90Sr and 239+240Pu from residual fallout
from older atmospheric contamination aredetected in a Durance river water sample taken
by IRSN downstream from the Cadarache site.
If 137Cs is detected in soils, vegetables ormilk, activity levels are low, and represent
residual activity from old atmospheric fallout.
The same applies for 239+240Pu detected in soils andvegetables.

The annual sediment samples collected by CEA
contain traces of 137Cs and 239+240Pu, at activity
levels similar to those recorded at a distance fromany facility.

© G. Le Sénéchal/CEA

Traces of 134Cs (0.13 Bq/kg) were detected in a
thyme sample in August 2014, at levels below thedecision threshold generally reached (approx. 0.5
Bq/Kg in 2014). 134Cs had already been measured
at this sampler in April 2011, after the Fukushima
Daichi accident. On this basis, these traces of 134Cs
could represent residual contamination from thisevent, although they could also partially comefrom Cadarache discharges. It is important toconsider the high level of uncertainty inherent tothis measurement (76%).

Sediment samples were taken in 2010, 2012 and2013 both at and off the Cadarache site, as partof inspections carried out by IRSN at the requestof ASN. Alpha emitters (238Pu, 239+240Pu and 241Am)
were detected in sediment samples collected in
the Bête ravine, both on- and off-site. The activity
levels measured were 5 to 10 times higher than
mean levels for sediments in France. Isotopic
ratios (238Pu/239+240Pu and 241Am/239+240Pu) confirm
that this contamination differs from residual
atmospheric fallout. ICP-MS measurements
taken to quantify uranium isotopes failed toreveal any anomalous values for activities or 235U
and 238U mass ratios. On the other hand, traces ofartificial 236U were detected, which most probably
indicates that discharges from the Cadarachesite are affecting its immediate environment.
The measurements acquired for Durance riverwater samples collected further downstream (atPertuis bridge) do not indicate any contaminationfrom the site at this distance.

Taking a ground water sample
RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /215

Grenoble sites
The CEA and ILL (Institut Laue-Langevin) researchfacilities are right next to each other and within
the urban sprawl of Grenoble (Isère; see figure 1).
These sites are at the entrance to the Isère valley
between the Vercors massif to the south and theChartreuse to the north.

The facility runs a highly intense source ofneutrons, the high-flux nuclear reactor, INB no. 67.
It also operates 40 high-technology spectrometers
able to provide information on the structure anddynamics of materials (solids, liquids, gases,etc.) in many research fields: particle physics,
nuclear physics, chemistry, biosciences, materials
sciences, etc.

Institut Laue-Langevin (ILL) is an international
research body in neutron science & technology
and was founded in 1967 by France and Germany(and later joined by the United Kingdom in 1973).

The decommissioning works for the CEA facilities in
Grenoble are now complete. The order authorising
the ASN decision on the decommissioning of INB
61 (LAMA) was published on 13 October 2017.

FIGURE 1 / THE ILL SITE AT GRENOBLE

© DR

216

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
GRENOBLE SITESRadioactive discharges
Gaseous discharges from the ILL site aremonitored at 2 outlets, downstream from theeffluent filtration systems. Gaseous discharges are
assigned to 5 radionuclide categories (noble gases,
tritium, carbon-14, iodines and aerosols). Gaseousdischarges are quantified by measuring gases inreal time and by taking representative samples
on a weekly basis. These samples are subjectedto laboratory measurements to determine thespectrum of the gaseous radionuclides.
Tritium is the most frequently detectedradionuclide in gaseous discharges from ILL(see figure 2), followed by noble gases (mainly
argon 41) and carbon-14, for which the activity
levels discharged are 10 times lower. In terms of
halogenated discharges and aerosols, the activity
levels discharged are rarely above the decisionthresholds (approx. a few thousandths of the total
authorised discharge). The CEA facility in Grenoble
ceased discharging gases in July 2013 with thedefinitive shutdown of the ventilation systemfollowing completion of the purification process
for INB 61 (LAMA).
Liquid effluents from ILL are discharged and tested
at the outlet in the Isère river, 1 km upstream
from its confluence with the Drac river. The endof this pipe is in the bed of the Isère river. Liquid
effluents are stored in tanks at the facility before
being discharged into the pipe leading to theoutlet. Discharges are characterised in this tankon the basis of representative samples taken after
mixing the contents. Tritium is the most frequently
detected radionuclide in liquid discharges, withactivity levels approximately 1,000 times higher
than carbon-14 in 2013 and 2,000 times higher
than that attributed to beta/gamma emitter
discharges (see table 2).
No radioactive liquid effluents have beendischarged from the INBs at the CEA facility in
Grenoble since February 2009.

217

FIGURE 2 / VARIATION IN GASEOUS DISCHARGES (NOBLE GASES, TRITIUM AND CARBON-14) FROM THE ILL SITE SINCE 2008

TBq/an
16
14
12
10
8
6
4
2
0

2008

2009

2010
Noble gases

2011

2012

Tritium

2013

2014

2015

Carbone-14

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /TABLE 1 / VARIATION IN GASEOUS DISCHARGES (NOBLE GASES, TRITIUM, CARBON-14) FROM THE ILL SITE SINCE 2008 (TBq)

Noble gas

Tritium

Carbon-14

2008

Year

1.28

13.1

0.68

2009

1.4

12.2

0.76

2010

0.74

7.7

0.46

2011

1.2

13.7

0.41

2012

0.88

11.6

0.45

2013

0.86

12

0.46

2014

0.81

8.3

0.076

2015

1.1

7.2

0.2

TABLE 2 / VARIATION IN LIQUID DISCHARGES (TRITIUM, CARBON-14 AND BETA/GAMMA EMITTERS) FOR THE ILL SINCE
2008 (GBq/year)

Year

218

Tritium

Carbon-14

Beta/gamma emitters

2008

220

0.23

0.0975

2009

32

0.11

0.094

2010

240

0.21

0.096

2011

170

0.27

0.13

2012

370

0.27

0.11

2013

240

0.25

0.11

2014

180

0.22

0.051

2015

430

0.1

0.033

Radiological monitoring of the site environment
The INBs at the CEA facility in Grenoble ceased all
potential effect on the environment in July 2013.
Only the ILL research reactor now contributes
substantial nuclear activity at the scientific site.
With this in mind, Institut Laue Langevin has been
responsible for monitoring the shared immediate
environment of the two sites since 4 January 2010.
Two types of monitoring programmes are run by ILL:
• continuous monitoring, using sampling stations
located at various points in the urban area. Twoto the north, at the foot of the weather station at
the tip of the peninsula, and farther to the northwest, at Rollandière, and two to the south, on theroof of the Chorier-Berriat pool and at Mûrier,above Saint-Martin-d’Hères;• deferred monitoring, based on regular sampling,followed by laboratory analysis. These samples
are taken at the intervals defined in regulations.
ILL takes approximately 2,000 samples eachyear (aerosols, gases, rainwater, ground water,river water (Drac & Isère), food and terrestrial
bio-indicators (milk, grass, farming output) andaquatic bio-indicators (fish, reeds), soils andsediments) (see figure 3). 5,000 analyses are
performed on these samples each year. The aim
is to ensure that the Grenoble environment andthe food chain are not affected radiologically.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
GRENOBLE SITESFIGURE 3 / MAP SHOWING THE LOCATION OF THE MAIN SAMPLING POINTS AROUND THE ILL SITE

Sampling points (Number)
Atmosphere (2)Rainwater (2)Surface water (4)Ground water (13)Grass (2)Milk (1)Road networks, hydrographics and site boundaries
Motorway
National road
Departmental road
Railway
Permanent river or stream
Seasonal river or stream
Site boundary
Municipal borderLand use
Construction or building
Anthropic surface (Structure)
Anthropic surface (Industry or shops)
ForestRiver, stream or lake
Other(source: RGE-BDTOPO@ & BDCARTO@ by IGN - 2015 ed.)

The impact of discharges from the site (ILL
only) on its immediate environment
Tritiated discharges are by far the key factors to
be considered when reporting on the impact of the
ILL research reactor on the environment.
Weekly ambient tritium monitoring is organised
using bubblers set up under the prevailing winds;
to the south-east of the site ("off-site" samplers)
and to the north-west of the site ("pylon" sampler
located at the confluence between the Dracand Isère rivers). Measurements are generally
below the decision threshold (see figure 4).
However, tritium can occasionally be detected
at between 0.5 and 1 Bq/m3. A peak value of 14.3
Bq/m3 was reached in December 2014, but wasnever equalled during the 2015-2017 period,
during which the maximum value was 1.3 Bq/
m3. During the winter, poor weather conditions
limit the dispersal of atmospheric pollutants andconcentrations are likely to increase. The ambient
tritium activity levels are well above backgroundradiation levels (approx. 0.01 Bq/m3) and indicatethat ILL operations have a clear impact.

The results acquired by IRSN since 2014 confirm
the operator's measurements, particularly
the peak value (14.3 Bq/m3) obtained 22 - 29
December 2014. According to the details of the
breakdown between HT gas and tritiated water
vapour (HTO) obtained by IRSN, this peak is mainly
caused by tritiated gas (HT) discharges. Most of
the ambient HTO tritium activity measurements
obtained by IRSN in 2017 were above the decisionthreshold, with a mean value of 0.18 Bq/m3.
This mean figure is below those calculated on thebasis of measurements for the 2011-2014 period.
This decrease is due to the approx. 40% decreasein tritium discharges from ILL.
Tritium can also be detected in rainwater samples
taken from near to the ILL site (see figure 5). Tritium
was detected slightly more frequently in rainwater
samples during the 2015-2017 period, (approx.
50% of the time), with a mean activity level at thenorth-west sampler significantly higher than thevalue for the south-east sampler. The significantly
higher levels recorded at the north-west sampler
are caused by the fact that this sampler is nearer
to the discharge point and under the prevailing

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /219

FIGURE 4 / AMBIENT TRITIUM ACTIVITY BY VOLUME NEAR TO THE ILL FACILITY BETWEEN JANUARY 2010 AND
DECEMBER 2017 (Bq/m3)
ILL and IRSN sites

Bq/m 3
15
14
13
12
11
10
9
8
7
6
5
4
3
2
1
0
Jan-10220

Dec-10Dec-11

Dec-12

Dec-13

Dec-14

Dec-15

Dec-16

Decision threshold
Off-site sampler
Pylon sampler

SSW winds in the ILL area. Over the 2015-2017
period, the maximum activity is approx. 30 Bq/L inrainwater and mean activity is close to 4.4 Bq/L.
This mean activity is approximately 3 times higher
than background radiation levels (approx. 1.3 Bq/L
over the same period) and similar to ambient
activity measurements.

In terms of river water samples, tritium has only
been detected on a very exceptional basis since 2015,(twice in January 2015) in the Isère river, andonly downstream from and immediately next
to the ILL site (see figure 6). The activity levels
measured (3.3 and 3.4 Bq/L) are similar to thosefound in ground water samples collected using thepiezometers installed at the ILL site (see figure 7).
These activity levels are similar to the backgroundradiation range (from less than 1 to 3 Bq/L).

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
GRENOBLE SITESFIGURE 5 / TRITIUM ACTIVITY BY VOLUME IN RAINWATER NEAR TO THE ILL FACILITY BETWEEN JANUARY 2010 AND
DECEMBER 2017 (Bq/L)
ILL and IRSN sites

Bq/L
40

30

20

10

0
Jan-10Jan-11

Jan-12

Dec-12

Dec-13

Dec-14

Dec-15

Dec-16
221

Decision thresholds
North-west sampler
South-east sampler

FIGURE 6 / TRITIUM ACTIVITY BY VOLUME IN THE ISÈRE AND DRAC RIVERS UPSTREAM FROM THE ILL SITE BETWEENJANUARY 2010 AND DECEMBER 2017 (Bq/L)

Bq/L
5
4
3
2
1
0
Jan-10Jan-11

Jan-12

Dec-12

Dec-13

Dec-14

Dec-15

Dec-16

Decision thresholds
Sassenage (Isère, downstream, near to ILL site)
Voreppe (Isère, downstream, at ILL site)

Fountain (Idrac, upstream from ILL site)
La Tronche (Isère, upstream)

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 7 / ACTIVITY BY VOLUME IN GROUND WATER SAMPLES TAKEN USING PIEZOMETERS LOCATED AT OR NEAR TO
THE ILL FACILITY BETWEEN JANUARY 2010 AND DECEMBER 2017 (Bq/L)

Bq/L
12
10
8
6
4
2
0
Jan-10Jan-11

Jan-12

Dec-12

Dec-13

Dec-14

Dec-15

Dec-16

Decision thresholds
222

Piezometers located at ILL site

Piezometers located at CEA site

Monthly grass samples are taken from May to
November. Such samples reliably indicate thecontamination of the terrestrial environment asplants integrate the radionuclides. Tritium wasalmost always detected in this type of matrix overthe 2015-2017 period (see figure 8). Detectionlevels vary from 92% at Grenoble to 82% at SaintMartin-d’Hères. Activity measurements for the
2015-2017 period range from 2 to 50 Bq/kg freshat Grenoble in the municipality of Saint-Martind'Hères. This difference is mainly due to the
distance of the sampling station at Saint-Martind’Hères (around 7.5 km to the south-east of ILL)
compared with the distance of 1 km (to the west)
for the sampling station at Grenoble. As with
ambient activity, the decrease in level comparedwith the 2011-2014 period is probably partially due
to the fact that the CEA site at Grenoble ceased

Piezometers located at CNRS sitedischarging gaseous tritiated effluents in July
2013, and to the decrease (approx. 40%) in tritium
discharges from the ILL site between 2013 and2015. The mean activity level of the grass samples
taken at Grenoble represents 8.1 Bq/kg dry versus
3 Bq/kg at Saint-Martin-d’Hères. This mean value
is mainly higher at Grenoble due to one single
value (53 Bq/kg dry), which is well above the othervalues and was recorded in April 2017. Excluding
this result, tritium activity in grass has remained
at approximately 5 Bq/kg dry for the nearest site
to ILL since 2015.
Milk is also monitored on a monthly basis. Free
tritium is detected in around 15% of milk samples
at levels of between 2 and 5 Bq/L, reflecting
the very low contamination levels in effluentsdischarged from the site.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
GRENOBLE SITESFIGURE 8 / TRITIUM ACTIVITY BY MASS IN GRASS SAMPLES TAKEN AT GRENOBLE AND SAINT-MARTIN-D'HÈRES
BETWEEN JANUARY 2010 AND DECEMBER 2017 (Bq/sec kg before 2015 and Bq/kg fresh since 2015)

Bq/kg dry
250

200

150

100

50

0
Dec-09Dec-10Dec-11

Dec-12

Dec-13

Grenoble

Dec-14

Dec-15

Dec-16

Dec-17Saint-Martin-d’Hères
223

Dosimetric evaluation
According to mean ambient tritium activity
levels measured by IRSN in 2017 (0.18 Bq/m3),
the dose potentially absorbed by inhaling andtranscutaneously by a person living at the locationof the sampler would be approx. 0.05 µSv/year.
Assuming that food grown locally is at equilibriumwith this activity measured in the air, which is highly
conservative due to the short distance to the site,
and assuming local food consumption as describedin chapter 8 of this document, the dose absorbed
by eating local food would be approximately
0.034 µSv/year. Activity levels measured in water do
not differ significantly from background radiationlevels, therefore the dose potentially absorbed
by drinking water is not taken into consideration.
The total dose attributable to tritiated discharges
from the ILL site would therefore reach a maximum
value of approx. 0.084 µSv/year. This evaluationis almost identical to the figure calculated by
ILL based on gaseous discharges from 2017:0.083 µSv/year.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /CEA DAM centre/Île-de-France region
The CEA-DAM site/Île-de-France region is
located in the municipalities of Bruyères-leChâtel and Ollainville in the south of the Essonne
département, in the drainage area for the Orge
river, one of the tributaries on the right bank of
the Seine, upstream from Paris. This researchsite works towards the design of French nuclear
weapons, as well as guaranteeing the operationand safety of these weapons, using simulations.
The site aims to prevent the spread of nuclear
weapons and terrorism, and especially oversees
the application of international treaties.
The nuclear activities of this site were transferredto the Valduc site in 1996.
The site has continued to be purified anddecommissioned since 1997. Tritium is discharged
as part of these operations and is the only
radionuclide which is authorised for discharge

224

from this site. The activity levels discharged havebeen constantly decreasing since 2003, particularly
since 2011 for atmospheric release (see figure 2).
Gaseous discharges are tested using bubblers
installed on two outlets (CH1 and CH2). Tritium isalso detected in liquid effluents discharged fromthe site in both industrial fluids and rainwater. The
tritium content of liquid discharges fell by a factorof 4 between 2007 and 2009. Discharges are now
relatively constant and slightly above 0.5 GBq/
year (see figure 3). The industrial effluents treated
and rainwater are all discharged into Grand Rué
steam, which then flows to the Rémarde stream,
the receiving environment for liquid effluentsdischarged from the INBS.
The atmosphere (precipitation and gases),terrestrial (plants and food) and aquatic(sediments, flora and fauna, river and groundwater) components are covered by environmental
monitoring programmes.

FIGURE 1 / LOCATION OF THE CEA-DAM SITE /ÎLE-DE-FRANCE REGION AND SAMPLING POINTS

Sampling points (Number)Gas (4)
Rainwater (3)Surface water (2)Ground water (3)Grass (2)
CEA-DIF site

Milk (1)Aquatic plants (2)Road networks, hydrographics and site boundaries
National road
Departmental road
Permanent river or stream
Seasonal river or stream
Site boundary
Municipal borderLand use
Construction or building
Anthropic surface (Structure)
Anthropic surface (Industry or shops)
ForestRiver, stream or lake
Other(source: RGE-BDTOPO@ & BDCARTO@ by IGN - 2015 ed.)/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
CEA DAM CENTRE/ÎLE-DE-FRANCE REGION

FIGURE 2 / VARIATION IN GASEOUS TRITIUM DISCHARGES FROM THE CEA-DAM SITE/ÎLE-DE-FRANCE REGION (TBq/year)

TBq/year
110
100
90
80
70
60
50
40
30
20
10
0

2003 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013 2014 2015 2016 2017
TBq/year
0.5
0.45
0.4
0.35
0.3
0.25
0.2
0.15
0.1
0.05
0

225

2011

2012

2013

2014

2015

2016

2017

FIGURE 3 / VARIATION IN LIQUID TRITIUM DISCHARGES FROM THE CEA-DAM SITE/ÎLE-DE-FRANCE REGION (GBq/year)

GBq/year
2.5
2
1.5
1
0.5
0

2003 2004 2005 2006 2007 2008 2009 2010 2011 2012 2013 2014 2015 2016 2017
RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /The impact of gaseous tritium discharges canoccasionally be detected in the atmosphere, as
tritiated gas (HT) and tritiated water vapour (HTO),
thanks to the bubblers set up at the four cardinalpoints around the site (see figure 4) up to 2013 andat the east and west points since that time. Total
tritium was monitored up to October 2013, and then
HT and HTO forms were monitored after this date.
Up to October 2013, according to the few tritium
measurements obtained for both HT and HTO, thecontributions of these two forms were similar.

Ambient tritium concentrations have decreased
since 2009 in parallel with the drop in tritium
discharges. A few values above the decisionthreshold were obtained in 2014. These
measurements were weak (max. 0.4 Bq/m3) but
well above background radiation levels (0.01 Bq/m3)
highlighting the effects of the discharges from the
CEA DAM site/Île-de-Fance region. The decisionthreshold was increased to approximately 50 times
background radiation levels for atmospheric tritiumin January 2015. On this basis, such levels cannot
be detected and analyses do not decisively indicate
if site discharges potentially affect the area.

FIGURE 4 / AMBIENT TRITIUM ACTIVITY BY VOLUME NEAR TO THE CEA-DAM SITE /ÎLE-DE-FRANCE REGION BETWEENJANUARY 2009 AND DECEMBER 2017 – BUBBLERS AT THE NORTH, SOUTH, EAST AND WEST SAMPLING STATIONS - TOTALTRITIUM UP TO OCTOBER 2013 FOLLOWED BY HTO TRITIUM (Bq/m3)

Bq/m 3
1.4
226

1.2
1
0.8
0.6
0.4
0.2
0
Jan-09Jan-10Jan-11

Jan-12

Jan-13

Decision thresholds

Jan-14Jan-15

Measurement/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

Jan-16

Jan-17

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
CEA DAM CENTRE/ÎLE-DE-FRANCE REGION

Tritium can also be detected in rainwater
samples taken from near to the site (see figure 5).
The maximum activity level recorded between
late-2014 and 2017 reached 63 Bq/L versus 208
Bq/L for the period running from 2011 to late2014. The decision threshold was raised from 5
to 10 Bq/L from January 2015, which meant that
tritium was only measured and characterised inrain on 7 occasions. If the same approach had
been applied between July 2011 and 2014, thenumber of significant measurements would havedecreased by approx. 60%. Despite this, as is thecase for atmospheric tritium, levels in precipitation
generally dropped due to reduced discharges.
The CEA's surface water monitoring programme,organised on a monthly basis for lakes and similar,
and on a weekly basis for Grand Rué stream, wasstopped in late-2013. Prior to this time, tritium
levels in Grand Rué stream varied cyclically withhigher values in summer and lower values over the
winter (see figure 6). Such variation was caused bysubstantial differences in flow rate for the GrandRué stream, meaning that dilution was less likely at
the very low water flow reached over the summer.
Once again, the general trend was caused by areduction in discharges, particularly for liquid
effluents. Tritium was detected in Remarde streamon 4 occasions in 2014, with measurements at 6
Bq/L or less. The decision threshold was raised
from 5 to 10 Bq/L from January 2015, whichmeant that any traces of tritium could no longer
be detected in the Rémarde river and the potential
impact of residual liquid discharges in the aquatic
environment could not be determined. Half-yearlyground water samples have also been taken at thesite, and tritium measurements taken upstream(1 point) and hydrogeologically downstream fromthe site (2 points), since 2016.

FIGURE 5 / TRITIUM ACTIVITY BY VOLUME IN RAINWATER NEAR TO THE CEA-DAM SITE / ÎLE-DE-FRANCE REGIONBETWEEN JANUARY 2009 AND DECEMBER 2017 (Bq/L)

Bq/L
250

200

150

100

50

0
Jan-11

Jan-12

Jan-13Jan-14Jan-15

Decision thresholds

Measurement

Jan-16

Jan-17RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /227

FIGURE 6 / TRITIUM ACTIVITY BY VOLUME IN SURFACE WATER SAMPLES TAKEN NEAR TO THE CEA-DAM SITE /ÎLE-DE-FRANCE REGION BETWEEN JANUARY 2009 AND DECEMBER 2017 (Bq/L)

Bq/L
90
80
70
60
50
40
30
20
10
228

0
Dec-08Dec-09Dec-10Dec-11

Dec-12

Dec-13

Dec-14

Dec-15

Dec-16

Dec-17

Decision thresholds
Le Grand Rué

Bassin de Trévoix

Grass sample analysis results are generally below
decision thresholds (only two significant values
were recorded in the period running from late2014 to December 2017, of 8.5 and 9.8 Bq/kg fresh
respectively). Such occasional contaminationreflects atmospheric discharges from the site.
All other measurements taken in the immediate
environment of this site are either naturalradioactivity (40K, 7Be, etc.) or residual fallout fromthe Chernobyl accident or the testing of nuclear
weapons (137Cs).

Arny

La Rémarde

Dosimetric evaluation
According to the radiological monitoring results
for the immediate environment of the CEA site
at Bruyères-le-Châtel, site discharges only
affect tritium levels due to atmospheric release.
However, due to the continuous decrease indischarge levels, combined with the progressive
reduction in residual tritium in the environment,
and increased decision thresholds, tritium levelsin the environment can no longer be quantified
and the dose inherent to the presence of tritium
around the CEA DAM site/Île-de-France region
cannot be evaluated.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
SACLAY SITE

Saclay site

Discharges and monitoring plans

The Saclay site is located in the Essonne
département around twenty kilometres from Paris(see figure 1). The site covers a surface area of
125 ha and is home to eight basic nuclear facilities.
The largest CEA sites: Orphée reactor (neutron
beam reactor), LECI (irradiated fuel researchlaboratory) and the gamma irradiator, Poséidon.
Curium/CIS-Bio international (manufacturer of
products used for medical nuclear applications)and the organic molecule marking laboratory arealso located at the site. The Osiris reactor was
shut down on 16 December 2016.

Figure 2 shows variation in liquid and gaseousdischarges over the 2014-2017 period. The activity
levels of annual gaseous discharges are relatively
constant over time, with the exception of β-γ emitters.
In addition to the noble gases, which dissipate in the
air and have no effect on the other environmental
components, tritium is the main content of both
gaseous and liquid discharges by far.
After treatment, the liquid effluents produced by
the site are routed via the Mineurs aqueduct toÉtang Vieux and then via the overflow to Étang
Neuf. The effluents then join Vauhallan stream, atributary of Bièvre river (see figure 1).
Table 1 shows the radiological monitoring plans
for the environment applicable to the area aroundthe Saclay site and drafted by CEA and IRSN.

229
FIGURE 1 / MAP SHOWING THE LOCATION OF THE SACLAY SITE

Road networks, hydrographics and site boundaries
National road
Departmental road
Railway
CEA-Saclay
site

Permanent river or stream
Seasonal river or stream
Site boundary
Municipal borderLand use
Construction or building
Anthropic surface (Structure)
Anthropic surface (Industry or shops)
ForestRiver, stream or lake
Other(source: RGE-BDTOPO@ & BDCARTO@ by IGN - 2015 ed.)

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 2 / GASEOUS AND LIQUID DISCHARGES FROM THE SACLAY SITE OVER THE 2008-2013 PERIOD (GBq/year)

GBq/year
100,000

Gaseous efﬂuents from INB + ICPE
2014
2015
2016
2017

10,000
1000
100
10
1
0.1
0.01
0.001
0.0001

Noble gases

GBq/year

Tritium

Carbon-14

Iodes

Other β and γ
emitters

Liquid efﬂuents from INB + ICPE

10,000

2014
2015
2016
2017

1000
100
10
1
0.1
0.01
0.001
0.0001

α emitters(gross activity)

Tritium

Carbon-14

Other β and γ
emitters

© CEA

230

Saclay site
/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
SACLAY SITETABLE 1 / MONITORING PLANS FOR THE SACLAY SITE

Environment monitored or typeof testing

CEA

IRSN

Soil air• 6 continuous sampling points;
4 gross α and β measurements–

Ambient gamma radiation• 6 points in the immediate environment +21 points at the perimeter fence• 1 point

Soil air• 4 weekly sampling points;
3
H and 14C measurements• 2 continuous aerosol samplers atflow rates of 7 and 700 m3/h with
1 γ spectrometry analysis per weekRain

• 2 weekly and monthly sampling points;
3
H and gross β measurements• 1 sampling point and a monthly 3H
measurement

The receiving environment for
liquid effluents discharged(water and sediments)• 14 continuous sampling points, weekly tomonthly analyses for 3H, gross α andβ activity, potassium, U, Sr andγ spectrometry• Water: 5 sampling points and a 6-monthly
measurement for: 3H, gross α and β,
potassium, Uiso, Sr and γ spectrometry• Sediments: 1 sampling point and a
6-monthly measurement for Pu, Am, andSr; γ spectrometry• Aquatic flora and fauna: free andorganically-bound 3H, 14C andγ spectrometry

Ground water• 23 monthly to annual sampling points;
3
H and gross α and β measurements• 2 sampling points and 6-monthly
measurements at each point for 3H, gross
α and β activity and potassium

Milk• 2 monthly sampling points; free andorganically-bound 3H, 129I and 90Sr
measurements and γ spectrometry• 1 quarterly sampling point and 1 free 3H,
129
I measurement and γ spectrometry

Plants(fruit, vegetables, grass)• 9 monthly sampling points; γ spectrometry,organically-bound and free tritium and 90Sr

• 6 annual sampling points with free andorganically-bound 3H, 14C andγ spectrometry

Cereals–• 1 annual sampling point and
1 organically-bound 3H measurement andγ spectrometry

The impact of the Saclay site on its immediate
environment and public exposure
Tritium

According to environmental monitoring results,
the area is contaminated by tritium fromdischarges. Tritium activity levels in excess ofnatural background radiation levels or old residual
fallout (see chapter 2), are therefore detected inall environmental components. The air sample
analyses performed at the Saclay, Saint-Aubin,
Villiers-le-Bâcle and Orsigny samplers detect
tritium as water vapour (HTO) and tritium as a gas(HT and organic forms such as CTH3) (see figure 3).
Ambient tritium activity by volume levels for these4 samplers is generally below decision thresholds(≈ 0.12 Bq/m3), but occasionally detected at levels
which are well above the current backgroundradiation levels for atmospheric tritium (approx.
0.01 Bq/m3 of air for tritiated water vapour).
Maximum tritium activity in water vapour between
2014 and 2017 was measured in a sample taken
at Saint-Aubin in 2015: 0.81 Bq/m3 (see figure 3);
the highest value for tritiated gas forms (HT +organic forms) was obtained for a sample from
Orsigny: 1.9 Bq/m3.
In the same way, while most of the tritium activity
measurements for rainwater are below the decisionthreshold, activity measurements occasionally
exceed background radiation levels (1 - 3 Bq/L):
between 4.3 Bq/L and 320 Bq/L (see figure 4).

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /231

FIGURE 3 / TRITIUM ACTIVITY MEASURED IN THE AIR (HTO + TRITIATED GASES) SAMPLES TAKEN AT THE MONITORING
POINTS IN THE IMMEDIATE VICINITY OF THE CEA SITE AT SACLAY (Bq/m3)

Bq/m 3
2.5
2
1.5
1
0.5

Decision thresholds

r-1
4

r-1
5

r-1
6

r-1
7

Ap

Ap

Ap

Ap

r-1
3
Ap

r-1
2
Ap

r-1
1
Ap

Ap

r-1
0

0

Tritiated gases

Tritiated water232
FIGURE 4 /TRITIUM ACTIVITY MEASURED IN RAINWATER SAMPLES COLLECTED AT SAMPLING STATIONS NEAR TO THE
CEA SITE AT SACLAY (Bq/L)

Bq/L
1000

100

10

Ja
nMa 14rMa 14
y-1
Ju 4
l-1
Se 4
p-1
No 4
v-1
Ja 4
n-1
Ma 5
rMa 15
y-1
Ju 5
l-1
Se 5
p-1
No 5
v-1
Ja 5
n-1
Ma 6
rMa 16
y-1
Ju 6
l-1
Se 6
p-1
No 6
Ja v-16
n-2
0
Ma 17
r-1
Ma 7
y-1
Ju 7
l-1
Se 7
p-1
7

1

Decision thresholds

Saclay/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

Saint-Aubin

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
SACLAY SITE

Due to these occasional tritium activity
measurements for both air and rainwater, tritium
activity levels in fruit, grass and milk can also
exceed background radiation levels (from lessthan 1 to 3 Bq/L or Bq/kg fresh; see figure 5).

Discharges from the Saclay site also affect theimmediate aquatic environment Tritium activity in
the Mineurs aqueduct, which transfers effluentsdischarged from the site, varied from 3.3 to 73
Bq/L over the 2015-2017 period, with a mean
activity level of 13.4 Bq/L (see figure 6). The sameis true of lake water samples, where the mean
tritium activity by volume over the same period
reached 10 Bq/L (see figure 7).

FIGURE 5 / FREE TRITIUM ACTIVITY MEASURED IN MILK, GRASS AND FRUIT SAMPLES COLLECTED IN THE IMMEDIATEENVIRONMENT OF THE CEA SITE AT SACLAY

Bq/L or Bq/kg fresh

18
16
14
12
10
8
6

233

4
2

Ju

n-1
4
Au
g-1
4
Oc
t-1
4
De
c-1
4
Fe
b-1
5
Ap
r-1
5
Ju
n-1
5
Au
g-1
5
Oc
t-1
5
De
c-1
5
Fe
b-1
6
Ap
r-1
6
Ju
n-1
6
Au
g-1
6
Oc
t-1
6
De
c-1
6
Fe
b-1
7
Ap
r-1
7
Ju
n-1
7
Au
g-1
7

0

Decision thresholds

Grass

Milk

Fruit

FIGURE 6 /TRITIUM ACTIVITY MEASURED IN WATER ROUTED VIA THE MINEURS AQUEDUCT AT THE ETANG VIEUX (Bq/L)

Bq/L
350

300
250
200
150
100
50

Ju
lOc 11t-1
Ja 1
nAp 12
r-1
Ju 2
lOc 12
tJa 12
n-1
Ap 3
r-1
Ju 3
lOc 13t-1
Ja 3
nAp 14r-1
Ju 4
lOc 14t-1
Ja 4
nAp 15r-1
Ju 5
lOc 15tJa 15
n-1
Ap 6
r-1
Ju 6
lOc 16t-1
Ja 6
nAp 17r-1
Ju 7
lOc 17t-1
70RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 7 / FREE TRITIUM ACTIVITY IN WATER FROM ETANG VIEUX AND ETANG NEUF (Bq/L)

Bq/L
25
20
15
10
5

Ja
n
Ap -09r
Ju - 0 9l
Oc - 0 9t
Ja - 0 9n
A p -10r
Ju -10Oc l-10
Ja t-10n
A p -11r
Ju -11
Oc l-11
Ja t-11n
A p -12r
Ju -12
Oc l-12
Ja t-12n
A p -13r
Ju -13
Oc l-13
Ja t-13n
A p -14r
Ju -14
Oc l-14
Ja t-14n
A p -15r
Ju -15
Oc l-15
Ja t-15n
A p -16r
Ju -16
Oc l-16
Ja t-16n
A p -17r
Ju -17
Oc l-17t-1
70Étang Vieux

Étang Neuf

234

This configuration cannot be identified basedon free tritium levels measured in fish and reedsamples from the lakes, which are similar to orvery slightly above background tritium radiationlevels in the immediate environment (1 - 3 Bq
/L). On the other hand, organically-bound tritium
activity (41 Bq/L) in a fish sample taken in 2017
was above this background radiation as the fish
had incorporated tritium throughout its life.
This measurement reflects both the past andcurrent contributions of tritiated discharges fromthe Saclay site.
In the past, CEA uploaded tritium data for groundwater samples, acquired using piezometers at the
Saclay site, to the RNM database, demonstratingthat ground water contamination reached up
to 60 Bq/L. This data is no longer available.
Despite this, ground water samples taken between
2014 and 2017 off the CEA site have led to tritium
activity levels above background radiation,
for several piezometers. Mean tritium
concentrations represent 13 Bq/L, which isabove the background radiation levels for thisradionuclide in the immediate environment(1 - 3 Bq/L). We also take note that the activity
levels measured in the ground water samples mostaffected by site discharges are constantly falling(the decrease is more substantial in borehole F1than the others; see figure 8).
The dosimetric impact of gaseous and liquid
effluents discharged containing tritium over the
2015-2017 period could only be calculated forindividuals eating local food and drinking local
water. In fact, due to the very high number ofmeasurements below the decision threshold in
the atmosphere, the doses absorbed by inhalingor transcutaneously could not be calculated. The
standard profile assumed is an adult obtaining
100% of their drinking water from a well down
to the Fontainebleau sands ground water, eating
5.3 kg (1) of fish per year from Étang Neuf, andpurchasing local vegetables and meat/eggs/dairy
products. On the basis of the above assumptions,the dose absorbed by this individual would reach
0.15 µSv/year, 99% of which would be due todrinking water. This dose is calculated based on
measurements taken during the 2014-2017 period
and matches the figures estimated by CEA for2016 based on discharges: between 0.11 and 0.22
µSv/year for an adult (tritium represents between
10 and 20% of the total dose received by an adult,
i.e. 1.1 µSv/year, as estimated by CEA in the 2016
report on nuclear safety and transparency).

1. This value is proposed by InVS-Anses and Afssa for the annual consumption of freshwater fish.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
SACLAY SITE

FIGURE 8 / VARIATION IN TRITIUM CONCENTRATION IN GROUND WATER FROM THE SACLAY PLATEAU (Bq/L)

Bq/L
80
70
60
50
40
30
20
10

Jan
A p 10
r-1
Jul 0
Oc 10
t-1
Jan 0
A p 11
r-1
Jul 1
Oc 11
t-1
Jan 1
A p 12
r-1
Jul 2
Oc 12
tJan 12A p 13
r-1
Jul 3
Oc 13
tJan 13A p 14
r-1
Jul 4
Oc 14
t-1
Jan 4
A p 15
r-1
Jul 5
Oc 15
t-1
Jan 5
A p 16
r-1
Jul 6
Oc 16
t-1
Jan 6
A p 17
r-1
Jul 7
Oc 17
t-1
7

0

Decision thresholds

F1

F2

F19

F22

F24

F26

F27

F29

F31

F33
235

Carbon-14

The terrestrial environment around the Saclay
site is little affected by atmospheric discharges ofcarbon-14. Ambient activity was never quantified
prior to 2015. Since that time, CEA has regularly
measured ambient carbon-14, mainly as HTO,
thanks to the lower decision threshold. Activity byvolume in this form represents 0.049 Bq/m3 forthe period studied.
Thanks to these metrological improvements,
carbon-14 can also almost systematically bemeasured in milk, grass and fruit samples(figure 9). While mean activity in milk andfruit samples (18.6 Bq/L and 15.7 Bq/kg fresh
respectively) cannot be differentiated frombackground radiation for carbon-14 (approx. 14 to
15 Bq/L or kg fresh), the same is not true for grass.
In fact, the results obtained vary from 69 to 210 Bq/
kg fresh over the period studied, with a mean valueof 139 Bq/kg fresh, which is over 10 times greaterthan background radiation. This radionuclide wasrarely detected between 2010 and 2015 (for 3 out of
19 measurements), but such observations confirm
that site discharges had already contaminated thiscomponent.

Although annual liquid discharges containing
carbon-14 were also limited, according to the study
completed over the 2011-2014 period, the activity
levels measured in fish samples captured in Étang
Vieux and Étang Neuf were very high. Only two fishsamples were taken between 2014 and 2017, andanalysed in 2017. Mean activity by mass, of 480 Bq/
kg fresh, is similar to that calculated during theprevious period (494 Bq/kg fresh). These results
for this radionuclide can be compared with natural
background radiation in fish, which is approx.
22 Bq/kg fresh. The fish taken (carp and catfish)
live for a long time, which means that carbon-14
activity probably accumulates over several years,
potentially even several decades, of discharges.
Fishing is not authorised in Étang Vieux, which
is classed as a ZNIEFF (2); fishing is, however,authorised in Étang Neuf. If a person eats 5.3 kg/
year (3) of fish captured in Étang Neuf, with a mean
additional activity of 458 Bq/kg, they will absorb
a dose of 1.4 µSv. This mean figure is similar
to that calculated for the previous radiologicalreport for the 2011-2014 period. This figure ishigher than the CEA's estimate in its 2016 reporton nuclear safety and transparency: 0.36 μSv/year
assuming that the person eats 8 kg/fish each year.

2. Area with a natural ecological, flora- or fauna-based interest.
3. This value is proposed by InVS-Anses and Afssa for the annual consumption of freshwater fish.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 9 / CARBON-14 ACTIVITY BY MASS MEASURED IN THE TERRESTRIAL ENVIRONMENT BETWEEN 2015 AND 2017

Bq/kg fresh
250
200
150
100
50

236

Other radionuclides

With the exception of residual caesium-137 fromold fallout, analyses carried out on aerosol filter
samples collected at IRSN's high-flow samplingstation at Orsay generally led to values below
the decision threshold. However, iodine-131
and cobalt-60 were occasionally detected, justlike during the previous period. Iodine-131 wasmeasured on 4 occasions during this period.
The activities measured in January-February
2017 (0.14 and 0.19 µBq/m3), part of this run,correspond to the arrival of masses of air fromthe continent, with higher contamination levels
than usual, probably caused by discharges by
the radiopharmaceutical industry amplified byweather conditions which were not conducive todispersing any type of atmospheric pollutants.

p-1
7

n-1
7

r-1
7

Se

Grass - St-Aubin

This difference is probably due to the fact that CEA
estimates are based on annual discharges, while
the carbon-14 activity levels measured in fish andthe inherent potential doses are accumulated over
several years, or even decades.

Ma

v-1
6
No

g-1
6
Au

y-1
6
Ma

n-1
6
Ja

t-1
5

Grass - Saclay

Ju

Grass - Orsigny

Oc

l-1
5
Ju

Ap

r-1
5

0

Grass - Villiers

Milk

Fruit

The highest activity of 0.24 µBq/m3 was measured
on 17 February 2016 and was a local phenomenon,
possibly attributable to discharges from the
Saclay site, in the same way as the iodine-131
detected in October 2015 (0.16 µBq/m3). The same
assumption can be made for traces of cobalt-60
detected, ranging from 0.03 to 0.3 µBq/m3,
and measured on 7 occasions over the 2015-2017
period, which were very probably released fromthe Saclay site. These values are within the rangeof occasional measurements from the previous
period (2011-2014).
According to analyses of sediment samples takenin the Mineurs aqueduct, caesium-137, cobalt-60,
plutonium, strontium-90 and americium-241 (seefigure 10) are present. Based on the presence of
cobalt-60, the activity levels measured (whichrange from a few becquerel to several dozen oreven hundreds of becquerel for caesium-137)
and the 238Pu/239+240Pu activity ratio, which is 1.6
to 25 times that expected for global atmosphericfallout (approx. 0.03), these activity levels are
generally attributable to past liquid effluentsdischarged from the site. This contamination by
the aforementioned radionuclides is also detectedin lake sediments, however at lower activity levels
and/or less frequently.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
SACLAY SITE

FIGURE 10 / ACTIVITY BY MASS FOR THE MAIN RADIONUCLIDES OF INTEREST IN THE SEDIMENT SAMPLES TAKEN IN THE
MINEURS AQUEDUCT AT ETANG VIEUX (Bq/kg dry)

Bq/kg dry
1000

100

10

1

0.1
Jan-11

May-12

Sep-13

Feb-15Jun-16

Americium-241

Caesium-137

Cobalt-60

Plutonium-238

Plutonium 239+240

Strontium-90

Nov-17237

Finally, out of all of the sediments collected fromrivers downstream from lakes, only caesium-137
can be detected at levels similar to backgroundradiation for this radionuclide.
Traces of caesium-137 and strontium-90 can still
be detected in lake water. If caesium-137 can bedetected, results do not exceed 3.9 mBq/L, while
the mean value for strontium-90 represents
2.3 mBq/L for the period studied. 137Cs levels inreeds reach 2.6 Bq/kg dry on average, comparedwith 0.8 Bq/kg dry for 90Sr. Caesium-137 activity
represents approx. 0.5 Bq/kg fresh in fish analysedin 2017, compared with 0.03 Bq/kg fresh forstrontium-90. These values are detected due topast discharges from the CEA site and global
atmospheric fallout.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Fontenay-aux-Roses site
The Fontenay-aux-Roses site (see figure 1) islocated on the Fontenay-aux-Roses plateau in an
urban area to the south/south-west of Paris (seefigure 2). The basic nuclear facilities at this sitewere definitively shut down in 2007.

The purification programme for nuclear facilities
and laboratories was started in 1999. The nuclear
facilities have been replaced by operations
focusing exclusively on life sciences.

FIGURE 1 / FONTENAY-AUX-ROSES SITE

© CEA

238

© CEA

Aerial view of the Fontenay-aux-Roses site

Piezometer used to take ground water samples/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
FONTENAY-AUX-ROSES SITE

FIGURE 2 / LOCATION OF THE FONTENAY-AUX-ROSES SITE

Road networks, hydrographics and site boundaries
Motorway
National road
Departmental road
Railway

FAR site

Permanent river or stream
Seasonal river or stream
Site boundary
Municipal borderLand use
Construction or building
Anthropic surface (Structure)
Anthropic surface (Industry or shops)
ForestRiver, stream or lake
Other(source: RGE-BDTOPO@ & BDCARTO@ by IGN - 2015 ed.)Radioactive discharges
The aerosols produced at the site are filtered by
two very high efficiency (VHE) filters before being
discharged into the environment. Radioactivity
measuring devices are fitted at outlets for gaseous
effluents. The effluents discharged can containaerosols, noble gases and traces of halogens.
Continuous radioactivity measuring devices areused to monitor gaseous radioactive effluentsfrom INBs. These devices are fitted in stacks,
after VHE filters, and the pre-discharge filters.
These devices determine the activity levels ofbeta-emitting aerosols and radioactive gases inreal time. Real-time test monitors are fitted onnine outlets to monitor the activity levels of betaemitting aerosols, five of which also test alphaemitting aerosols. Four of these monitors are fittedwith a device for the continuous measurement ofradioactive gases.

Measuring results for noble gases based onthese test monitors are all below detection limits.
The total beta "halogen + aerosol" activity
discharged has been less than or equal to0.002 GBq since 2015 (see figure 3).
No liquid effluents from the laboratories of theformer INBs likely to contain radioactive elements
are discharged without prior authorisation. Liquids
containing radioactive substances are collected
in tanks and then routed to a nuclear treatment
centre. All other effluents are collected in buffertanks, and then transferred to the urban seweragesystem after obtaining authorisation and checking
compliance with the applicable regulations(activity by volume, total activity discharged,
chemical conformity of the effluent). Radioactive
test devices are fitted at the test station for
effluents in the urban sewerage system, locatedimmediately downstream from the facility, as well
as a continuous sampling device used to collectsamples which are representative of the effluents.
The devices installed at the outlets, and on theurban sewerage system, run in real time, and an
alarm system is connected to the environmental
control panel at the Fontenay-aux-Roses site.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /239

The radiological monitoring of liquid effluent
transfers covers alpha emitters (total
measurement), beta-gamma emitters (total
measurement) and tritium.
Tritium activities by volume measured in theoutlets used for liquid effluents transferred fromthe site regularly exceed 10 Bq/L, but cannot be
attributed to site discharges (see figure 4). In fact,
similar activity levels are measured in Seine riverwater, which supplies the Fontenay-aux-Roses
facility. These levels are caused by discharges
from the EDF facility at Nogent.

Radiological monitoring of the site environment
CEA provides around 6,000 measurements
annually based on samples taken from allenvironmental components (air, water, soil). The
atmosphere is monitored based on measurements
for four fixed sampling stations (FAR Atmos, FAR
2, Clamart and Bagneux), located at distances ofbetween 0.2 and 2 km around the centre. The air ismonitored, including alpha and beta activity levelmeasurements for dust samples collected using
filters, the identification of halogens on sampling
cartridges, ambient irradiation measurements
and gaseous tritium measurements.

FIGURE 3 / GASEOUS AND LIQUID DISCHARGES FROM THE FACILITIES AT THE FONTENAY-AUX-ROSES SITE OVER THE 20142017 PERIOD

Gaseous effluents

GBq/year
0.01
240
0.001

0.00010.00001

Aerosols

Halogens

Effluent transfers

GBq/year
0.01

0.001

0.00010.00001

α emitters2014

β emitters
2015

2016

2017

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
FONTENAY-AUX-ROSES SITE

FIGURE 4 / TRITIUM ACTIVITY MEASURED IN WATER SAMPLES TAKEN IN THE URBAN SEWERAGE SYSTEM FOR THE
FONTENAY-AUX-ROSES SITE BETWEEN 2010 AND 2017 (Bq/L)
Data: CEA

Bq/L
40
35
30
25
20
15
10
5
Fe
b
Ma -10yAu -10g
No -10v
Fe -10b-1
Ma 1
Au y-11
Nog-11v
Fe -11b-1
Ma 2
yAu -12g
No -12v
Fe -12b-1
Ma 3
yAu -13
Nog-13v
Fe -13b
Ma -14yAu -14g
No -14v
Fe -14b-1
Ma 5
yAu -15g
No -15v
Fe -15b-1
Ma 6
yAu -16g
No -16v
Fe -16b-1
Ma 7
yAu -17
Nog-17v-1
70

Decision thresholds

Radiological monitoring also focuses on water(rainwater, ground water and surface water)using measurements taken in the immediate
environment of the facility. Rainwater samples
collected using rain gauges (2 x 1 m² rain gauges
and 2 rain gauges with a collection area of 0.04 m²)
are used to measure gross alpha and beta activity
and tritium.

Measurements

Sediment, soil and plant samples are taken tomonitor and determine the impact of discharges on
the immediate environment around the Fontenayaux-Roses site (monthly plant samples are taken atfour points located at off-site monitoring stations,annual soil and surface samples are taken at thesite and at the four off-site monitoring stations).

Perched ground water is located at a depth 65
metres above general ground water (see figure 5),
and is monitored on a monthly basis with samples
taken in six bore holes (piezometres) and analysedby laboratories. The perched ground water
emerges at two points: Lavoir fountain and Moulin
fountain at Fontenay-aux-Roses, which are tested
on a monthly basis. Periodic water and sediment
samples are taken from Colbert lake near to thesite for the purposes of monitoring surface water.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /241

FIGURE 5 / SUB-SURFACE CROSS-SECTION OF THE FONTENAY-AUX-ROSES SITE
Source: CEA

CEA site at FAR
Lavoir fountain
Moulin fountain
Fontainebleau sand
Venus fountainTestpiezometer

PERCHED GROUND WATERGROUND WATER

Colbert lake

242

The impact of the Fontenay-aux-Roses site on
its immediate environment
No measurement for the radionuclides targetedin gaseous form in the atmosphere (iodine-131,
tritium), exceeds the decision threshold(0.2 mBq/m3 for iodine-131 and 0.25 Bq/m3
for tritium).
Tritium has only exceeded the decision threshold in
rainwater samples collected near to the site threetimes since September 2014, with a maximum
acitivity level of 7.2 Bq/L.
No artificial radionuclide was detected in ananalysis of Colbert lake water samples. Tritium
has not been detected since October 2014,
despite having been measured at levels above thedetection threshold in the past.

Tritium levels were measured between thedetection threshold (3 - 7 B/L) and 15 Bq/L
(figure 6) in perched ground water samples(points A, B, C, F, G and H) and samples from two
points where springs emerge (Moulin fountain,
Lavoir fountain). These results exceed backgroundradiation in ground water and are attributableto past and current discharges from the
Fontenay-aux-Roses site.
Grass sample results for the terrestrial component
and food chain, for samples taken near to the
Fontenay-aux-Roses site by CEA only indicate
natural radioactivity (40K, 7Be, etc.). No activity
levels were recorded above background radiation
for the artificial radionuclides targeted during thestudy period.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Research sites / 3.4
FONTENAY-AUX-ROSES SITE

FIGURE 6 / TRITIUM ACTIVITY BY VOLUME MEASURED IN GROUND WATER NEAR TO THE FONTENAY-AUX-ROSES SITE
BETWEEN JULY 2011 AND DECEMBER 2016 (Bq/L) AND THE ASSOCIATED DECISION THRESHOLDS (DT)
Data: CEA

Bq/L
25
20
15
10
5

Fe
b
Ma -10yAu -10g-1
No 0v
Fe -10b-1
Ma 1
yAu -11g-1
No 1
v
Fe -11b-1
Ma 2
yAu -12g
No -12v
Fe -12b-1
Ma 3
yAu -13g-1
No 3
v
Fe -13b
Ma -14yAu -14g
No -14v
Fe -14b-1
Ma 5
yAu -15g
No -15v
Fe -15b-1
Ma 6
yAu -16g
No -16v
Fe -16b
Ma -17yAu -17g-1
70

Decision thresholds
Le Moulin
Ground water F

Ground water A
Ground water G

243

Ground water B
Ground water H© F. Jannin/CEA

Le Lavoir
Ground water C

Taking samples using an aerosol filter

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /3.5. NUCLEAR NAVAL BASES

Cherbourg military port

Four of the French Navy's military ports inmainland France are home to nuclear naval bases.
These nuclear facilities are special in that they are
geographically part of large urban areas: Toulon,
Brest and Cherbourg.

The military port at Cherbourg (on the Channel)
hosts the DGA (Direction Générale de l’Armement- Military procurement office), and is mainly
dedicated to constructing or decommissioning
nuclear-powered submarines (attack or missile
versions).

These sites are responsible for hosting andproviding local support for military vessels basedat or transiting through the ports.

In addition, the naval base at Cherbourg can hostnuclear-powered submarines and vessels bothdocked and anchored.

Brest military port and Île-Longue
operational baseToulon military port

As the leading military port on the Atlantic coast,
the military port in Brest (Finistère) is used tomaintain and for stopovers for French military
nuclear-powered vessels such as ballistic missile
submarines (SNLE), attack submarines (SNA), andaircraft carriers.

When at the site, the nuclear steam supply
systems of the submarines and aircraft carriers
are systematically stopped or set to very low
power.

FIGURE 1 / CHERBOURG NAVAL BASE

© Marine nationale

244

An operating base at Île-Longue, to the south of
the Brest naval base, is used to launch ballistic
missile submarines, and represents a strategic
ocean component for the purposes of dissuasion.
All SNLE and the equipment fitting out sixteen
intercontinental missiles are maintained at thissite.

The military port at Toulon (Var) is the main Frenchnaval base, alongside of Brest. 70% of the French
fleet is based here, including six attack submarines(SNA) and the "Charles de Gaulle" aircraft carrier.
These vessels are all nuclear powered.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Nuclear naval bases / 3.5

Radioactive discharges
Radioactive effluents can potentially bedischarged, with authorisation, as part of somenuclear operations carried out in military ports,such as through-life support for nuclear-powered
vessels or major maintenance works on the steam
supply systems of nuclear submarines.
These discharges are mainly likely to contain thefollowing radionuclides: noble gases (krypton,
xenon), tritium, carbon-14 and gamma emitterssuch as caesium-137 and 134 and cobalt-60.

Radiological monitoring of theenvironment

Military ports are also monitored with multiple
regular samples taken in the aquatic environment(sea water, sediments, sand, shellfish, molluscs,
fish, algae). These samples are analysed for grossbeta and tritium activity and subjected to gamma
spectrometry.
Milk and plant (grass, tree leaves) samples aretaken as per the prevailing winds in the terrestrial
environment. Samples of the main farming outputs(fruit, vegetables) are also taken from topsoil.
Gamma spectrometry is performed and tritium
activity is measured in terrestrial samples, andcarbon-14 activity is analysed in plants and milk.

245© Marine nationale

The analysis, monitoring and appraisal
laboratories of the French Navy (LASEM) at
each naval base and IRSN take samples as pera monitoring plan defined based on discharge
properties, the environment and the features ofthe facilities for the purposes of monitoring theradiological profiles of sites.

The atmosphere is monitored at each site with
continuous on-site measurements of ambient
gamma dose rate via the French Navy's nuclear
monitoring system (2SNM) and the IRSN's Téléray
network, and using air and rainwater samples.

Take samples of ocean sediments

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 2 / MONITORING PLAN FOR THE FRENCH NAVY'S SITE AT TOULON (2A) AND IRSN SITE (2B)

2A

French Navy sampling points (Number)
Ambient gamma radiation (13)Aerosols or gas (3)Rainwater (1)Grass (12)Vegetable (2)Tree leaves (12)Sediment (2)Road networks, hydrographics and site boundaries
Motorway
Departmental road
Railway
Permanent river or stream
Seasonal river or stream
Site boundaryLand use
Construction or building
Anthropic surface (Structure)
Mediterranean Sea

Anthropic surface (Industry or shops)
Vineyards and orchards
ForestRiver, stream or lake
Mediterranean Sea

246

Other
(source: RGE-BDTOPO@ & BDCARTO@ by IGN - 2015 ed.)2B

Sampling points (Number)
Ambient gamma radiation (6)Aerosols or gas (1)Sea water (1)Aquatic plants (1)Aquatic fauna (2)Sediment (1)Road networks, hydrographics and site boundaries
Motorway
Departmental road
Railway
Permanent river or stream
Seasonal river or stream
Site boundaryLand use
Construction or building
Anthropic surface (Structure)
Anthropic surface (Industry or shops)
Vineyards and orchards
ForestMediterranean Sea

River, stream or lake
Other(source: RGE-BDTOPO@ & BDCARTO@ by IGN - 2015 ed.)/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Nuclear naval bases / 3.5

TABLE 1 / ENVIRONMENTAL MONITORING PLAN FOR THE TOULON SITE APPLIED BY THE FRENCH NAVY AND IRSN

Environment monitoredor type of testing

French Navy

IRSN

Ambient gamma
radiation• 26 sensors on-site, 3 sensors off-site at• 8 sensors in the immediate environment:
Fort de Six-Fours, Fort de la Croix Faron andBarjols, Hyères, La Farlede, Le Beausset,
Fort du Cap brun: ambient γ dose rate,
Rians, St-Cyr-Sur-Mer, Toulon andincluding 16 sensors able to resist exceptional
Toulon-Arsenal:
events (earthquakes, flooding, etc.) and/or
ambient γ dose rate
14 alpha, beta, and noble gas sensors

Atmospheric aerosols• 3 sampling point at the site:
gross β activity (daily),γ spectrometry if gross β > 2 mBq/m3

Ambient tritium• 1 sampling point at the site:
ambient tritium (HTO - HT) (weekly)

Rainwater• 1 sampling point at the site:
gross α and β activity levels,
tritium (for each event)• 1 sampling point, Tour Royale:
tritium (monthly)

Seawater
Sediments• 1 sampling point at Seyne-sur-Mer:γ spectrometry (weekly)• 2 sampling points at Toulon west –Ollioules and Toulon west – Le Pradet:γ spectrometry (annual)• 1 sampling point, Tour Royale:
γ spectrometry, Pu, Am (annual)

Aquatic fauna• 1 sampling point, Tour Royale: mussels,
γ spectrometry, Pu, Am (annual),
fish, γ spectrometry (annual)

Aquatic plants• 1 sampling point, Tour Royale: algae,
γ spectrometry, Pu, Am, OBT (annual)Grass• 2 sampling points at Toulon west
and Toulon east: γ spectrometry (monthly);carbon-14 (annual) and tritium (distillationwater) (quarterly)

Tree leaves• 2 sampling points at Toulon west andToulon east, 2 – lentisk and cypress species:
γ spectrometry (monthly), carbon-14 (annual)

Vegetables• 2 sampling points, Toulon west
and Toulon east, samples taken for 4
vegetable species (lettuces, tomatoes,
potatoes and courgette) : γ spectrometry(annual), tritium (distillation water) for
lettuces, tomatoes, courgettes (annual) andcarbon-14 (annual) for lettuces

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /247Site impacts on the environment
Weekly tritium samples are taken for both tritiatedhydrogen (HT) and water vapour (HTO) using
bubblers at the 4 sites of the French Navy formeasurements.
The level of atmospheric tritium (HTO and HT)
detected over the 2015-2018 period is similar
to that measured since 2009, although 9.5% of
current activity measurements are above thedecision threshold (between 0.017 and 0.37 Bq/m3),
compared with the previous 6.2%. If we exclude
the 7 unusual values measured at the Toulon sitein March and April 2017, due to the temporarystorage of tritiated plates in a building located nearto the sampling point, activity by volume oscillates
around 0.1 Bq/m3 (between 0.039 and 0.27 Bq/m3).
This range of values is above background radiationlevels in areas unaffected by nuclear facilities(between 0.005 and 0.01 Bq/m3), but will have no
impact on human health.
248

Tritium activity is also analysed in rainwater
samples taken near to these facilities. Activity
levels range between 2.16 and 4.31 Bq/L with
10.5% of data above the decision threshold, which
is similar to results for atmospheric tritium. Mean
activity levels recorded at all sites are similar tothe background radiation range (from less than
1 to 3 Bq/L).

Tritium is also measured in the terrestrial
environment around the Cherbourg base, inplants such as grass and gorse, with 29 out of
the 32 samples analysed exceeding the decisionthreshold. The values obtained vary from 1.16
to 5.74 Bq/fresh kg in plants, with a mean
measurement of 2.3 Bq/fresh kg, which is within
the background radiation range (from less than
1 to 3 Bq/fresh kg).
Background radiation for this radionuclide in
the ocean environment, in areas unaffected byfacilities discharging tritium, is approximately
0.1 - 0.2 Bq/L (see chapter 2).
Activity levels recorded in samples taken in
Cherbourg port, near to the naval base, aremuch higher than these values and in linewith measurements taken in the immediate
environment around the La Hague site (seechapter 3.3 on the La Hague site). They are causedby discharges from this site. Measurements vary
widely between 2.96 and 21.2 Bq/L (see figure 4).
Living organisms, particularly algae, shellfish andfish will integrate the tritium in this environment.
The results obtained for these samples taken by
the French Navy since 2015 range between 2.59
and 8.18 Bq/fresh kg and confirm this transfer.
In the same way, the brackish ground water fromthe Homet zone at Cherbourg is contaminated dueto the tritium contributed from sea water, with amean tritium value of 4.8 Bq/L for the 2015-2017
period and results which fluctuate between 2.72
and 10.58 Bq/L.

FIGURE 3 / AMBIENT TRITIUM (both HT and HTO) ACTIVITY BY VOLUME NEAR TO THE MILITARY PORTS OF THE FRENCH
NAVY BETWEEN 2009 AND 2017 (Bq/m3) - ONLY RESULTS EXCEEDING THE DECISION THRESHOLD ARE SHOWN

Bq/m 3
1
0.8
0.6
0.4
0.2
0
Jan-09Jan-10Jan-11

Jan-12

Jan-13Brest

Cherbourg – OctevilleJan-14Jan-15

Île-Longue/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

Jan-16
ToulonJan-17

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Nuclear naval bases / 3.5

FIGURE 4 / TRITIUM ACTIVITY BY VOLUME FOR SEAWATER SAMPLES TAKEN NEAR TO THE MILITARY PORT
OF CHERBOURG BETWEEN 2009 AND 2017 (Bq/L) – ONLY RESULTS EXCEEDING THE DECISION THRESHOLD ARE SHOWN

Bq/L
25
20
15
10
5
0
Jan-09Jan-10Jan-11

Jan-12

Jan-13Jan-14Jan-15Jan-16

Jan-17Jan-18Cherbourg – Octeville – Querqueville

IRSN very rarely detects tritium in sea water
samples taken from Brest bay despite theadvanced equipment used (see figure 5).
The maximum value recorded of 3.2 Bq/L is within
the background radiation range for tritium.

fish or sediments, for which values fluctuate
between 0.2 and 1 Bq/dry kg and are therefore
within the range of background radiation (0.02 2 Bq/dry kg), or discharges from the La Hague site
for the immediate environment around Cherbourg.

In Toulon bay, 5 results were recorded above thedecision threshold, for 31 samples analysed by
IRSN, between 0.18 and 11.1 Bq/L, mostly well
above the tritium background radiation for themarine environment (see figure 5). The source of
this tritium has not been identified.

The impact of La Hague site is particularly clear
for cobalt-60 and iodine-129 measurements. In
fact, over the 2015-2017 period, cobalt-60 was
repeatedly detected in sea water samples taken in
the immediate environment of the Cherbourg naval
base, especially in algae, shellfish and sediments.
In the same way, iodine-129 is frequently detected
in aquatic fauna samples and systematically inalgae.

Most of the measurements taken in the othercomponents of the marine environment fail toindicate any radiological impact attributable tothe facilities of the French Navy. The radionuclides
measured are either historical residual fallout(see chapter 2), such as caesium-137 in algae,

These data match those recorded over the entire
coast of Normandy on either side of the La Haguesite (see chapter 3.3; La Hague site).

TABLE 2 / COBALT-60 AND IODINE-129 ACTIVITY LEVELS MEASURED IN THE OCEAN ENVIRONMENT IN AND NEAR TO
CHERBOURG PORT

Alga
(fucus)Aquatic fauna(spider crabs)

Sediments

Cobalt-60

0.31 - 0.86 Bq/dry kg
9/14

0.06 - 0.19 Bq/fresh kg
5/5

0.22-6.86 Bq/dry kg
43/150Iodine-129

14 - 46.7 Bq/dry kg
18/18

0.06 - 0.64 Bq/fresh kg
7/13-

2015-2017 period

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /249

FIGURE 5 / TOTAL TRITIUM ACTIVITY BY VOLUME FOR SEAWATER SAMPLES TAKEN NEAR TO THE MILITARY PORTS OF
THE FRENCH NAVY BETWEEN 2009 AND 2017 (Bq/L)
IRSN data

Bq/L
20
18
16
14
12
10
8
6
4
2
0
Jan-09Brest - Anse du Fret

Jan-10Jan-11

Jan-12

Jan-13Jan-14Significant values

250

Bq/L
20
18
16
14
12
10
8
6
4
2
0
Jan-09Jan-16

Jan-17Jan-18Jan-17Jan-18Jan-17Jan-18

Decision thresholds (DT)
Cherbourg bay

Jan-10Jan-11

Jan-12

Jan-13Jan-14Significant values
Bq/L
20
18
16
14
12
10
8
6
4
2
0
Jan-09Jan-15Jan-15Jan-16

Decision thresholds (DT)Toulon bay

Jan-10Jan-11

Jan-12Significant values

Jan-13Jan-14Jan-15Jan-16

Decision thresholds (DT)/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Nuclear naval bases / 3.5

According to the data acquired for plutonium
isotopes between 2015 and 2017 and measured
in sand and ocean sediment samples in theimmediate environment around the military portof Cherbourg, the 238Pu/239+240Pu ratio is greaterthan 0.2 (0.27 - 0.63), which indicates an industrial
source (see chapter 2).

Caesium-137 has been systematically detectedin the 16 soil samples taken near to Brest bay
since 2015, with wide-ranging values, including
some above background radiation levels (0.20- 29.56 Bq/dry kg). A special programme has
been launched to identify the causes of these
phenomena.

Finally, measurements for terrestrial sample
results (cow's milk, grass, vegetables, fruit, tree
leaves) taken near to the French Navy's militaryports are generally below decision thresholds.
The only values measured in the terrestrial
environment around these sites are either naturalradioactivity (40K, 7Be, etc.) or residual fallout fromthe Chernobyl accident or the testing of nuclear
weapons (for Caesium-137).

FIGURE 6 / GAMMA SPECTROMETRY MEASUREMENTS BY LASEM AT BREST© Marine nationale

251

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FOCUS ARTICLE
PLANNED RENOVATION OF THE FRENCH
NAVY'S NUCLEAR MONITORING SYSTEMThe French Navy has redesigned its radioactivity
monitoring system since 2015. The new version(2SNM V2) can both regularly monitor theenvironment and track and forecast discharges incase of an accident. This system will becommissioned in 2018 at the military base in Toulon, followed by the Île-Longue, Brest andCherbourg sites by late-2019.

FIGURE A / MAP SHOWING THE LOCATIONS OF 2SNM V2 MONITORING SENSORS AT THE TOULONNAVAL BASE
Map by the French Navy

town centre
Sampling point (Quantity)
Aerosol/gas sensors (14)Gamma dose rate sensor (10)INES-PN gamma dose rate sensor (16)Naval base

Weather stations (2)Sodar (1)252Road networks, hydrographics and site boundaries
Motorway
Departmental road

Military port

INES-PN gamma sensor

Permanent river or stream
Seasonal river or stream
Site boundaryLand use
Constructions and buildings
Anthropic surface (Structure)
Anthropic surface (Industry or shops)
Tree-planted areas and sports fields
River, stream or lake
Mediterranean sea
Other(source: RGE-BDTOPO@ & BDCARTO@ by IGN - 2015 ed.)Aerosol and gas
measuring system

This system comprises 26 ambient gamma dose rate sensors at the Toulon site. 15 of these sensors
are also equipped with earthquake-resistant solar panels (INES-PN) placed in an area away fromflooding risks. Hard wired communications are reinforced with radio transmissions. 14 sensors
able to measure the activity by volume of gases and aerosols are also fitted. The network iscompleted with two weather stations and a SODAR, providing indispensable information in viewof data analysis.
●●●/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DATA FOR THE DIFFERENT NUCLEAR SITES IN FRANCE / 03
Nuclear naval bases / 3.5

Data are collected using a centralisation system, which is also used to manage and supervise
radiological alarms. This data is forwarded to the decision-making help and information system(SIAD) If an alarm is activated, this application can be used to model the plume and calculate
doses every 15 minutes, particularly based on terrain effects and meteorology, as well as forecast
variation over various time intervals.

FIGURE B / DECISION-MAKING HELP AND INFORMATION SYSTEM

253

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Landscape of the flooded open-pit mine at Jaladis© L. Zylberman/Graphix-Images/IRSN

254/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

O4
FORMERMINING SITES
4.1. INTRODUCTION. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 256
General information on mining sites . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 257
4.2. P OTENTIAL INFLUENCE OF FORMER MINING SITESON THEIR ENVIRONMENT AND PUBLIC EXPOSURE . . . . . . . . . . . . . . . . . 260
 ONITORING THE ENVIRONMENT
4.3. M
AROUND FORMER MINING SITES . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 260
Regulatory aspects. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 260
General description of monitoring mechanisms . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 261
4.4. D ETAILED PRESENTATION OF 4 FORMER MINING SITESCHOSEN FOR THE RADIOLOGICAL REPORT. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 261
L'Écarpière site. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 263
Le Bosc site . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 273
La Commanderie site . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 285
La Porte site . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 293

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /

255

O4

FORMER MINING SITES

4.1. INTRODUCTION
An exhaustive survey of all former exploration,mining and processing sites for uranium ore
was undertaken by IRSN as part of a programme
entitled MIMAUSA (Mémoire et impact des minesd’uranium : synthèse et archives - Inventory
and impact of uranium mines: summary andarchives) at the request of the French Ministryof Ecology. All the available data is accessible
via a cartographic interface on the IRSN website(https://mimausabdd.irsn.fr/).

Currently, the MIMAUSA database covers 250
mining sites spread over 27 French departments(cf. figure 1). These 250 sites differ widely in termsof their size (from several hundred square metresto several hectares), the mining activities that werepractised there (simple reconnaissance work to
the presence of an ore treatment plant, etc.) or
the quantities of uranium produced by the mining
activity (from 20 kg to more than 14,000 tonnes
for the Le Bosc site in the Hérault department,
cf. figure 2). The former mining sites therefore
today present widely differing characteristics
and challenges, not only in terms of the mining
work and industrial activities practised on the

FIGURE 1 / LOCATION OF FORMER URANIUM MINES AND URANIUM ORE PROCESSING TAILINGS REPOSITORIES IN FRANCE

256

From MIMAUSA data

Mining sites

Storage of mining residues/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

FORMER MINING SITES / 04
Introduction / 4.1

sites, but also with respect to the redevelopments
conducted after their closure, their environment
and the use made of this environment.
This chapter of the Radiological report firstof all presents general information about theformer French uranium mining sites. It provides
information about the types of mining operation,
the industrial activities practised on the sites,
the by-products generated and the managementof these by-products, and the different types ofredevelopment. Next, the report presents thevarious potential influences that a mining site
can have on its environment, and the monitoringthat can be done to characterise this influence andthe potential exposure of the local population that
may result from this. Lastly, to illustrate thesegeneral factors, four sites were selected for a
detailed presentation.

General information on mining sites
Industrial mining of uranium in France began
after World War II and ceased in 2001 with theclosure of the country's last working mine. The
CEA (French Atomic Energy Commission, as was)
was the first to prospect for and mine uranium.
These operations were pursued by its subsidiary,
COGEMA (Compagnie générale des matières
nucléaires) from 1976, and by several small
private companies. Progressively, COGEMA, then
Areva and, currently, Orano, assumed operator
responsibility for most of the former mining
sites. Only a few, operated by companies that havedisappeared without being previously taken over,today directly depend on the French State.

FIGURE 2 / GEOGRAPHIC DISTRIBUTION OF FRENCH URANIUM PRODUCTION
From MIMAUSA data

257

Uranium produced (tonnes)< 100

100 to 1000

1000 to 5000

5000 to 10,000> 10,000

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /The former mines are mainly distributed acrossgranitic massifs such as the Massif Central or
the Massif Armoricain. These formations arenaturally rich in uranium, with the highest local
concentrations. Uranium is in fact present innature in many minerals (such as pitchblende,coffinite or autunite). Rock containing theseminerals in sufficiently abundant proportions
to justify mining operations is then qualified
as ore. Prior to full-scale mining, small-scalereconnaissance work could be carried out toestimate the feasibility of a mining operation. This
work could consist in excavating trenches or small
shafts linked to the surface via a pit. In France, theore was then extracted via two mining methods:• open-pit mining;• underground mining.

258

Uranium mining and the processing of uraniumores led to the generation of two types ofby-product: tailings and processing residues.
Indeed, accessing the ore required, in somecases, excavation of rocks with uranium content
too low for the industrial exploitation of thegeological formation. These rocks are designated"tailings" (cf. table 1). Two types of tailings may be
distinguished:• Waste rock tailings corresponding to the countryrock surrounding the granitic or sedimentarydeposits that have been extracted to accessthe deposits. This waste rock has low uranium
content, in the order of several g/t.

• Uranium deposit tailings which correspondto the materials from the deposit whose
uranium content has been judged insufficient,and below the "cut-off threshold", forconsideration as marketable ore. The cutoff threshold value changed over time inline with changes to the price of uranium
and the development of mining techniques.
At the start of the 1990s, with the collapse of theuranium price, the cut-off threshold went from100 to 400 g/t for open-pit mines and from 200
to 400 g/t for underground mines (higher costs).
When the mines were running, these tailings
were disposed of in waste piles or used for theredevelopment of the mining sites.
Once separated from the rock, the ore was groundthen treated chemically to extract the uranium
from it. The corresponding industrial operations
were conducted either in-plant (processing by
dynamic leaching) or in piles on managed areas
on the mining site (processing by static leaching).
There were eight ore extraction plants distributed
over the various mining sites and which processed
the rich ores of neighbouring mines. Oreconsidered as poor was placed in hermetic areas
where it was watered with water and sulphuricacid to extract the uranium by solubilisation(static processing). After the processing steps,
two products were recovered:• the uranium in the form of yellow concentratecalled "yellowcake", used in the preparation offuel for nuclear reactors;• the processing residues.

TABLE 1 / ORDERS OF MAGNITUDE OF URANIUM CONTENT AND RADIOACTIVITY LEVELS TRADITIONALLY ASSOCIATED WITH
MATERIALS AND RESIDUES PRESENT ON MINING SITESUranium content (g/t)

U-238 activity (Bq/kg)

Ra-226 activity (Bq/kg)

Average for soils
Several g/t
and rocks in France*

Several dozen

Several dozen

Granitic rock**

Several dozen g/t

Several hundred

Several hundred

Tailings

Several dozen to
several hundred g/t

Several hundred toseveral thousand

Several hundred toseveral thousand

Residues

Several dozen to
several hundred g/t

Several hundred toseveral thousand

Several tens of thousands

Ores

Around 1000 g/t

Several tens of thousands

Several tens of thousands* Average values observed for soils and rocks in France, whatever the geological context concerned.
** Excluding ore.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

FORMER MINING SITES / 04
Introduction / 4.1

The ore processing residues were stored asthey were produced close to the ore processing
activities in open-pit mines, in ponds surroundedby dikes or in valley bottoms enclosed by dikes.
These dikes consisted of waste rock, static
processing residues and/or cyclone sand fromdynamic processing.
A little over 48 million tonnes of ore was extracted
from French mines. After processing, around76,000 tonnes of uranium were produced overhalf a century and 48 million tonnes of uraniumore processing residue were stored in 16 tailings
repositories distributed around 15 former mining
sites and on a tailings repository at Gueugnon(which hosted an ore processing plant with nomining operation) (cf. figure 2).
Once mining operations ceased, the mine works
were made safe to prevent mine-related risks(in particular, ground subsidence) and the sites
were redeveloped so as to reduce their impact
on man and the environment and integrate theminto the landscape (cf. figure 3). Access to theshafts were blocked off, the pits sealed and theunderground mine works flooded and, in certain
cases, backfilled. Open-pit mines not used as a
receptacle for processing residues were either
flooded, thus creating artificial lakes, or backfilledwith tailings. Lastly, the land was re-shapedusing waste piles to mitigate the topographicalmodifications generated by the mining operationand to limit run-off. Nowadays, the traces of pastmining activity are limited visually to a moreor less marked modification of the topography(hollows associated with old open-pit mines,
mounds consisting of mining waste deposits, etc.).
The old plants were dismantled and a multi-layer

covering, generally consisting of static leaching
residues, tailings and soil was laid over the mining
residue tailings repositories. This coverage
provides physical and radiological protection bylimiting the emission of gamma radiation andthe release of radon directly above the tailings
repository. It should be noted that there is a
tailings repository for which the protection fromgamma radiation is provided by a layer of water
covering the residues. This is the site of Les Bois
Noirs Limouzat. The tailings repository at La
Commanderie is also under a layer of water, but
unlike Les Bois Noirs Limouzat it also has a solid
multi-layer covering.
The operations and plant dismantling waste wasalso stored with the residues. Furthermore,certain tailings repositories may periodicallyreceive sludge from the wastewater treatment
plants located on some old uranium mining sites,
subject to prefectural authorisation.
Some of the land concerned by mining explorationand operation was surrendered to private
individuals, municipal authorities or companies,
while some of it remained the property of Orano.
This meant that land directly concerned by themining activity (in particular waste deposit zones
and open-pit mines) were returned to theirinitial usages or assigned new usages such as
agricultural, forestry or recreational use (fishing,country walks, etc.). Orano retains responsibility
for as long as the sites have not been subject tolegitimate administrative closure, whether or not
it owns the land.

FIGURE 3 / OPEN-PIT MINE ON THE BELLEZANE SITE (Haute-Vienne) BEFORE AND AFTER REDEVELOPMENTSource: Orano

Bellezane open-pit mine during operation.

Bellezane open-pit mine after redevelopment.
RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /259

4.2. POTENTIAL INFLUENCE OFFORMER MINING SITES ON THEIRENVIRONMENT AND PUBLICEXPOSURE
Around a mining site the public may be exposed:• to gamma radiation (external exposure)produced by the various sources that may bepresent on the mining site (tailings, residues).
This gamma radiation may have an influence on
the site itself or on its immediate environment,
leading to a modification of the external dose
received by persons likely to frequent its locality;• to radon, an isotope of the decay series ofuranium-238, naturally present in granitic
massifs and therefore in the materials from themine (tailings, residues);260• to airborne particles from the radioactive materials
present on the site. However, the redeveloped sites
are not theoretically likely to generate significant
dust emissions on account of the landscaping
carried out (presence of plant cover, etc.) and,in the absence of any changes (e.g., worksite
projects), the release of airborne particles on andaround a mining site is generally negligible;• to radionuclides present in the food chain or
drinking water. Indeed, mine water run-off or
rainwater run-off on the mining site can affect thenatural radionuclide content of waterways, lakes
and pools situated downstream of the site, and of
sediments. Food is therefore mainly likely to be
impacted by the irrigation or livestock watering
usages with water affected by a mining site.

Furthermore, to limit the impact on the food chain
and water supply, water from certain mining sites
and tailings repositories undergoes treatment
before being discharged into the environment.
There are currently fifteen water treatment plants
in operation. The treatment may concern theradiological parameters, in particular the uranium
content and/or radium-226 activity, as well as
physical-chemical parameters such as the pH or,in certain cases, the metals content.
Conducting an impact analysis on the population
makes it possible to check that the influence ofthe sites on their environment remains limited.
Exposure is therefore assessed according to the
spread of the population on and around the site and,above all, according to the usage that the population
makes of this environment: frequentation oflocations in close proximity to the site or on thesite, recreational fishing in the waterways or in theold open-pit mines, use of water for irrigating crops
or watering livestock, etc.
Inasmuch as the mining sites are situated on
territory that is naturally rich in uranium, theimpact attributable to a given site is assessed by
the difference between the results of monitoringaround the site and the measurements made atreference stations or reference points beyond theinfluence of the site.

4.3. MONITORING THE
ENVIRONMENT AROUNDFORMER MINING SITES
Monitoring should make it possible on the one handto assess the radiological impact of mining sites
on population and environment and, on the other,to check the efficiency of the redevelopments.
This is why the monitoring around former mining
sites relates to uranium-238 and its progeny, andmay concern the various compartments of theenvironment: air, surface and/or undergroundwater, soils, sediments and foodstuffs.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

FORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4

Regulatory aspects
Tailings repositories are "Installations Classified
for the Protection of the Environment" (ICPE)
and are subject to environmental monitoring.
Certain former mining sites, which are still
governed by the Police des Mines, are also
subject to environmental monitoring by Orano.
The monitoring may be regulatory and/or involve
complementary monitoring initiated by theoperator. How regulatory monitoring is conducted
is defined on a case-by-case basis in prefecturalorders, generally on the basis of the provisions laidout in the "general regulations for the extractive
industries" (RGIE). A distinction is to be madebetween:• prefectural orders regulating site discharges
and defining the monitoring required forassessing the impact of these discharges on theenvironment;• prefectural orders determining the provisions
applicable to certain environments subject to the
influence of mining when these environments
are used for sensitive purposes: swimming,fishing, drinking water supply.
In addition to the monitoring conducted by Orano,
checks are carried out by the DREAL (Directions
régionales de l’environnement, de l’aménagement
et du logement - Regional Departments for theEnvironment, Development and Housing), in
particular involving inspections with sampling
for analysis. Spot measurement campaigns
are also conducted by several bodies. These
campaigns may result from questions arisingfrom the population, elected representatives,
local or national associations, or in response toa request from the authorities. IRSN can provide
technical support to the DREAL or in response to
any request from the authorities. Furthermore, aspart of its specific national radiological monitoring
mission, IRSN also conducts regular monitoringof the local environment around some former
mining sites. In addition, IRSN conducts widerscale studies of the impact of former uranium
mining sites on the regional scale. For example,
the Institute conducted, from 2011 to 2015, a
radiological study to characterise the influence ofthe former mining sites of the drainage basin of the
Dordogne (1).

General description of monitoringmechanisms
Radiological monitoring conducted around certain
former mining sites is designed to characterise asite's radiological impact on the environment, andin particular to quantify the possible changes withrespect to the local natural background radiation,and to estimate the potential exposure of the
population resulting from this:• Monitoring air quality: this consists in tracking
the potential alpha energy concentration(PAEC) due to short-lived daughter isotopes ofradon-222 and radon-220 (cf. chapitre 1, p. 12)
and the activity per unit volume of long-lived
alpha emitters contained in dust.
• Monitoring the dose rate: this is done using
sensors positioned permanently on the site, in its
immediate environment and in the surrounding
inhabited areas (cf. chapter 1, pp. 9-10 andchapter 2, pp. 50-52).
• Monitoring surface water: this essentiallyinvolves measurements of uranium andradium-226 made in the water and sedimentsof the waterways system around the sites.
• Monitoring the food chain: this monitoring
concerns various foodstuffs (vegetables, fruit,
milk, fish, etc.) that are likely to be impacted
by the site via irrigation or the watering of
livestock. Based on these measurements, Oranomakes assessments of the doses that would bereceived by people in the general public who may
consume them.

4.4. DETAILED PRESENTATION
OF 4 FORMER MINING SITESCHOSEN FOR THE RADIOLOGICALREPORT
Considering the large number of sites, the choice
was made to present monitoring conducted onlyaround four former mining sites: L'Écarpière,
La Commanderie, Le Bosc and La Porte(cf. figure 4). These sites were selected according
to various criteria. The first criterion is theexistence of a regulatory monitoring obligation

1. IRSN, 2016, Mining radiological report for the drainage basin of the Dordogne based on a pluralistic approach conducted with stakeholders in
the territory.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /261

making it possible to have access to a set ofmeasurements over several years, such as is
the case with the other facilities presented inthis report. Some 30 sites are concerned bysuch a regulatory monitoring obligation, which
include sites containing a tailings repository.
Furthermore, concerning the latter, the choice
was made to present as a priority the sites forwhich regulatory monitoring of the food chain iscarried out. Hence, the sites of L'Écarpière and
Le Bosc were chosen because, in addition to theaforementioned criteria, these sites played host to
significant mining activity and an ore processing
plant, and both have a working water treatment
plant. Moreover, these two sites make it possible
to illustrate two different geological contexts:
granitic for L'Écarpière and sedimentary for
Le Bosc. The choice of the La Commanderie site
may be explained by the fact that this is a sitewhich has a tailings repository but did not hosta plant (only static ore processing). This site waschosen as it illustrates the use of mining water forcrop irrigation. To illustrate the variability of site
types, it was also decided to include the La Portesite, which is not a tailings repository but a flooded
former open-pit mine.
It is important to note that these sites illustrate
situations specific to them (in particular in terms
of usages) and should not, as such, be taken as
representative of all situations existing in France.

FIGURE 4 / LOCATION OF THE L'ÉCARPIÈRE, LA COMMANDERIE, LA PORTE AND LE BOSC SITES

262

L’Écarpière
La Commanderie

La Porte

Le Bosc/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

FORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4
L'ÉCARPIÈRE SITE

L'Écarpière site

Monitoring plan

The L’Écarpière site is located in the municipalities
of Gétigné (Loire-Atlantique) and Saint-Crespinsur-Moine (Maine-et-Loire), along the Moine river.
Covering an area of 240 ha, this site was operated
from 1952 to 1990, with underground mine works
and four open-pit mines, producing 4109 tonnesof uranium (cf. table 1). An ore processing plant,
which processed most of the ore in the region, wasalso in operation from 1956 to 1991 (cf. table 1).
This plant was dismantled and the entire site
was redeveloped (cf. figure 1). Currently, thesite has a tailings repository containing dynamic
and static processing residues from uraniumore (cf. table 1), a water treatment plant andthe operator's offices. Part of the site has been
upgraded with the installation of a solar park.

The L’Écarpière site is subject to regulatory
monitoring prescribed by prefectural order.
The Orano monitoring plan is presented below(cf. table 2 and figure 2), involving the monitoringof the following:• site water (from the old mining works zone:
run-off water, water from mining work, drainage
water from the tailings repository);• gamma radiation on and around the site;• air quality on and around the site (radon anddust);• the aquatic environment around the site(the Moine river);• the food chain around the site;• underground water.
This is complemented by regular monitoring by
IRSN downstream of the site and by spot analyses,
in particular in the framework of random checks
and the MIMAUSA programme.
263

TABLE 1 / TONNAGE OF DIFFERENT PRODUCTS ISSUING FROM THE L’ÉCARPIÈRE MINE AND THE PROCESSING FACILITIESUranium extracted
by the L’Écarpière
mining operation(tonnes)4109
or 5.1%of French production

Tonnage of ore
processed
at theL’Écarpière
plant (tonnes)

Uranium
produced in theplant (tonnes)

9,292,000

14,761or 18.3 %of French production

Uranium produced
Tailings fromby static
dynamic processing
processing(millions of tonnes)(tonnes)

1266

Tailings from static
processing(millions of tonnes)

7575
3775
or 24.7%
or 21%
of tailings from dynamic of tailings from static
processing produced in processing produced in
FranceFranceFIGURE 1 / THE L’ÉCARPIÈRE SITE BEFORE AND AFTER REDEVELOPMENT Source: Orano

Tailings repository
during operation

Ore processing 
plant

Former plant zone

Tailings repository

L'Écarpière site during operation (1989)

Redeveloped L'Écarpière
RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /TABLE 2 / MEASUREMENTS MADE ON AND AROUND THE L’ÉCARPIÈRE SITE

Monitored
environment or
nature of inspection

Orano

Site water

Regulatory monitoring:• 15 sampling points• At discharge (point SIMO3):
weekly measurement of
uranium, 226Ra, flow rate, pH,
TSS, COD, barium and iron
• Other points: monthly
measurements

Gamma radiation

Regulatory monitoring:• 19 measurement stations:
4 in the natural environment,
9 in the surrounding villages
and 6 on-siteAir(radon-222
and radon-220)

Regulatory monitoring:• 19 measurement stations:
4 in the natural environment,
9 in the surrounding villages
and 6 on-site• Monthly measurementsof the 222Rn PAEC, the 220Rn
PAEC and the dust

264

Continental aquatic
environment

Regulatory monitoring:• 4 measurement points in the
Moine river• Water: half-year
measurements (in the event,measurements made monthly)of uranium (soluble),226
Ra (soluble and insoluble),
flow rate, pH, TSS and iron
• Sediments: annual
measurements of 238U, 226Ra,
and 210Pb• Aquatic plants: annual
measurements of 238U, 226Ra,
and 210Pb

Overgroundenvironment (foodchain)

Regulatory monitoring:• Annual measurements of 238U,
226
Ra, 230Th, 210Pb and 210Pb
around the site

Underground water

Regulatory monitoring:• 9 wells around the site
Half-yearly measurementsof uranium and 226Ra

IRSN

DREAL and ASN
Random checks(2009 and 2010):• 3 points (at the regulatory
monitoring points: SIMO3,
SBS10bis and TAILO)• Spot measurementsof uranium, 226Ra andphysical-chemical parameters

Random checks(2009 and 2010):• 3 points (water and sediments)
at the regulatory monitoring
points: SERPA, GAUDB andCASSB and a point in the Moine
river at the point of discharge(water only)• Water: spot measurementsof uranium, 226Ra
and physical-chemical
MIMAUSA programme
parametersin 2013:• Sediments: spot
• Water: 4 points (atmeasurements of 238U,
point SERPA, in the Moine river
226
Ra, and 210Pb
at the discharge point, near
monitoring point FROB
and far downstream of thesite), spot measurementsof uranium and 226Ra• Sediments: 1 point(entirely downstream of sitenear monitoring point CASS B),
spot measurements ofradionuclides of theuranium-238 chain

Environment monitoring since2009:• 1 measurement point in thewater of the Moine river
entirely downstream of the site
• Quarterly measurementsof uranium, 226Ra,
global alpha decay,
global beta decay, 235U and234
U…

TTS: total suspended solids.
COD: chemical oxygen demand.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

FORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4
L'ÉCARPIÈRE SITE

FIGURE 2 / MAP OF LOCATIONS OF SAMPLES LINKED TO THE REGULATORY MONITORING OF THE L’ÉCARPIÈRE SITE
Mining site footprint: Source Orano

ECA49

Tail Reg FCASSBla Moine
ECA106

Tail OECA54BN

Fromont
Fontaine 68N

St-Crespin est

Fromont Village

St-Crespin ouest

Fromont Village Bas

Tail Reg M

St-Crespin ouest

FROB
Tail Bram

Le Tail

ECA109N
SBS6bisLe Tail Village

Gaudu
BRD Exut
ECA35
GAUDB
Braudière Site
Haute-Gente
SBS19
Braudière ECAPT4
Haute-Gente
SBS16bis Gaudu sitevillage
ECA25
SBS23
La Braudière Village

Gaudu village bas

SIE Carreau usine
La Petite Gagnerie

SIE digue
nord-ouest

Ore processing
residue storage

SERPA
SIMO3
SIMO Bi
SBS8bis
SBS9
SBS10bis

la M
oine

SIE digue est
La Charpraie

ECA9

ECA43 Charpraievillage
SIE diguesud-ouest
ECA13

Gaudu
SITE Inspection of air and dose rate (dosimeter + thermoluminescent dosimeters)
Gaudu Inspection of food chain
SIMO3 Physical discharge point of water treatment station (…)
ECA9Water sampling: farm wells

SBS19 Sampling of untreated site water
SBS9

Sampling of treated site water

SERPA Sampling: surface water,
sediments and aquatic plants
Footprint of old mine operation

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /265

Influence of the L'Écarpière site
on its environment• The intermediate values were recorded at theredeveloped former industrial zones (pit head,plant, etc.).

Gamma radiation and air quality• The highest average was recorded at the La
Braudière Site station, directly above an old
open-pit mine, partly filled in with mine tailings.

For the period 2015-2016, the dose rate varied
between 120 and 303 nGy/h on average for themeasurement stations located on-site, andbetween 93 and 260 nGy/h on average for thoselocated in the villages around the site (cf. figure 3).
These values are consistent with the values
generally observed on former mining sites and intheir environment.

For the surrounding villages, the highest average
was recorded in La Charpraie village, around
200 m from the tailings repository (cf. figure 3).
Considering the distance, this dose rate cannot
result from radiation emitted by the site
(cf. chapter 1). This high dose rate, comparedto the other villages, can be explained mostprobably by a local variation of the dose rate at
the measurement station. More generally, adifference in the average dose rate was observed
between the villages situated on the left bank of
the Moine river (mining site side) and those on
the right bank. This is explained by a variation in
the geology between these two banks, with thegeological formation on the left bank being richer
in uranium.

The different values measured on the site canbe explained by the nature of the soils at themeasurement stations:• The lowest averages were to be found at thestations positioned on the tailings repository:
the gamma radiation from the mining residues is
attenuated by the cover on top of these residues.

266
FIGURE 3 / 2015-2016 AVERAGE OF DOSE RATES MEASURED BY ORANO ON AND AROUND THE L’ÉCARPIÈRE SITE (nGy/h)
Mining site footprint: Source Orano

St-Crespin est

Fromont Village bas

St-Crespin ouest(144 nGy/h)(103 nGy/h)(96 nGy/h)

Fromont Village(93 nGy/h)Braudière Site
Le Tail Village(145 nGy/h)(216 nGy/h)Gaudu Village bas(303 nGy/h)Haute-Gente Village(123 nGy/h)Gaudu Site
(185 nGy/h)

La Braudière Village(171 nGy/h)

SIE Digue est
SIE Carreau usine(158 nGy/h)(216 nGy/h)

SIE Digue nord-ouest(126 nGy/h)

Dose rate (nGy/h)Footprint of old mining
operation

Dose rate <150
150 ≤Dose rate <200
200 ≤Dose rate <250

Gaudu
Site

Measurement station
on site250 ≤Dose rate <302

Le Tail
Village

Measurement stationin site environment

SIE Digue sud-ouest(120 nGy/h)/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

Charpraie Village(260 nGy/h)FORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4
L'ÉCARPIÈRE SITE

The PAEC measurements for 222Rn on and aroundthe site for 2015-2016 illustrate the influence of the
topography on the measurement of this quantity,
independently of the location of the measurement
station on-site or off-site (cf. figure 4). The
highest averages are therefore to be found in thestations located in the valley bottom, a situation
less conducive to the dispersion of radon in the
air. Conversely, the lowest averages correspondto the stations located in summit position, more
conducive to radon dispersion. The off-site PAEC
measurement of 222Rn can be explained more by
the station's exposed situation to the winds thanby the geology, unlike the dose rate.

radium-226 activity. The reagents used are milkof lime, barium chloride and an anionic organic
flocculant.
The treated water is the water from the drainage ofthe tailings repository, representing less than 5%of the total treated volume (points SBS8bis, SBS9,
SBS10bis) and the pit water from the undergroundmining works (point ECA PT4) (cf. figure 2). The
run-off water from the mining zone, the pit waterfrom the old mining works zone and the waterfrom the tailings repository are not subject totreatment, but they are monitored.
The water from the L'Écarpière site, after
treatment, is discharged at point SIMO3 into theMoine river (cf. figure 2). The discharge standards,
determined by prefectural order, are as follows:

Surface water

Currently, some of the water issuing from the site
is collected at the water treatment plant on the
L’Écarpière site, to reduce the water's radium-226
activity and its uranium and iron concentration,and to neutralise the pH. The treatment consists
first of all in precipitating the iron and trapping
the uranium with the previously-formed ironhydroxides and oxyhydroxides. Treatment by
precipitation and coagulation – flocculation –decantation is then carried out to reduce the• The pH must be between 5.5 and 8.8.
• The uranium, radium-226 and iron must,
respectively, be less than 1800 µg/L (in solubleform), 370 mBq/L (in soluble form) and 5 mg/L,
as a monthly average for the samples taken
weekly.

FIGURE 4 / 2015-2016 AVERAGE OF 222Rn PAEC MEASURED BY ORANO FOR THE MONITORING ON AND
AROUND THE L’ÉCARPIÈRE SITE (nJ/m3)

PAEC 222Rn (nJ/m3)
350

Measurement
stationsin valley bottom

300

Measurement
stationsin valley
bottomMeasurement
stations
on hillside

250
200
150
100

Measurement stations
in summit position

Measurement stations
in summit position

50
0CharpraieLa
village Braudière
village

Haute St-Crespin St-Crespin Le Tail
Gente
est
ouest
villagevillage

Fromont
villageGaudu
villagebas

Fromont SIE Digue SIE Digue
SIE
villagenordsudCarreau
bas
ouest
ouest
usine

Measurement station in nearby environment to site

SIE
digue
est

Gaudu
La
site Braudière
site

Measurement station on site

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /267

The measurement logs show that the water
treatment enables a reduction in the uranium
concentration and the radium-226 activity andcompliance with the discharge values (cf. figures 6
and 7). Furthermore, the uranium concentration in
the discharges has reduced since 2006 (cf. figures
6 and 7), whereas the radium-226 activity in thesesame discharges has increased since 2015. This
increase results from a reduction in the quantityof reagent used by Orano for treating the water,
with the objective of optimising the consumptionof reagents and reducing the chemical impact of
the barium on the environment while respecting
the regulatory value (source: Orano).

268

The measurements also show that the discharges
have little influence on the uranium concentrationand the radium-226 activity in the waters of theMoine, close downstream of the discharge point(point GAUD B - cf. figures 5 to 7). Indeed theaverages, for the period 2006-2016, for these twoparameters are of the same order of magnitude atpoint GAUD B (U = 2.7 µg/L et 226Ra = 29.1 mBq/L) as
upstream of the site at point SERP A (U = 1.6 µg/L
and 226Ra = 27.4 mBq/L).

As far as the water discharged without treatment
is concerned, the monitoring of run-off waterfrom the mining zone and the tailings repository
conducted between 2006 and 2016 (points Tail
RegF, Tail RegM, Tail Bram, BRD EXUT, SBS 6bis,
SBS 19 and SBS 23) indicates that the average
concentrations of uranium in this water isbetween 13.6 µg/L (point SBS6Bis) and 867.5 µg/L
(point Tail RegF) and that the average radium-226
activity is between 46.3 mBq/L (point Tail RegM)
and 191.3 mBq/L (point Tail Bram). These values,in particular at points Tail Bram and Tail RegF,
are in some cases significantly higher than thosemeasured at point SERP A (upstream of site). It
should be noted that the run-off water flows are
discontinuous.
The measurements made in the Moine river reveal
an average radium-226 activity in the same orderof magnitude entirely downstream of the site(measurement point CASS B) as upstream, andan average uranium concentration three times
higher (U = 5.8 µg/L).

FIGURE 5 / AVERAGE MEASUREMENTS OF URANIUM AND RADIUM-226 MADE BETWEEN 2006 AND 2017 IN THE MOINE RIVER(purple labels) AND THE UNTREATED SITE WATERS (red labels)
Mining site footprint: Source Orano

Tail Reg F
FROB

CASSB
Tail O

Tail Bram
Tail Reg M
GAUDBBRD Exut

IRSN
Monitoring

SERPA

SBS6bis
SBS16bis226

Ra (mBq/L)

Data<decision threshold226
Ra < 5050 ≤ 226Ra < 100
100 ≤ 226Ra ≤ 191

Uranium (µg/L)
U<4
4≤U<8
8 ≤ U < 30
30 ≤ U < 100
100 ≤ U < 500
500 ≤ U ≤ 868/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

SBS19
SBS23

FORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4
L'ÉCARPIÈRE SITE

FIGURE 6 / URANIUM CONCENTRATION IN THE SITE WATERS BEFORE TREATMENT, AT THE DISCHARGE POINT
AFTER TREATMENT AND IN THE MOINE RIVER (µg/L)

Uranium (µg/L)
10,000
1000
100
10
1

Jan-06
Apr-06
Jul-06
Oct-06
Jan-07
Apr-07
Jul-07
Oct-07
Jan-08Apr-08
Jul-08
Oct-08Jan-09Apr-09Jul-09Oct-09Jan-10
Apr-10Jul-10
Oct-10Jan-11
Apr-11
Jul-11
Oct-11
Jan-12
Apr-12
Jul-12Oct-12
Jan-13Apr-13
Jul-13Oct-13Jan-14Apr-14Jul-14Oct-14Jan-15
Apr-15
Jul-15Oct-15Jan-16
Apr-16
Jul-16Oct-160.1

Orano monitoring data

Decision thresholds
Spot measurements

La Moine - upstream of site (SERP A)
La Moine - downstream near to discharge (GAUD B)
Discharge after treatment (SIMO 3)

DREAL and ASN (11/2009 and 06/2010)
La Moine - upstream of site (SERP A) (decision thresholds)
La Moine - downstream near to discharge (GAUD B)
La Moine - at discharge

Site waters before treatment
West drain of storage (SBS 8b)

IRSN (09/2013)
La Moine - upstream of site (SERP A) (decision thresholds)

North drain of storage (SBS 9)
East drain of storage (SBS 10b)
Pit water from underground mining works (ECA PT4)

La Moine - downstream near to discharge (GAUD B)
La Moine - at discharge

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /269

FIGURE 7 / RADIUM-226 ACTIVITY IN THE SITE WATERS BEFORE TREATMENT, AT THE DISCHARGE POINT
AFTER TREATMENT AND IN THE MOINE RIVER (mBq/L)

Ra (mBq/L)

226

1,000

100

10

Jan-06
Apr-06
Jul-06
Oct-06
Jan-07
Apr-07
Jul-07
Oct-07
Jan-08Apr-08
Jul-08
Oct-08Jan-09Apr-09Jul-09Oct-09Jan-10
Apr-10Jul-10
Oct-10Jan-11
Apr-11
Jul-11
Oct-11
Jan-12
Apr-12
Jul-12Oct-12
Jan-13Apr-13
Jul-13Oct-13Jan-14Apr-14Jul-14Oct-14Jan-15
Apr-15
Jul-15Oct-15Jan-16
Apr-16
Jul-16Oct-161

270

Orano monitoring data

Decision thresholds
Spot measurements

La Moine - upstream of site (SERP A)
La Moine - downstream near to discharge (GAUD B)
Discharge after treatment (SIMO 3)
Site waters before treatment
West drain of storage (SBS 8b)
North drain of storage (SBS 9)
East drain of storage (SBS 10b)
Pit water from underground mining works (ECA PT4)DREAL and ASN (11/2009 and 06/2010)
La Moine - upstream of site (SERP A)(decision thresholds)
La Moine - downstream near to discharge (GAUD B)(decision thresholds)
La Moine - at discharge
IRSN (09/2013)
La Moine - upstream of site (SERP A)(decision thresholds)
La Moine - downstream near to discharge (GAUD B)(decision thresholds)
La Moine - at discharge/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

FORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4
L'ÉCARPIÈRE SITE

Sediments

The results of monitoring the sediments in the
Moine river, between 2006 and 2016, indicate thatthe average uranium-238 and radium-226 activity
levels are higher at points GAUD B and CASS B(cf. table 3) compared to those upstream (SERP
A). The results of spot measurements made by
the ASN at the same sampling points also confirm
this trend.

TABLE 3 / ACTIVITY PER UNIT MASS OF URANIUM-238 AND RADIUM-226 IN THE SEDIMENTS SAMPLED FROM THE MOINE
RIVER BETWEEN 2006 AND 2016 (Bq/kg sec)Nameof sampling
point

Orano monitoring(2006-2016)

DREAL and ASN inspections(2009 and 2010)

238
U(Bq/kg dry)

226
Ra
(Bq/kg dry)

238
U
(Bq/kg dry)

226
Ra
(Bq/kg dry)

SERP A

Average: 91.8
[min.: < 50; max.: 150]

Average: 82.7
[min.: 40; max.: 130]2009812010119< 69
138

GAUD B

Average: 247.9[min.: < 50; max.: 654]

Average: 251.8[min.: 90; max.: 560]

2009463
2010170

964
300

FRO B

Average: 78.0
[min.: < 30; max.: 148]

Average: 81.8
[min.: 50; max.: 130]CASS B

Average: 259.5[min.: < 65; max.: 1500]

Average: 175.5[min.: 50; max.: 470]2009/
20101100/
86

Downstreamof siteIRSN second-level
MIMAUSA inspection(2013)
238
U(Bq/kg dry)

226
Ra
(Bq/kg dry)

271

160

100

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Food chain

Figure 8 presents the radium-226 activity levels
measured in certain foodstuffs sampled aroundthe site. Since 2009, measurements have been
made on mixtures of foodstuffs of the same
category taken from several villages located on
the right bank of the Moine river (Saint-Crespinsur-Moine, Fromont, Gaudu) and on its left bank(Braudière, Haute-Gente and Charpraie). The
radium-226 activity levels are between:• 0.037 (decision threshold) and 0.76 Bq/kg freshfor leafy vegetables;• 0.070 (decision threshold) and 0.94 Bq/kg freshfor fruits;• 0.050 (decision threshold) and 0.71 Bq/kg freshfor poultry;• 0.055 (decision threshold) and 0.13 Bq/kg freshfor a mixture of chicken and rabbit.
These values are situated within the ranges
observed in France in zones with "high naturalradioactivity levels" (abbreviated as HNRN, cf.
chapter 2 figure 10), and indeed in zones that areless rich in natural uranium.

• 0.035 (decision threshold) and 0.33 Bq/kg freshfor root vegetables;

FIGURE 8 / RADIUM-226 ACTIVITY FOR VARIOUS FOODSTUFFS SAMPLED AROUND THE L’ÉCARPIÈRE SITE (Bq/kg fresh)

Bq/kg fresh
1
272

0.9
0.8
0.7
0.6
0.5
0.4
0.3
0.2
0.1
0
2007

2008

2009

Leafy vegetables

2010

2011

2012

2013

Decision thresholds
Root vegetables
FruitsPoultry/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

2014

2015

2016

Chicken and rabbit

FORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4
LE BOSC SITE

Le Bosc site

Covering an area of around 220 ha, this site wasoperated from 1978 (2) to 1997, with undergroundmine works and several open-pit mines, producing
14,632.5 tonnes of uranium (cf. table 1). An ore
processing plant was also in operation on the site
between 1981 and 1997. This plant was dismantled
and the entire site was redeveloped (cf. figure 1).
Currently, the site contains a uranium ore
processing tailings repository (4,142 Mt of dynamic
processing tailings) and a water treatment station.
Furthermore, part of the site was redeveloped as
an industrial zone and another part turned into asolar park.

The Le Bosc site is situated in the Hérault
department in the municipalities of Soumont andLe Bosc, located several kilometres to the southeast of Lodève. The Lergue river runs to the westof the site and has several tributary streams thatpartially drain the Le Bosc site (cf. figure 2). The
Lodève region is characterised by a Mediterranean
climate with a "Cévennes"-type rainfall pattern(i.e.: very intense rain spells that can extend over
2 to 3 days). This particular rain pattern can leadto intense leaching of the soils over a short period.

TABLE 1 / TONNAGE OF DIFFERENT PRODUCTS ISSUING FROM THE LE BOSC MINE AND THE PROCESSING FACILITIESUranium extracted
by the Le Bosc mining
operation (tonnes)

Tonnage of ore processedat the Le Bosc plant (tonnes)

14,633or 18.1% of French production

4,141,518

Uranium producedin the plant(tonnes)Tailings from dynamic
processing(millions of tonnes)

12,853or 13.5% of tailings
from dynamic processing
produced in France

4142

or 15.9% of French production

FIGURE 1 / THE LE BOSC SITE BEFORE AND AFTER REDEVELOPMENT
Source: Orano

Old factory zone

Ore processing plant
Storage of residues
during operation

Residue storage

2. Small-scale reconnaissance work took place on this site starting in 1959.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /273

Monitoring plan

• the food chain around the site;

The Le Bosc site is subject to regulatory
monitoring, along with complementary
monitoring at the initiative of the operator.
The Orano monitoring plan is presented below(cf. table 2 and figure 2), involving the monitoringof the following:• underground water on the site and in theenvironment.

• site water (discharge and drainage waters fromthe tailings and mining works);• gamma radiation on and around the site;• air quality on and around the site (radon and dust);• the aquatic environment around the site;

One of the specific characteristics of the site is
the presence, in the uranium deposit rocks, ofminerals containing molybdenum and arsenic.
For this reason, the concentrations of arsenic
and molybdenum are also among the parameters
included in the monitoring, as well as theradiological parameters.
This monitoring is complemented by spot analyses,
in particular in the framework of random checks
or of the MIMAUSA programme.

TABLE 2 / MEASUREMENTS MADE ON AND AROUND THE LE BOSC SITE

274

Monitored
environment or
nature ofinspection

Orano

DREAL

Site water• Random checks• Regulatory monitoring at the(2010 and 2013):
discharge point (point 92REJLER)
At the discharge point: spot
Measurements:
measurements of uranium,−−Continuous: flow rate, pH, soluble
226
Ra, and 210Pb
uranium−−Weekly on an average daily
sample: T°, TSS, SO42-,226
Ra (in event of 226Ra processing)−−Quarterly on an average daily
sample: COD−−Every 3 days on an average sample
over 3 days: uranium, barium(in event of processing withbarium chloride),226
Ra (in event of processing
with barium chloride), arsenic(in event of processing arsenic)−−Monthly on an average daily
sample: molybdenum, arsenic(except in the event of processing
arsenic)

Gamma radiation• Regulatory monitoring:
9 measurement stations:
1 in the natural environment,
4 in the surrounding villages and4 on-siteAir(radon-222
and radon-220)• Regulatory monitoring:
9 measurement stations:
1 in the natural environment,
4 in the surrounding villages and4 on-site.
Monthly measurements of the222
Rn PAEC and the 220Rn PAEC

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017IRSN

FORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4
LE BOSC SITE

Monitored
environment or
nature ofinspection

Orano

DREAL

IRSN

• MIMAUSA programme• Regulatory monitoring:• Random checks
in 2014:(2010 and 2013):−−Water: 3 sampling points
Water: 9 points
Surface water:(90 RMA, 90 RVA and 90 LERGP)−−1 point at regulatory
Monthly measurements of−−2010: 5 sampling points
monitoring point 90RMA.
uranium, 226Ra, 210Pb,(points 13 = LERGF,
14 = LERGP, 12 = Mas d’Alary, −−Other points:
pH, SO42-, arsenic and
16 = far upstream the Lergue,
molybdenum. Quarterly
Lergue river:
15 = Rivieral stream).
measurements of the COD.
entirely upstream of
Spotmeasurementsofthe site – near Lodève,−−Sediments: 4 sampling points (90226210uranium, Ra and Pb.
at point LERGF,
RMA, 90 RVA, 90 LERGF and 90
immediately downstream
LERGP), measurements made−−2013: 4 sampling pointsof Le Bosc site discharge,
every 5 years (238U, 226Ra, 210Pb and(points LERGF, LERGP, Mas
Continental aquaticMas d’Alary stream:d’Alary, Rivieral stream).
particle sizes)
environment
ahead of confluence
Spot measurements−−Bio-indicators (aquatic plants,
with the Lergue;of uranium, 226Ra and 210Pb.
fish): 4 sampling points (90 RMA,
Domergoux stream: entirely
90 RVA, 90 LERGF and 90 LERGP),
downstream of site;measurements made every 5 years
Rivieral stream: entirely(238U, 226Ra and 210Pb)
downstream of site,• Monitoring at the operator's
downstream of confluence
initiative: 1 additional monitoringwith Domergoux stream,
point for surface water (90 LERGF).
immediately downstream ofMonthly measurements of uranium,
La Plane Campagnac site
2226
210
Ra, Pb, pH, SO4 , arsenic and• Spot measurements
molybdenum. Quarterlyof uranium and 226Ra
measurements of the COD.
Overgroundenvironment (foodchain)• Regulatory monitoring:
Every 2 years, for 5 food categories(composite samples)• Regulatory monitoring:
10 piezometers on and around thesite;
Quarterly measurements ofuranium, 226Ra, 210Pb, pH, SO42-,
arsenic
and molybdenum.
Underground water• Monitoring at the operator's
initiative: 2 additional points:
91 S1: uranium and226
Ra measurements 91 TUIL:
uranium measurements• Random checks (2013):
2 points (piezometer FS andP33). Spot measurements ofuranium, 226Ra and 210Pb

TTS: total suspended solids, COD: chemical oxygen demand.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /275

FIGURE 2 / MAPS OF LOCATIONS OF SAMPLES LINKED TO THE REGULATORY MONITORING OF THE LE BOSC SITE
Mining site footprint: Source Orano
VLODEVE
Lodève

ral
ivie
eR
au d
sse
Rui
oux
erg
om
uD
au d
sse
Rui

la Lergue

Site Puech Buissou

Site Le Bosc
Ruisseau du
Mas d’Alary

Site La Plane-Campagnac

Ruisseau de Rivieral

Site Rabejac

90LERGP

l
iera
Riv

streamTréviels

am
stre

am
stre

oux
erg
Dom

m
trea
res s
Tuilè

276

Mas Campagnard
MASCAMP

91TUILssing
roce geOre pue stora
resid
STOCKSITE
P33
PZFS
STE
St-Julien
92REJLER PZ7FTREVIELHYDRO34

PZ8

ZI

91S1

Tréviels farm

Mas
d’Alary
streamPZ1

la Lergue
90LERGF

PZ6

P37

PZ3

ZLSITE

St-Martin
VSMARTIN

VSJULIEN

90RMA
PZ2

PZ4
Physical discharge point of STE

Rivieral stream

90RVA

Sampling: surface water,
sediments, aquatic plants

ZI

Air inspection (dosimeter + TLD)

90RMA

PZ1

Piezometers and pumping well

92REJLER Water treatment station discharge

91TUIL Resurgence

Physical discharge pointof water treatment station/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

St-Martin Food chain
inspection
Mine footprint

FORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4
LE BOSC SITE

Influence of the Le Bosc site
on its environment
Gamma radiation and air quality

For the period 2015-2016, the dose rate varied
between 139 and 225 nGy/h on average for themeasurement stations located on the Le Boscsite, and between 140 and 216 nGy/h on averagefor those located in the villages around the site
(cf. figures 3 and 4). These values are consistent
with the values generally observed on former
mining sites and in their environment.
The different values measured on the site canbe explained by the nature of the soils at themeasurement stations:• The lowest average is located at the station
close to the water treatment plant (STE).
This was installed directly above a former
open-pit mine partially backfilled with mining
waste.

• The intermediate values are to be found in
the former industrial zone (former ore
processing plant), which has been redeveloped(stations ZI = dismantled industrial zone and
ZLSITE = developed/re-converted industrialzone).
• The highest average is recorded at the station
located on the tailings repository.
The dose rate measurements in the villages
illustrate the variability of this parameter according
to the geology. Indeed, the measurement stations
can be categorised according to the geology of theland on which they are located (cf. figure 4).
• The villages of Saint-Martin and Saint-Julien,
situated over rock belonging to the "red"Autunian stage, present average dose rate
values of 140 and 141 nGy/h respectively.
• Mas Campagnard and Ferme de Tréviel, situatedover rock belonging to the "grey" Autunian
stage, present average dose rate values of 185
and 216 nGy/h respectively.
277

FIGURE 3 / 2015-2016 AVERAGE OF DOSE RATES MEASURED BY ORANO ON THE LE BOSC SITE (nGy/h)

Dose rate [nGy/h]
250
200
150
100
50
0

STOCKSITE(storage area)

ZLSITE(developed zone)

ZI(industrial zone)

STE

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 4 / SITING OF MEASUREMENT STATIONS AND AVERAGE 2015-2016 DOSE RATES (nGy/h)
MEASURED BY ORANO AROUND THE LE BOSC SITE AGAINST THE GEOLOGICAL MAP BACKGROUND
Map background: geological map 1/50,000th No. 989 Lodève sector ©BRGM. Source: Géoportail.

MASCAMP185 nGy/h
FTREVIEL
216 nGy/h

Le

c
Bos

site
VSMARTIN
140 nGy/h

VSJULIEN
141 nGy/hN
Scale 1/34,110

Background map : Carte géologique 1/50,000 n°989 secteur de Lodève ©BRGM, source Géoportail© IRSN

278

Solar panels on the Le Bosc site

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

FORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4
LE BOSC SITE

The average 222Rn PAEC values for 2015-2016
amount to between 35 and 58 nJ/m3 in the villages
and between 43 and 152 nJ/m3 on the site (cf.
figure 5). The highest averages are therefore
to be found in the stations located in the valley
bottom (stations STE and ZI), a situation lessconducive to the dispersion of radon in the air.
It should be noted that the measurements madefor the topographical situations most conducive tothe dispersion of radon ("summit" and "hillside")at L’Écarpière present comparable levels (cf.
p. 264). This can be explained by the fact that theenvironment of the Le Bosc site presents a relief
that is less markedly conducive to the dispersionof radon.

FIGURE 5 / 2015-2016 AVERAGE OF 222RN PAEC MEASURED BY ORANO FOR THE MONITORING
ON AND IN THE SURROUNDING ENVIRONMENT OF THE LE BOSC SITE (nJ/m3)

PAEC 222Rn (nJ/m 3)
160

Measurement stations
in valley bottom

140
120
100
80
60

279
Measurement
station insummit position

Measurement station on hillside

40
20
0
VSMARTIN(St-Martin
village)

FTREVIEL(Tréviel
farm)

MASCAMP(Mas
Campagnard)

Measurement stationin nearby environment to site

VSJULIEN(St-Julien
village)

STOCKSITE(storage
area)

ZLSITE(developed
zone)

ZI
(industrial
zone)

STE

Measurement station on site

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Figure 6 shows that the uranium concentrations in
the water to be processed are very high (around
10,000 µg/L on average) compared to the othermining sites. By way of comparison, the water
treated on the L'Écarpière site presented average
concentrations (2006-2016 period) of between
90 µg/L and 411 µg/L. It next appears that thetreatment has been very efficient, with a more thantenfold reduction in the uranium concentration.

Surface water

The water issuing from the underground mining
works (pumped via well P33) along with the water
issuing from the drainage of the ore processing
tailings repository are treated before being
discharged into the Lergue river. One of thechallenges of this site is the management of
the seasonal flow rate variations, which can bevery significant, such as during "Cévenne"-type
heavy rain episodes. To manage these flow ratevariations, therefore, the site has two water
treatment processes:

The measurements made around the site, for theperiod 2010-2016, show that the streams draining
the various zones of the site (points 90RMA and
90RVA, cf. figure 7) presented higher uranium
concentrations than the point located upstreamof the site (point LERGF, ULERGF = 1.5 µg/L, cf.
figure 7). The average uranium concentrationsat points 90RMA and 90RVA are therefore
1230.2 µg/L and 574 µg/L respectively. The
streams of Mas d’Alary and Rivieral receive therainwater of the site, which might explain thesehigh concentrations. These various streams andthe discharge have an influence on the Lergue
river downstream of the site, with the average• uranium sequestration on ion-exchanging resins(in normal operation);• treatment by precipitation-decantation after
addition of lime (in periods of heavy rain or
failure of sequestration on resins).

280

The purpose of this processing is to lower theuranium content in the water so as to comply withthe regulatory limit of 1800 µg/L for uranium. For
the period 2010-2016, the average concentrationof uranium in the discharges was 242 µg/L.

FIGURE 6 / AVERAGE URANIUM CONCENTRATIONS BETWEEN 2002 AND 2012 IN THE WATERS BEFORE TREATMENT (points 91
P33 and 91 B10000) AND AFTER TREATMENT (point 92 REJLER) (µg/L)
Source: Oranoµg/L
100,000
19,00010,0001000

11,15010,850 10,215 10,138

14,856 12,631 10,596

10 600370 390

310

310

200

210

9,210

140

9,080

9,033

230
60

100

11,453

110

7,976

210

10
1
2002

2003

2004

2005

2006

2007

2008

2009

2010

2011

2012

Data from regulatory monitoring and from monitoring at the operator’s initiative
Regulatory monitoring
Monitoring at the operator’s initiative of site waters before treatment
Discharge after processing
Pit water pumped from well P33 (91 P33)
(92 REJLER)
Water from pool 10,000 which collects the drainage water fromthe mining residue storage (91 B10000)/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

FORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4
LE BOSC SITE

uranium concentration around 3 times higher atpoint LERGP (ULERGP = 5.8 µg/L) than upstream ofthe site (ULERGF = 1.5 µg/L).

2015. Generally, the discharge and the contribution
from the streams have very little influence on theradium-226 activity in the Lergue river. Indeed, themeasurements made entirely downstream of thesite reveal average radium-226 activity of similar
magnitude to that measured upstream (upstream:
226
RaLERGF = 31.9 mBq/L, downstream: 226RaLERGP =42.6 mBq/L) for the entire measurement period.

For the period 2010-2016 (cf. figure 8), thehighest radium-226 activity was recorded at
the discharge point (226Ra =257.6 mBq/L on
average) and, to a lesser extent, in the streamsof Mas d’Alary and Rivieral (average activity:
226
RaRMA = 82.1 mBq/L, 226RaRvA = 75.1 mBq/L). It should
be noted that there were nine occasional overshootsof the regulatory discharge limit for radium-226(which is 740 mBq/L) between December 2015
and the end of April 2016 following an exceptional"Cévennes"-type heavy rainfall episode in late

The results of the various spot measurements
carried out in the framework of random checks
or the MIMAUSA programme are consistent withthose deriving from the monitoring of the operator(cf. figures 7 and 8).

FIGURE 7 / URANIUM CONCENTRATION, BETWEEN 2010 AND 2016, AT THE DISCHARGE POINT AND IN THE SURFACE WATERS
IN THE ENVIRONMENT OF THE LE BOSC SITE (µg/L)µg/L
10,000
281
1000

100

10

1

01
6
7/
2
/0

28

01
/2

01
6

15
10
/

6/
/0
24

20

20

15

14

/1
2/
06

/0

5/

20

01
3
20

01
3

01
/1
1/
2

/2
04

01
2

15
/

9/
2

20

27
/0

3/
11
/0

8/
/0
24

2/
/0

12

11
20

11
20

01
0
05

7/
2
/0

20

01
/0

1/
2

01
0

0.1

Decision thresholds

Data from regulatory monitoring and from monitoring at the operator’s initiative
Discharge after processing (92 REJLER)
Monitoring point for water from Lergue riverat operator’s initiative - upstream discharge
and Mas d’Alary (point 90 LERGF)
Lergue river - entirely downstream of site(point 90LERGP)

Mas d’Alary stream, receiving rainwater from site - mining zone
and coverage of demolition products storage (point 90RMA)
Rivieral stream, receiving rainwater from site - mining zone
and coverage of ore processing residues (point 90RVA)

Spot measurements (random checks 2010, 2013 and MIMAUSA)At point 92 REJLER

At point 90 LERGF

At point 90RMA

At point 90RVA

At point 90 LERGPRADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 8 / RADIUM-226 ACTIVITY, BETWEEN 2010 AND 2016, AT THE DISCHARGE POINT AND IN THE SURFACE WATERS
IN THE ENVIRONMENT OF THE LE BOSC SITE (mBq/L)

mBq/L

1000

100

10
282

01
3
01
/1
1/
20
13
20
/0
5/
20
14
06
/1
2/
20
15
24
/0
6/
20
15
10
/0
1/
20
16
28
/0
7/
20
16

15
/

04

/2

01
2
9/
2

20

27
/0

3/
11
/0

8/
/0
24

2/
/0

12

11
20

11
20

01
0
05

7/
2
/0

20

01
/0

1/
2

01
0

1

Decision thresholds

Data from regulatory monitoring and from monitoring at the operator’s initiative
Discharge after processing (92 REJLER)
Monitoring point for water from Lergue riverat operator’s initiative - upstream discharge
and Mas d’Alary (point 90 LERGF)
Lergue river - entirely downstream of site(point 90LERGP)

Mas d’Alary stream, receiving rainwater from site - mining zone
and coverage of demolition products storage (point 90RMA)
Rivieral stream, receiving rainwater from site - mining zone
and coverage of ore processing residues (point 90RVA)

Spot measurements (random checks 2010, 2013 and MIMAUSA)At point 92 REJLER

At point 90 LERGF

At point 90RMA

At point 90RVA/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

At point 90 LERGPFORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4
LE BOSC SITE

Sediments

Fish

The results of the monitoring of the sediments
around the Le Bosc site, between 2006 and 2016,indicate that the average 238U and 226R activity ishigher in the streams of Mas d’Alary and Rivieral(points 90RMA and 90RVA, cf. table 3) than in the
Lergue river. These results are consistent withthe markings observed in the water of these two
streams. Furthermore, these results indicate that
there is no significant marking in the Lergue river
downstream of the site.

The radium-226 and polonium-210 activity
measured in two fish species (chub andbarbel), sampled in the Lergue river upstream
and downstream of the site, was found to be(cf. figure 9):• for radium-226, between 0.31 and 1.52 Bq/kg
fresh upstream and < 0.25 (decision threshold)and 0.58 Bq/kg fresh downstream;• for polonium-210, between 0.06 and 1.29 Bq/kg
fresh upstream and < 0.113 (decision threshold)and 0.97 Bq/kg fresh downstream.
It should be noted that fish taken downstream ofthe sites may also spend time upstream, whichmakes it difficult to compare the results obtained.

TABLE 3 / AVERAGE ACTIVITY PER UNIT MASS OF URANIUM-238 AND RADIUM-226 IN THE SEDIMENTS SAMPLEDAROUND THE LE BOSC SITE BETWEEN 2006 AND 2016 (Bq/kg dry)

Orano monitoring (2006-2016)
Names of sampling points

238

U(Bq/kg dry)

226
Ra
(Bq/kg dry)Lergue – Upstream of site (90LERGF)

Average: 70.4
[min.: 25; max.: 300]

Average: 59.9
[min.: 40; max.: 87.6]

Lergue – Downstream of site (90LERGF)

Average: 47.7
[min.: 31.8; max.: 75]

Average: 67.2
[min.: 40; max.: 120]

Rivieral stream (90RVA)

Average: 280[min.: 170; max.: 420]

Average: 378[min.: 261; max.: 510]

Average: 344.7[min.: 245.2; max.: 503.7]

Average: 329.7[min.: 285.9; max.: 399]

Mas d’Alary stream (90RMA)

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /283

FIGURE 9 / RADIUM-226 AND POLONIUM-210 ACTIVITY IN FISH FLESH (chub and barbel) SAMPLED AROUND THE LE BOSC
SITE (Bq/kg fresh)

Bq/kg fresh
1.6
1.4
1.2
1
0.8
0.6
0.4
0.2
0
Jan.-08

Jan.-09

Jan.-10Jan.-11Chub
Ra measurement

226

Capitoul (site upstream)
Petout (site downstream)

Jan.-12Jan.-13

Barbel230

Po measurement

Capitoul (site upstream)
Petout (site downstream)

Ra measurement

226

Capitoul (site upstream)
Petout (site downstream,
decision threshold)284/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017230

Po measurement

Capitoul (site upstream)
Petout (site downstream)

FORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4
LA COMMANDERIE SITE

La Commanderie site
The La Commanderie site is situated between
the municipalities of Treize-Vents (Vendée) and
Mauléon (Deux Sèvres). This site is located on
granitic terrain, with an area of around 60 ha,
and was operated from 1955 to 1990, with
underground mine works and an open-pit mine,
producing 3977 tonnes of uranium (cf. table 1). In
1969, a static leaching processing facility for lowcontent ore (150 to 600 ppm of uranium) was set
up on the La Commanderie site. The ore, crushed
down to 80 mm and placed in a sealed area, waswatered with a mixture of water and sulphuric
acid. This process enabled the uranium to be
extracted by solubilisation. The uranium liquor

obtained in this way was then transported to the
L’Écarpière plant. The product residues (0.25
Mt) were then stored with the materials issuingfrom the dismantling of the static processing
facility (pools, concrete storage area for the ore,leaching area) at the bottom of the open-pit mine
under a cover consisting of a layer of lime andmine tailings. The open-pit mine was then flooded.
The site now plays host to diverse activities suchas a solar park and agricultural and industrial
activities. Furthermore, the water from the La
Commanderie open-pit mine has been used for
irrigation purposes since 1993.

TABLE 1 / TONNAGE OF DIFFERENT PRODUCTS ISSUING FROM THE LA COMMANDERIE MINE AND THE PROCESSING FACILITIESUranium extracted by the
La Commanderie mining operation(tonnes)

Uranium produced
by static processing(tonnes)Tailings fromstatic processing(millions of tonnes)

3977.5or 4.9% of French production

Included in the productionof the L’Écarpière plant

0.25
or 1.4 % of tailings
from static processing produced in France

FIGURE 1 / THE LA COMMANDERIE SITE, DURING MINING OPERATION, BEFORE AND AFTER REDEVELOPMENT
Source: Orano

La Commanderie during operation (1975)

La Commanderie during redevelopment

La Commanderie after redevelopment
RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /285

Monitoring plan
The La Commanderie site is subject to regulatory
monitoring prescribed by prefectural order,
amended in January 2017. However, in theframework of this Radiological report, only thedata obtained until 2016 are presented. The
complementary points deriving from the newmonitoring plan are indicated for information
purposes in table 2. The monitoring conducted
before 2017 by Orano is presented below(cf. table 2 and figure 2), involving the monitoringof the following:• site waters (waters of the open-pit mine);• the food chain around the site (in particular thefields and crops that are irrigated by the waterfrom the mine).
This monitoring by the operator is complemented
by spot analyses, in particular in the framework of
random checks or of the MIMAUSA programme.
It should be noted that the monitoring of the
air quality and gamma radiation ceased in 1995
upon production of the site relinquishment andpartial abandonment report, which is why nomeasurement concerning these two parameters
is presented below.

• the aquatic environment around the site
(La Commanderie stream, La Boisdrotière stream);
TABLE 2 / MEASUREMENTS MADE ON AND AROUND THE LA COMMANDERIE SITE

286

Monitored
environment or
nature ofinspection

Orano

IRSN

DREAL and ASN• Regulatory monitoring:• Open-pit water: surface water(CDR O) and bottom of pool (waterused for irrigation = CDR IR)• Measurements: 238U, 226Ra, pH, Al,
As, Fe, Mn- for point CDR O: quarterly
measurements- for point CDR IR: at the start ofeach pumping campaign thenmonthly during the pumping
campaign• Random checks(2009 and 2010):
1 point (CDR O), spotmeasurements of uranium,
226
Ra
and physical-chemicalparameters• Regulatory monitoring:• Water: 6 sampling points(RUCDR A, RUDIG A, RUCDR O,
RU CDR, CDR S1, RUDIG)
Quarterly measurements of
238
U, 226Ra, pH, Al, As, Fe and Mn.
5 additional points from 2017:
Continental aquatic
CDRA1, CDRA2, CDRB1, RUBLA,
environment
MALLB• Sediments: 2 sampling points(RUCDRA, RUDIG), annual
measurements (Uby weight by
gamma spectrometry)
2 additional points from 2017:
CDRB1, RUBLA• Random checks(2009 and 2010): 9 points• Water: 5 points at theregulatory monitoring points(RUDIGA, RUDIG, RUCDRA,RUCDRO, RUCDR).
- Other points: theLa Boisdrotière stream
downstream of theconfluence with the La
Commanderie stream, the
La Boisdrotière stream,
downstream of point RU
CDR B, at the level of alavoir, southeast stream at
the level of the lavoir(2 different points).
Spot measurementsof uranium, 226Ra
and physical-chemicalparameters• Sediments: same sampling
points as for the water.
Spot measurements of 226Ra,
238
U and 210Pb

Site water• MIMAUSA programmein 2013:• Water: 4 sampling points- 3 points at the regulatory
monitoring points: RUCDRO,RUDIG and a little further
upstream from point RUDIGA).
- Other point : the
La Commanderie stream,at the foot of the mining
waste pile.
Spot measurementsof uranium and 226Ra• Sediments: 1 point(La Commanderie stream,at the foot of the mining wastepile), spot measurementsof radionuclides of theuranium-238 chain/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

FORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4
LA COMMANDERIE SITE

Monitored
environment or
nature ofinspection

Orano

Overgroundenvironment (foodchain)• Regulatory monitoring:• Soils and crops:- fields irrigated by water from theopen-pit mine- fields not irrigated by water fromthe open-pit mine-> composite soil and crop
samples per crop variety (annual
measurements: Uby weight by gamma
spectrometry)• From 2017: beef (adult cattle, bornand reared on site), every 3 years,
measurements of the 238U, 230Th,
226
Ra, 210Pb and 210Po• Monitoring at the operator's
initiative: beef (cattle fed withirrigated maize), measurements ofthe 238U, 230Th, 226Ra, 210Pb and 210Po

IRSN

DREAL and ASN

FIGURE 2 / MAP OF LOCATIONS OF SAMPLES LINKED TO THE REGULATORY MONITORING IN THE IMMEDIATE ENVIRONMENTOF THE LA COMMANDERIE SITE
Mining site footprint: Source Orano

287

La
Bo
i
str sdroea tièm re

RUDIG ACDRS1

CDR A2ore
processing
residues
storage

CDR IRRUCDR

RUCDR OCDR A1RUCDR ALa
Com
str maea nde
m ri
e

CDRO

RUDIG

CDRIR

CDRIR
RUBLA

CDR B2

CDR O

Sampling ofsite water

SERPA

Sampling:
surface water and sediments

RUDIG A

Sampling of
surface water

CDR IR

Inspection of food chain(soils and associated crops)

Footprint of old mining zone

CDR A1

New monitoring points (2017)
in redRADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Influence of the La Commanderie site
on its environment
Surface water

The two monitoring points considered as upstreamof the site, one in the La Boisdrotière stream(point RUDIG A), the other in the La Commanderie
stream (point RUCDR A, cf. figures 2 to 4) present
different average values, with higher averagevalues in the La Commanderie stream (pointRUCDR A):
• RUDIG A: U = 6.6 µg/L and 226Ra = 42.3 mBq/L;• RUCDR A: U = 17.5 µg/L and 226Ra = 173 mBq/L.

The various spot measurement campaigns(cf. figures 3 et 4) also show values globally higher
at point RUCDR A than at point RUDIG A. One of
the theories put forward is that point RUCDR A
is probably already under the influence of themine. The new monitoring points located further
upstream on the La Commanderie stream (points
CDR A1 and CDR A2, cf. figure 2) will enable thistheory to be verified.
The measurements made in the La Boisdrotière
downstream of the site revealed average valuesof uranium concentration and radium-226 activity(U = 19.9 µg/L and 226Ra = 74.7 mBq/L at point
RUDIG, cf. figure 3) approximately 1.5 to
3 times higher than upstream (point RUDIG A).

FIGURE 3 / URANIUM CONCENTRATION (µg/L) AND RADIUM-226N ACTIVITY (mBq/L) MEASURED BETWEEN 2009 AND 2016
IN THE LA BOISDROTIÈRE STREAM

100
10
1

Jan-09

May-10Sept-11

Feb-13June-14

Nov-15Ra (mBq/L)
10,000

226

1000
100
10
1
Jan-09Mar-09
May.-09
Jul-09Sept-09
Nov-09Jan-10Mar-10May.-10
Jul-10Sept-10
Nov-10Jan-11Mar-11
May.-11
Jul-11Sept-11
Nov-11
Jan-12Mar-12May.-12
Jul-12Sept-12
Nov-12
Jan-13Mar-13May.-13
Jul-13Sept-13
Nov-13Jan-14Mar-14May.-14
Jul-14Sept-14
Nov-14Jan-15Mar-15May.-15
Jul-15Sept-15
Nov-15Jan-16
Mar-16May.-16
Jul-16Sept-16
Nov-16288

U (µg/L)
1000

Regulatory monitoring data
La Boisdrotière stream
RUDIGA (La Boisdrotière stream - upstream)
RUDIG (La Boisdrotière stream - downstream)
Other
Emergence of a source at the foot of the waste pile

Decision thresholds
Spot measurements(random checks 2009, 2010 and MIMAUSA)La Boisdrotière stream
At point RUDIGA (La Boisdrotière stream - upstream)
At point RUDIG (La Boisdrotière stream - downstream)/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

FORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4
LA COMMANDERIE SITE

The existence of a source located at the foot of
the waste pile (point CDRS1, cf. figures 2 and 3),
which presents the highest measurements aroundthe site, could explain the increase in the values
recorded downstream of the site at the level of the
La Boisdrotière stream.

For the La Commanderie stream (cf. figure 4),
the high values of uranium concentration andradium-226 activity at point RUCDR A, potentiallyalready under the influence of the mine asindicated previously, do not make it possible todetermine a clear trend downstream of the site.

FIGURE 4 / URANIUM CONCENTRATION (µg/L) AND RADIUM-226N ACTIVITY (mBq/L) MEASURED BETWEEN 2009 AND 2016
IN THE LA COMMANDERIE STREAM AND IN THE OPEN-PIT MINE

U (µg/L)
90
80
70
60
50
40
30
20
10
0
Jan-09

May-10Sept-11

Feb-13Jun-14

Nov-15May-10Sept-11

Feb-13Jun-14

Nov-15Ra (mBq/L)

226

900
800
700
600
500
400
300
200
100
0
Jan-09Regulatory monitoring data
La Commanderie stream
RUCDRA (La Commanderie stream - upstream)
RUCDRO (canal feeding the open-pit mine)RUCDR (La Commanderie stream - downstream)

Other
Water of the open-pit mine (CDRO)

Spot measurements(random checks 2009, 2010 and MIMAUSA)La Commanderie stream
At point RUCDRA (La Commanderie stream - upstream)
At point RUCDRO (canal feeding the open-pit mine)
At point RUCDR (La Commanderie stream - downstream)

Other
Water of the open-pit mine (CDRO)RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /289

Food chain

Part of the food chain around the La Commanderiesite is subject to monitoring of the foodstuffs
irrigated by the water from the mine. For this,measurements are made in:• the irrigation water (during the pumping
periods);• the irrigated soils along with the associatedcrops (maize and potatoes);• the beef (from cattle fed with the maize).

The radium-226 and thorium-234 activity levels
measured in the maize are low (cf. figure 7):

Furthermore, the water from the open-pit mines
used for irrigation must comply with the following
values:• for radium-226, between 0.003 (decisionthreshold) and 0.024 Bq/kg fresh for nonirrigated maize and < 0.25 (decision threshold)and 0.58 Bq/kg fresh for irrigated maize;• The pH must be between 5.5 and 8.5.
• The uranium and the radium-226 must,
respectively, be less than 1800 µg/L (in solubleform) and 370 mBq/L (in soluble form).

290

measured in the soils of the maize fields both
irrigated and not irrigated with the water from theopen-pit mine are of the same order of magnitude,
except for the year 2016, when the irrigatedsoil presented an activity per unit mass of 234Th(corresponding to the 238U) considerably higher
than in previous years (cf. figure 6), despite no
significant increase in the uranium content of the
open-pit mine waters being observed that year.

The measurements in the irrigation water show
uranium concentration between 7 and 39 µg/L andradium-226 activity between 80 and 270 mBq/L(cf. figure 5). These values are consistent withthose deriving from the monitoring of the open-pit
mine water, with its average uranium concentrationof 27.6 µg/L and average radium-226 activity of
145.7 mBq/L (Point CDRO, cf. figure 4).

• for thorium-234, the measurements are all
below the decision threshold (< 0.02 Bq/kg fresh)for non-irrigated maize, and the irrigated maize
presents a single significant measurement
equal to 0.004 Bq/kg fresh.
The activity per unit mass of the radionuclides
measured in the beef of cattle fed with maize
irrigated with the water from the open-pit mineare for the most part below the decision threshold(cf. figure 8).

The activity per unit mass of the radionuclides

FIGURE 5 / URANIUM CONCENTRATION (µg/L, left axis) AND RADIUM-226 ACTIVITY (mBq/L, right axis)
MEASURED IN THE WATER OF THE OPEN-PIT MINE USED FOR IRRIGATION BETWEEN 2009 IN 2016

Ra (mBq/L)
300

U (µg/L)
45

226

40

250

35
30

200

25

150

20

100

15
10

50

5
0
Dec-08May-10Sept-11Jan-13
Uranium

Jun-14
Ra

226/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

Oct-150
Mar-17

FORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4
LA COMMANDERIE SITE

FIGURE 6 / ACTIVITY PER UNIT MASS OF 234Th (corresponding to the 238U) AND OF 226Ra MEASURED IN THE IRRIGATED SOILS(maize crop) AND NON-IRRIGATED SOILS (maize crop) WITH THE WATER FROM THE OPEN-PIT MINE BETWEEN 2009 AND
2016 (Bq/kg dry)

Bq/kg dry
1000
900
800
700
600
500
400
300
200
100
0

2009

2010

2011

2012

2013

2014

2015

2016

Decision thresholds
Soils not irrigated with waterfrom open-pit mine
Measured value
234
Th

Soils irrigated with waterfrom open-pit mine
Measured value
234
Th

Ra

Ra

226

226

291

FIGURE 7 / ACTIVITY PER UNIT MASS OF 234Th (corresponding to the 238U) AND OF 226Ra MEASURED IN THE IRRIGATED SOILS(available data: 2009-2016) AND NON-IRRIGATED SOILS (available data: 2012-2016) WITH THE WATER FROM THE OPEN-PITMINE (Bq/kg fresh)

Bq/kg fresh
0.2
0.18
0.16
0.14
0.12
0.10
0.08
0.06
0.04
0.02
0

2009

2010

2011

Maize not irrigated with waterfrom open-pit mine
Measured value234
Th (seuils de décision)
Ra

226

2012

2013

2014

2015

2016

Decision thresholds
Maize irrigated with waterfrom open-pit mine
Measured value
234
Th
Ra

226

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 8 / ACTIVITY PER UNIT MASS OF 238U AND OF 226Ra MEASURED IN BEEF BETWEEN 2009 AND 2016 (Bq/kg fresh)

Bq/kg fresh
1.8
1.6
1.4
1.2
1
0.8
0.6
0.4
0.2
0

2009

2010

2011

2012

2013

2014

2015

2016

Decision thresholds
292

Measured value
238
U
Ra

© IRSN226

La Porte former open-pit mine
/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

FORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4
LA PORTE SITE

La Porte site

Monitoring plan

The La Porte site is situated in the municipalityof Saint-Julien-aux-Bois in Corrèze. It is locatedalong the Riou-Tort river, downstream of several
other mining sites (the main ones being Galerie
des Biaurottes, Le Jaladis, La Clare and La
Besse, cf. figure 1). This site, which covers an
area of 6.5 ha and is located on granitic terrain,
was operated between 1982 in 1984 for open-pit
mining and produced 29.6 tonnes of uranium. The
site was redeveloped in the mid-1990s, and theflooded open-pit mine, property of Orano, is not
used and access to it is prohibited. The rest of thesite belongs to private landowners and is used for
pasturing.

The La Porte site is subject to regulatory
monitoring. The Orano monitoring plan ispresented below (cf. table 1 and figure 1), involving
the monitoring of the following:• the waters of the open-pit mine;• gamma radiation
La Porte village;

on

the

site

and

in

• air quality on the site and in La Porte village(radon and dust);• the aquatic environment around the site(the Riou Tort river).
In addition, spot analyses were also conducted,
in particular in the framework of random checks
or the MIMAUSA programme.

TABLE 1 / MEASUREMENTS MADE ON AND AROUND THE LA PORTE SITE

Monitored
environment or
nature of inspection

293
Orano

IRSN
• MIMAUSA programmein 2011:in the open-pit mine (atpoint POR4): spotmeasurements of uranium,
226
Ra and physical-chemicalparameters

DREAL

Site water• Regulatory monitoringin the open-pit mine (point
POR4): Quarterly
measurements of uranium,
226
Ra and pH• Random checks in 2012:
in the open-pit mine (atpoint POR4): spotmeasurements of uraniumand 226Ra

Gamma radiation• Regulatory monitoring:
2 measurement stations:
1 in La Porte village
and 1 on the siteAir(radon-222
and radon-220)• Regulatory monitoring:
2 measurement stations:
1 in La Porte village
and 1 on the site
Monthly measurements of the222
Rn PAEC, the 220Rn PAEC
and the dust

Continental aquatic
environment• MIMAUSA programmein 2011:
Water: 2 points (at the• Regulatory monitoring:open-pit mine, alongside point • Random checks in 2012:
Water: 2 sampling points (POR
POR B and upstream of the La
Water (at pointA
Porte site but downstream of
POR B): 1 point, spot
and POR B)
the Galerie des Biaurottes
measurement of uranium
Monthly measurements of thesite), spot measurements
and 226Ra
uranium, 226Ra and pHof uranium, 226Ra
and physical-chemicalparameters

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 1 / SURFACE WATERWAYS NETWORK IN THE PROXIMITY OF THE LA BESSE, LA CLARE, LE JALADIS,GALERIE DES BIAUROTTES AND LA PORTE FORMER MINING SITES - SAMPLING LOCATIONS LINKED TO THE
REGULATORY MONITORING OF THE LA PORTE SITE
Mining site footprint: Source Orano

Le Jaladis
Site

La Besse
Site

POR A

Rochette
streamGaleriedes Biaurottes
Site

Le

294

rt

To

ou

Ri

Le Riou-Tort

La ClareSite

La Porte
Village

La Porte
Site
Site

Le Jaladis
Site

POR 4

Galeriedes Biaurottes
La Porte
Site
Site

SITE

SITE air inspection (dosimeter + TLD)POR A Sampling: surface water
Mining site footprint/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

POR B

FORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4
LA PORTE SITE

Influence of the La Porte site
on its environment
Air quality and gamma radiation

For the period 2015-2017, the dose rate varied
between 160 and 260 nGy/h on the La Porte mining
site, and between 130 and 220 nGy/h at La Porte
village (cf. figure 2). These values are consistent
with the values generally observed on former
mining sites and in their granitic environment.
The average value for the dose rate for thismeasurement period is higher on the La Portesite (average: 213 nGy/h) than in La Porte village(average: 176 nGy/h). The average value observedon the site is probably due to the location of thedosimeter directly above a redeveloped mining
waste pile.
In the absence of a station measuring theimmediate natural environment of the site, Orano
has chosen to compare the potential alpha energy
concentration (PAEC) of the 222Rn measured as partof the monitoring with the values defined in theframework of the third-party expert assessment
conducted by IRSN for the 10-year environmental
report on the sites of the La Crouzille mining
division, for the three wind exposure situations(3).
Thus, the values measured on the La Porte site,
described with a "valley bottom"-type topographic
condition, were compared with the reference
value of 178 nJ/m3, and those of La Porte village,
described with a "hillside"-type topographic
condition, with the reference value of 154 nJ/m3(cf. figure 3). The results of the measurements for
2015-2017 on the La Porte site indicate an averagevalue of 336 nJ/m3 for the PAEC of 222Rn.
These measurements highlight the impact of themining operation on the PAEC of 222Rn at the La
Porte site, with the position of the site in the valley
bottom and the presence of mining waste on thesite favouring the accumulation of radon-222 at
the La Porte site. For La Porte village, the PAECof radon-222 is on average 77 nJ/m3 for theperiod 2015-2017. This value is below the chosenreference value of 154 nJ/m3.
295

FIGURE 2 / LOG OF DOSE RATE MEASUREMENTS MADE BETWEEN 2015 AND Q1 2017
ON THE LA PORTE SITE AND IN LA PORTE VILLAGE (nGy/h)

Dose rate (nGy/h)
300
250
200
150
100
50
0
Mar-15Jun-15

Sep-15

Dec-15

La Porte site

Apr-16

Jul-16Oct-16

Jan-17

La Porte village

3. 2007, IRSN, Expertise globale du bilan décennal environnemental d’AREVA NC (Global 10-year environmental expert study of AREVA NC),
Part 2, ref.: DEI/SARG/2007-042.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 3 / TIMELINE OF 222RN PAEC MEASUREMENTS MADE BETWEEN 2015 AND Q1 2017
ON THE LA PORTE SITE AND IN LA PORTE VILLAGE (nJ/m3)

PAEC 222Rn (nJ/m 3)
1000

100

10

1
Mar-15Jun-15

Sep-15

Dec-15

La Porte site (valley bottom)

Apr-16

Jul-16Oct-16

Jan-17

La Porte village (hillside)

Valley bottom reference (178 nJ/m )3

Hillside reference (154 nJ/m 3)© M.-O. Gallerand/IRSN

296

Old mining waste pile

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

FORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4
LA PORTE SITE

Surface water

The measurements made since 2010 at the point
located on the Riou-Tort river, upstream of themining sites and therefore outside of their influence(point POR A, cf. figure 1), reveal an average uranium
concentration of 1.4 µg/L and average radium-226
activity of 18.3 mBq/L (cf. figures 4 and 5).
These values are of the same order of magnitude as
those usually encountered in a natural environment
with the same geological context.

The highest radionuclide values in the waters aremeasured in the open-pit mine of the site with,on average, a uranium concentration of 76.7 µg/L
and radium-226 activity of 109.3 mBq/L (cf. figures
4 and 5). These high values, compared to thebackground radiation, probably derive from theleaching by the water of the granitic rock in which
the open-pit mine was excavated.

FIGURE 4 / TIMELINE OF URANIUM MEASUREMENTS MADE ON AND AROUND THE LA PORTE SITE (µg/L)

U (µg/L)
1000

100
297
10

1

Jul-10
Sep-10Nov-10Jan-11Mar-11
May-11
Jul-11
Sep-11
Nov-11
Jan-12Mar-12
May-12
Jul-12
Sep-12
Nov-12
Jan-13Mar-13May-13
Jul-13
Sep-13
Nov-13Jan-14Mar-14May-14Jul-14
Sep-14
Nov-14Jan-15Mar-15May-15
Jul-15
Sep-15
Nov-15Jan-16
Mar-16May-16
Jul-16
Sep-16
Nov-16
Jan-17Mar-170.1

Orano monitoring data
Le Riou-Tort - upstream of site (POR A)
Le Riou-Tort - downstream of site (POR B)
Open-pit mine (POR 4)

Decision thresholds
Spot measurements
IRSN (04/11)
DREAL (06/12)
Le Riou-Tort - downstream of site (POR B)
Le Riou-Tort - downstream of site
Open-pit mine
Open-pit mine

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /FIGURE 5 / TIMELINE OF RADIUM-226 MEASUREMENTS MADE ON AND AROUND THE LA PORTE SITE (mBq/L)
NB: 51.9% of the samples present radium activity below the decision threshold

Ra (mBq/L)
1000

226

100

10

298

Jul-10
Sep-10Nov-10Jan-11Mar-11
May-11
Jul-11
Sep-11
Nov-11
Jan-12Mar-12
May-12
Jul-12
Sep-12
Nov-12
Jan-13Mar-13May-13
Jul-13
Sep-13
Nov-13Jan-14Mar-14May-14Jul-14
Sep-14
Nov-14Jan-15Mar-15May-15
Jul-15
Sep-15
Nov-15Jan-16
Mar-16May-16
Jul-16
Sep-16
Nov-16
Jan-17Mar-170.1

Orano monitoring data
Le Riou-Tort - upstream of site (POR A)
Le Riou-Tort - downstream of site (POR B)
Open-pit mine (POR 4)

Decision thresholds
Spot measurements
IRSN (04/11)
DREAL (06/12)
Le Riou-Tort - downstream of site (POR B)
Le Riou-Tort - downstream of site
(Decision thresholds)
Open-pit mine
Open-pit mine

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

FORMER MINING SITES / 04
Detailed presentation of 4 former mining sites chosen for the radiological report / 4.4
LA PORTE SITE

The monitoring conducted since 2010 at point
POR B, located immediately downstream of
the La Porte site, reveals an average uranium
concentration of 2.3 µg/L, similar to thatmeasured at point POR A. The measurementsof radium-226 activity show greater variability,with values between 10 mBq/L and 150 mBq/L.
The fact that this variation is not observed atpoint POR A probably testifies to the influence ofthe past mining activities. However, on accountof the absence of a monitoring point immediately
upstream of the La Porte site, the current
monitoring does not permit these variations to be
attributed to the La Porte site alone, considering
the presence of other uranium mines also locatedin the Riou-Tort drainage basin.

© IRSN

299

Sampling sediments

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Atmospheric aerosols sampling station OPERA-AIR TGD 700 m3/h

© IRSN300/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

O5
DOSIMETRIC SUMMARY

AND NEWS ITEMS FOR THE
PERIOD 2015-2017
5.1. SUMMARY OF DOSIMETRIC ASSESSMENTS .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 302
 ETECTION OF IODINE-131 IN THE AIR
5.2. D
IN JANUARY AND FEBRUARY 2017 . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 305
 ETECTION OF RUTHENIUM-106 IN THE AIR
5.3. D
FROM LATE SEPTEMBER TO EARLY OCTOBER 2017. . . . . . . . . . . . . . . . . . 306
 VERVIEW OF THE RADIOLOGICAL MARKING
5.4. OOF THE RU DES LANDES ZONE . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 308

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /

301

O5

DOSIMETRIC SUMMARY
AND NEWS ITEMS FOR THE
PERIOD 2015-2017
5.1. SUMMARY OF DOSIMETRICASSESSMENTS302

On the thirty-six mainland French sites where basic
nuclear facilities (INB) are operated, twenty-eight
were able to undergo dosimetric assessments
based on radiological measurement results intheir environment. These measurements were
undertaken over the period 2015-2017, either
by the nuclear operators as part of regulatory
monitoring or in supplementary studies orderedby them, or by IRSN in the framework of its
environmental radiological monitoring mission.
Table 1 presents in summary form the estimateddoses due to the discharges from nuclear facilities
and to which the populations residing around thesites are exposed, and which are estimated basedon environmental measurements. This table canalso be used to compare these doses with thoseestimated in the previous Radiological Report which
covered the period 2011-2014. These estimations
are presented per radionuclide and per route of
exposure.
Persons living close to one of these nuclear sites
are likely to be concerned by exposure to theradionuclides measured in the air and issuingfrom atmospheric pollution: external exposure to
krypton-85 for persons residing around La Hague,
inhalation of uranium dust for the sites of Malvési,
Tricastin or Romans-sur-Isère, inhalation or
cutaneous transfer of tritium around the sites of
Valduc, Grenoble or Creys-Malville. This exposure
varies according to the scenarios and the distancefrom the site; the stated doses often correspondto the most conservative scenario (immediateproximity).
However, the doses linked to the incorporation ofradionuclides by ingestion of foodstuffs presenting
a measurable level of radionuclides (14C, 129I, 60Co,
plutonium and americium around La Hague,

C and 3H around the nuclear power plants, 3H
around Valduc, Grenoble or Creys-Malville, forexample) can only be received by persons likely
to consume the foodstuffs concerned. Theseestimated doses are therefore proportional to thequantities consumed.

14

It should be noted that, in the case of nuclear
power plants, the doses by ingestion of wateror freshwater fish can only concern persons
living close to a nuclear power plant situatedon the bank of a river. Conversely, the nuclear
power plants of the Manche department are
the only ones concerned by the consumption ofseafoods fished locally. In the particular case of
the Flamanville nuclear power plant, a person
consuming seafoods issuing from local fishingwould also be exposed to the liquid discharges
from the La Hague site, on account of its proximity.
Lastly, a person consuming water or fish from the
major rivers receiving the discharges from several
basic nuclear facilities (INBs) (Rhone, Garonne,
Loire, Meuse, Seine, Rhine and Moselle) may beconcerned to a lesser degree, even if the person
is situated far downstream of one or more INBs.
The doses likely to be received by the population
residing around French nuclear installations
and estimated based on measurement results
are very low. Thus, any person residing in thevicinity of a nuclear power plant, and who may
be prone to all the routes of exposure (regularly
consuming locally produced food, consuming
2 L/day of water from the river and several kg/yearof fish taken downstream of the site discharges),
would receive a dose of less than 1 µSv/year, i.e.:less than 1000th of the public exposure limit
set at 1 mSv/year (1000 µSv/year). The same
accumulated routes of exposure would lead,around La Hague, to a maximum dose of
8 µSv/year: the highest level estimated in thisreport but which is almost 400 times lower than/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DOSIMETRIC SUMMARY AND NEWS ITEMS FOR THE PERIOD 2015-2017 / 05
Summary of dosimetric assessments / 5.1

TABLE 1 / DOSES IN µSV/YEAR POTENTIALLY RECEIVED BY THE POPULATION RESIDING CLOSE TO THE NUCLEAR SITES,ASSESSED ON THE BASIS OF ENVIRONMENTAL MEASUREMENT RESULTS ACQUIRED AROUND EACH OF THESE SITES.
DOSES DUE TO NATURAL RADIOACTIVITY IN FRANCE.

Sites

La Hague

Malvési

Tricastin
Romans-sur-Isère
Marcoule

SaclayGrenoble (ILL)
Bruyères-le-Châtel
ValducNuclear power plant sites

Creys-MalvilleDownstream Rhone(all Rhone valley nuclear
installations)

Natural radioactivity

Dose (µSv/year)

Radionuclide and route of exposure

RR 2011-2014

RR 2015-2017

0.6 to 3.5

1.6 to 5.4 (1); 3.3 (2)

85

0.7

0.4

14

1.1

0.2

129

–

< 0.002

14

–

0.05

Kr – external exposure
C – ingestion of land-grown food and seafood
I – ingestion of land-grown food and seafood

C – inhalation
Sr – ingestion of milk

90

Co, plutonium and 241Am – ingestion of seafood

0.62

0.02

(3)

60

-

< 0.03

3

2–

Uranium – inhalation

0.4–

Uranium – ingestion of vegetables

–

0.002

Uranium – occasional ingestion of 1 L of water

–

0.01

Uranium – occasional ingestion of 1 kg of wheat

0.05

0.06

Uranium – inhalation

0.003

0.003

Uranium – occasional ingestion of 1 L of water

0.5

0.15

Uranium – inhalation

0.28

–

3

0.12

–

3

–

0.07

14

0.28

0.15

3

1.4

1.4

14

0.14

0.05

3

–

0.03

3

0.14

–

3

1.0

• 0.14 to 0.22: 3H – inhalation / skin absorption• 0.10 to 0.15: 3H – ingestion of food• 0.7: 3H – ingestion of water

0.39

H – inhalation, skin absorption and ingestion of foodH – inhalation, skin absorption
H – ingestion of foodC – ingestion of land-grown foodH – ingestion of food (and particularly water)
C – ingestion of lake fish

H – inhalation, skin absorption
H – ingestion of foodH – inhalation, skin absorption

C – ingestion of land-grown food0.1

0.05 to 0.075

14

0.12

0.007 to 0.2

140.01 to 0.7

0.04 to 0.5

3

–

0.003

3

–

< 0.001

14

0.08< 0.02110m

0.0004< 0.001

Co, 58Co, 110mAg… – exposure to the air: external andinhalation< 0.070.06

3

C – ingestion of river fish

H – ingestion of waterH – ingestion of land-grown foodC – ingestion of river fish
Ag – ingestion of sea fish60

H – inhalation, skin absorption

0.06

Miscellaneous radionuclides (4) – ingestion of water from the Rhone

0.4

14

310

Exposure to cosmic radiation

550

Frequent flyer

C – ingestion of fish from the downstream Rhone

360 – 1100

Exposure to terrestrial radiation

380 – 2500

Ingestion of natural radionuclides(maximum: heavy consumers of seafood)10
540 – 3150
300

Consumption of 200 g of mussels (210Po essentially)
Inhalation of radon (max = Lozère, Cantal…)
Heavy smokers(1) Based on the measured 85Kr activity levels. (2) Based on the dose rate measurements. (3) Shellfish only.
(4) This dose is calculated on the basis of the activity levels of all artificial radionuclides present in the water of the Rhone in dissolved form andmeasured by IRSN's SORA (Rhone observation station at Arles), after deduction of the background radiation. 80% of this dose is due to the tritiateddischarges from Rhone valley nuclear facilities, 17% from strontium-90 discharges and less than 3% from other radionuclides (mainly iodine-131
from hospital discharges and cobalt-60).

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /303

the average dose received annually by the French
population outside of any influence from a nuclear
facility, on account of the background radiation
present throughout France. These doses match
those estimated by calculation (modelling thedispersion and transfer of radionuclides in thevarious components of the environment, throughto Man) by the operators of the nuclear sites, basedon the actual discharge radioactivity (a summaryof these dosimetric impact calculations based on
the actual discharges from nuclear facilities ispresented in the annual report of the ASN on thestate of nuclear safety and radiation protection in
France, available from www.asn.fr).

304

Unlike the calculation estimations conducted by
the operators, which make it possible to take into
account all routes of exposure for the public andall discharged radionuclides, the environmental
measurements only enable assessment of the
preponderant exposure resulting from measurable
radiological marking in the environment. For
certain sites such as Valduc, Grenoble or CreysMalville, the doses due to tritium alone, estimatedon the basis of measurements conducted in theenvironment, represent the majority of the total
calculated dose for these sites, taking all routes of
exposure and all radionuclides into consideration.
In the case of La Hague or the nuclear power plants,
the doses presented in table 1 represent morethan 70% of the total dose that can be potentiallyattributed to the site. Lastly, in the case of Tricastin,inhalation of uranium dust represents almost 60%of the dose calculated by the operator (which takes
account of all potential exposure to radionuclides
discharged by the site's installations).
Knowledge of the radioactivity in the environment,
based on the various environmental monitoring
programmes of the French nuclear sites,
therefore makes it possible to estimate the main
doses likely to be received by the neighbouring
population. It also feeds into the validation of thecalculations conducted by the operators. Thisknowledge does not, however, derive solely from
regulatory monitoring. Supplementary studies
conducted at the initiative of IRSN or certain
operators also contribute to this.
The report shows that the doses estimated for theperiod 2015-2017 are for the most part entirely
concordant with those presented in the previous
Radiological Report, for the period 2011-2014.
This is the case in particular for the potential
doses around the nuclear power plants, aroundthe sites of Creys-Malville, Valduc, Saclay andTricastin, and for the doses due to carbon-14
and krypton-85 around the La Hague site. In thecase of the sites of Grenoble and Romans-surIsère, the reduction in the doses between the two
periods 2011-2014 and 2015-2017 is due to thedrop in discharges. In the case of Marcoule orBruyères-le-Châtel, the reduction in discharges
was such that the environmental radiation cannot
for the most part be measured (below the decisionthresholds), so that it is no longer possible tocalculate any doses. Around Malvési, the doses
linked to the inhalation of uranium dust were able
to be calculated for the previous report based on
measurements made during the specific study
conducted by IRSN. Since this study has not been
repeated, and pending the upcoming installationof a permanent sampling station close to thissite, this dose could not be assessed. However,
the activity levels in the plants, of the same orderof magnitude as in the previous period, testify
to the fact that the activity levels in the air andtherefore the associated doses have also beenof the same order of magnitude. Furthermore,certain data that were not used in the dosimetricevaluations for the previous report did get used inthis one. Lastly, some deviations can be explainedby changes to the usable set of data or the way
in which this data set is used. Hence, for the La
Hague site, only the ingestion of molluscs could
be taken into consideration with regard to theincorporation of certain radionuclides, the activity
levels of which could only rarely be measured in
the other seafoods.
Just as with the previous Radiological Report, thedoses could not be estimated around certain
sites whose discharges had too insignificant an
influence on the environment to be quantifiable
by measurement. This concerns the sites of
the French Navy (Cherbourg, Toulon, Brest),
Fontenay-aux-Roses, Cadarache and Brennilis,
and CSA-Cires, to which has also been recently
added the site of Bruyères-le-Châtel. For thesesites, the doses estimated by the operatorsfor calculation on the basis of radiation fromdischarges, taking into account all routes of
exposure and radionuclides, are lower - in somecases far lower - than 0.1 µSv/year (with the
exception of the Cadarache site, for which thedose of 1.5 µSv/year, estimated by the CEA, ismainly due to the additional emanation of radon,
for which the measurements are not available
in the RNM (national network for radioactivity
measurement in the environment)).

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DOSIMETRIC SUMMARY AND NEWS ITEMS FOR THE PERIOD 2015-2017 / 05
Detection of iodine-131 in the air in January and February 2017 / 5.2

Lastly, the chapter relating to the former mining
sites is not subject to dosimetric assessmentsin the framework of this report. There are threemain reasons for this choice: (1) the radioactivity
levels measured in the environment aroundthese sites relate for the most part to thebackground radiation, which may potentially belocally reinforced; (2) the available measurement
results, in particular for dose rate and radon,
are not for the most part discernible in thisbackground radiation on account, in part, of therelatively imprecise knowledge we have of its
variability (summarily illustrated in chapter 2);(3) in the case of surface waters and fish, theanalysis results available from monitoring would
only enable very partial doses to be estimated.

5.2. DETECTION OF IODINE-131
IN THE AIR IN JANUARY ANDFEBRUARY 2017
Traces of particulate radioactive iodine (1) (131I)
were detected in the atmosphere of a dozen or
so European countries between mid-January
and the end of February 2017. In all, around 40
detections were signalled over a period of eightweeks by 20 monitoring stations spread around
Europe. The concentrations of this nuclear
fission product remained very low (between 0.1
and 10 μBq/m3) and did not lead to any significant
health impact (cf. figure 1). Nevertheless, IRSN
has looked into the various reasons that enabledthese detections to be made. One reason is the

FIGURE 1 / COMPILATION OF IODINE-131 LEVELS IN THE FORM OF AEROSOLS IN THE AIR (value in µBq/m3 and dates)
Source: IRSN

305

1. Adsorbed on aerosols or present in the form of nanoparticles.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /considerable improvement in the performanceof the atmospheric dust collection stations (interms of sampling rate) and of the metrology.
It is likely that, considering the levels observed,
this episode would have gone undetected only
a decade ago. IRSN also reviewed the different
types of facility authorised to discharge thisradionuclide, and classified them according
to their expected contribution in a situation of
normal operation. These are the discharges of theradiopharmaceuticals industry, and in particular
those of an institute situated at Obninsk, around200 km south-south-west of Moscow, whichappear to be the most likely contributors to theactivity levels measured across Europe, far aheadof the incinerators of the wastewater purification
stations situated downstream of the nuclear
medicine services, and in last place the discharges
from nuclear power plants (2).

306

Reconstitution of the air mass trajectories
associated with these detections also indicate
a source of radiopharmaceuticals iodine (usedin particular for diagnosing and treating thyroid
cancers) as being the most probable and mostsignificant source. The poor conditions ofatmospheric dispersion that prevailed at this periodof the year over Europe contributed significantly tothe increase in the concentrations in the air by afactor of 4 to 5 for the daily average of particulatematter in the air (PM10(3) and PM2.5(4)) and theradionuclides of natural origin (7Be, 210Pb, 40K),
and facilitated the detection of the iodine-131. The
winter weather conditions characterised by strong
inversions of the vertical temperature gradient in
the lower layers of the atmosphere are known forgenerating episodes of atmospheric pollution.
Iodine is a volatile species whose presence in theatmosphere is divided into gaseous form (around¾) and particulate form (around ¼) throughadsorption of part of the gaseous species onaerosols. Except for a station in Italy equippedwith a high flow-rate iodine sink, no other gaseousiodine value higher than the detection limits wasmeasured for the gaseous fraction, despite its
predominance. The reason for this derives fromthe far higher flow rate of the aerosol samplers,
enabling far lower detection limits for theiodine-131 in particulate form.

Despite being of shorter duration, simultaneous
detections of this radionuclide on the European
continent had already occurred between
September and October 2011, originating fromthe Isotopes Institute in Hungary responsible forthe radiopharmaceutical production of iodine-131.
Other episodes affecting several European
countries are to be signalled in February 2012,
December 2013, March and May 2015 and, more
recently, in January and February 2018. Besides
improvements in the conditions of sampling andmeasurement, radiopharmaceutical industry
production is increasing to face a growing demandin the number of diagnostics and treatments using
iodine-131. This has resulted in an increase in theemissions and detections.

5.3. DETECTION OF
RUTHENIUM-106 IN THE AIR
FROM LATE SEPTEMBERTO EARLY OCTOBER 2017
Between late September and early October
2017, around 250 monitoring stations conducting
aerosols collection and spread around most ofEurope signalled the detection of ruthenium-106
in the atmosphere. The map at the top of figure
2 indicates the activity concentration ranges(a circle may represent several stations).
This radionuclide of artificial origin had neverbeen observed on a continental scale since
the Chernobyl disaster. In France, 9 of the
45 aerosol collection stations of the IRSN OPERAAIR network recorded activity by unit volumelevels for ruthenium-106 of between 0.17 and46 µBq/m3. These very low activity by unit volumelevels generated no health concerns. Dependingon the country, the sampling period ranged fromless than one day to one week, or even one monthin certain cases. The shortest periods were able
to demonstrate that in a given location the plume
had remained for between one and three days on
average. The shortest periods of presence wereobserved in eastern Europe and the longest in
western Europe. These extended to up to 6 days
in Italy on account of local stagnation of the air
masses. The highest value (176 mBq/m3), not

2. Masson et al. (2018) Potential source apportionment and meteorological conditions involved in airborne 131I detections in January/February 2017
in Europe. Environ. Sci. Technol. 2018, 52, 8488−8500.
3. P
 articles in suspension in the air, with an aerodynamic diameter of less than 10 µm.
4. P articles in suspension in the air, with an aerodynamic diameter of less than 2.5 µm.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DOSIMETRIC SUMMARY AND NEWS ITEMS FOR THE PERIOD 2015-2017 / 05
Detection of ruthenium-106 in the air from late September  to early October 2017 / 5.3

FIGURE 2 / ACTIVITY BY UNIT VOLUME OF RUTHENIUM-106, RAW (left map) AND CORRECTED FOR AN AVERAGE 7-DAY
PRESENCE PERIOD FOR THE PLUME (right map)
Source: IRSN.

307

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /The radiological marking of the Ru des Landes
goes back some years: it is known to the ASN
and the CLI (first exchanges of correspondence in1995 between CSPI [CLI] and DSIN [ASN today]).
It is subject to regulatory radiological monitoring
conducted by Orano, which has since been
reinforced. Nevertheless, the operator on the one
hand and IRSN on the other conducted a new study
in 2016 and 2017 aimed at better characterising
the radionuclides and the radiological activity
encountered, and determining the origin and extent
of the contamination observed. These sampling and

es s

trea

m

FIGURE 3 / NORTH-WEST ZONE OF THE ORANO SITE AT LA HAGUE

et

zo

ne

Detection on a continental scale, and at theselevels, suggests that the source term wassignificant. IRSN estimated the discharge
at between 100 and 300 TBq, which cannot
correspond to a discharge from an installation innormal operation. Only ruthenium was detected,
which also makes it possible to exclude an accident
in a nuclear power plant. The exact location of thedischarge is unknown, but the various trajectories
of air masses in the days preceding the detectionsin the various European stations suggest that theemission location would be between the Ural andthe Volga. To date, no IAEA Member State has
declared any accident on its territory.

On 10 October 2016, ACRO (Association for theinspection of radioactivity in western France)
published a press release reporting on thepresence of americium-241, caesium-137,
cobalt-60 and iodine-129 in the sediments andaquatic mosses sampled at the Ru des Landes("Landes stream") source situated to the northwest of the Orano establishment at La Hague.

W

308

5.4. OVERVIEW OF THE
RADIOLOGICAL MARKING OF
THE RU DES LANDES ZONE

Land

corrected for the period of the plume's presence,
was recorded in just one day at a station insouthern Romania. To be able to compare theseresults obtained over variable sampling periods,
all the levels were averaged over seven days. The
data corrected in this way (cf. figure 2, bottommap) show that the highest ruthenium-106 activity
levels were distributed randomly between the
countries of central Europe (Romania, Hungary,
Serbia, Bulgaria) and eastern Europe (southern
Ukraine and southern Russia). According to theRussian weather agency, the situation in southern
Ural during the period from 25 September to 6
October was due to a vast anticyclone centredaround the White Sea (to the south of the Kola
Peninsula), almost closed in by the anticyclone in
the central part of western Siberia. The conditions
for an active transfer of air masses and pollutantsfrom the territory of the southern Urals andsouthern Siberia to the Mediterranean region thento northern Europe began in the southern part ofwestern Siberia, then the Caspian Sea plain andthe northern Caucasus.

Drinking troughResurgenceNorthwest zone of ORANO site

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DOSIMETRIC SUMMARY AND NEWS ITEMS FOR THE PERIOD 2015-2017 / 05
Overview of the radiological marking of the Ru des Landes zone / 5.4

measurement campaigns also made it possible
to provide supporting information for the IRSN
act of referral from the French Nuclear Safety
Authority (ASN) concerning the technical noterequested of Orano by the ASN in December 2016
(IRSN/2017-00136 notice of 20/04/2017), and thezone rehabilitation report filed by the operator in
July 2017 (notice 2017-00376 of 04/12/2017).
In the framework of this report, IRSN on the one
hand and Orano on the other conducted a large
number of additional samples and analyses. IRSN
carried out, in particular, five missions involving
six laboratories, running between October 2016
and July 2017. These campaigns involved the useof varied and complementary resources: on-board(car-mounted) and in-situ gamma spectrometry,sampling of the water, the soil, the grasses, thesediments and the aquatic plants (representing
more than 120 analysed samples and more than
200 measurements). Together, they enabled theentire zone to be covered.

By analysing the data obtained, and in particular
the spatial distribution of the activity levels overthe zone, it is possible to observe how different
radionuclides behave differently.
The caesium-137 is distributed relatively
homogeneously and uniformly over the entire zone,
with values nevertheless higher close to the drinking
trough. Marking is also to be noted however further
away, to the north of the wet zone and on the edgeof a field to the west of the zone, with single points
also observed using mobile and in-situ gamma
spectrometry. Concerning the aquatic environment,
the levels of caesium-137 observed in the sediments
are lower, and all the measurements in the watersof the Ru are below the decision thresholds. IRSN
estimates for its part that these characteristic
elements tend to point toward an old atmosphericorigin of the deposit, linked to leaks observed in 1974
from blocks of concreted waste stored in the open
air to the north-west of the site and deriving from theactivities of the Elan IIb workshop (production of 90Sr
and 137Cs sources, which ceased in 1973).

FIGURE 4 / SAMPLING DONE BY ACRO, IRSN AND ORANO FOR THE ZONERADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /309

These cesium-137 activity levels should be placedin the context of those observed in the soils: in theorder of 6 Bq/kg dry in the Omonville zone and 2 to
6 Bq/kg dry in the Manche department.
The markings observed in plutonium aresignificantly more localised and observed almost
exclusively in the aquatic environment, in particularin the sediments, with values higher than the local
background radiation, including around the site (inthe order of 0 to 2 Bq/kg dry in the sediments). The
only significant value observed for plutonium-238
and plutonium-239+240 in the soils is situated in
the immediate proximity of the drinking trough,and could therefore be explained by a directtransfer from this trough to the surrounding
soil. It may also be noted that the sediments(point to the north of the drinking trough) andthe grass (point to the south-west) sampled at a
distance from the flow do not present a significant
plutonium value. Based on these supplementary

310

elements and analyses, IRSN concluded, as did
the operator, that the water table was marked
with alpha emitters (plutonium and americium).
For the sedimentary component, the study ofthe observed levels of americium and plutonium
in the sediments show a correlation between
the two radionuclides, and therefore a common
source. The reports on the isotopic activity
levels assessed by the various parties who haveconducted measurements in the zone (ACRO,IRSN and ORANO) show that these levels derivefrom historic activities for reprocessing spent
fuels from the old natural uranium / graphite /gas (UNGG) reactor system.

FIGURE 5 / ACTIVITY RANGES OF CAESIUM-137 AND AMERICIUM-241 MEASURED IN THE SOILS (Bq/kg dry)

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DOSIMETRIC SUMMARY AND NEWS ITEMS FOR THE PERIOD 2015-2017 / 05
Overview of the radiological marking of the Ru des Landes zone / 5.4

FIGURE 6 / ACTIVITY RANGES OF PLUTONIUM-239+240, AMERICIUM-241 AND STRONTIUM-90 MEASUREDIN THE SEDIMENTS(Bq/kg dry)

311

Concerning americium-241, a dual geographicalcoincidence is observed with, on the one hand,plutonium in the aquatic environment and, on theother, the highest values of caesium in the soils.
Input via two distinct channels is therefore to beenvisaged:• airborne, in similar fashion to caesium but
via different types of waste (blocks issuingfor example from AT1 on which cracks had
been detected in 1979), or else, under certain
conditions, via run-off from the plots situated tothe east;• aquatic, such as for plutonium, with very highlocalised values (in the sediments, for example,
with more than 10 times the activity levels
observed elsewhere around the establishment
and less than 5 Bq/kg dry).

The levels observed in the water and sediments
and the distribution of the strontium-90 show that
this is the primary input channel, with levels higher
by a factor of 2 to 3 in the water and by more than
10 in the sediments, compared to those usuallyobserved in the environment, including around
La Hague. Furthermore, bioaccumulation in themosses of the drinking trough and the aquaticplants of the wet zone, associated with the highmobility of strontium in this type of matrix, wereobserved. However, the presence of strontium inthe grass sampled to the south of the plot adjacentto the site and to the drinking trough could havethe same origin as that of the caesium.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /TABLE 2 / SUMMARY OF THE MEASUREMENT RESULTS ACQUIRED FOR THE RADIOLOGICAL CHARACTERISATION
OF THE RU DES LANDES AND AVAILABLE IN THE RNM

Fresh
water
(Bq/L)

Cs

137

Number of values < DT

35

Number of significant values

0

Pu

312

Am

241

Sr

0

6

2

8

16

142

2.10

0.648

1.29

0.584

Maximum value

0.598

51.6

7.50

45.2

550

0.598

26.9

4.30

3.85

27.8

4

1

0

1

10

0

1

0

1

1

4

4

Minimum value

0.001

0.381

0.286

0.464

1.15

Maximum value

0.001

0.381

0.286

15.6

3.57

Mean value

0.001

0.381

0.286

2.84

2.26

Number of values < DT

3

1

0

0

6

0

Number of significant values

2

0

1

2

8

4

Minimum value

0.001

4.00

0.013

0.857

14.4

Maximum value

0.004

4.00

3.31

174

40.2

Mean value

0.002

4.00

1.66

3.98

26.2

Number of values < DT

28

2

0

2

12

77

Number of significant values

1

0

4

8

8

58

Minimum value

0.001

8.92

8.80

0.356

0.40

Maximum value

0.001

28.0

25.0

97.8

198

Mean value

0.001

11.5

14.0

17.4

1.90

0

0

0

0
0

Number of values < SD
90

1

1

Number of significant values

239+2402

0.598

Mean value

Pu

0

Soils
(Bq/kgdry)

Minimum value

Number of values < DT
238

Aquatic
GrassesMosses
Sediments
plants (Bq/
(Bq/kg dry) (Bq/kg dry)
(Bq/kg dry)kg dry)00Number of significant values

35

1

1

2

6

Minimum value

0.008

10.3

221

29.4

1.45

Maximum value

3.13

10.3

221

963

323

Mean value

0.77

10.3

221

497

107

All these elements led IRSN to identify at least
three potential modes of transport in its notice2017-00136 of 20/04/2017:• transfer through the water table via its
resurgence, possibly resulting from aphenomenon of water-borne pollutants(plutonium and americium in particular) at very
low concentrations and progressive fixation ofthese pollutants in the soils traversed;• airborne transfer, explaining a more generalised
and homogeneous distribution, for example of
caesium-137;• transfer by run-off, in particular in the eventof strong rainfall, from the land situated in
immediate proximity to the source of the Ru desLandes, and presenting marking of the soils, inparticular with caesium-137 and americium-241.
In order to obtain additional information and be
capable of assessing the impact on foodstuffs
that may come from the zone in question (withcertain fields open to livestock in the immediateproximity of the drinking trough), a milk sample
was taken by the French General Department ofFood (Direction générale de l’alimentation - DGAL)
and analysed by IRSN. All the measurements
made using gamma spectrometry on this sample/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

DOSIMETRIC SUMMARY AND NEWS ITEMS FOR THE PERIOD 2015-2017 / 05
Overview of the radiological marking of the Ru des Landes zone / 5.4

were below the decision threshold, and the 90Sr
activity was 0.135 ± 0.017 Bq/L, within the highbracket of the analyses conducted on the milk of
the establishment at La Hague. This activity would
lead to an effective dose for an adult consuming
this milk of 0.1 µSv/year.

FIGURE 7 / NEW MONITORING PLAN
IMPLEMENTED BY ORANO

Orano decided to withdraw the most marked
land at the level of the resurgence deriving fromthe Ru des Landes, and to lower the water table
upstream of the site by means of two boreholes
so as to avoid any fresh input of artificial
radionuclides as the source of this marking, andimplement a programme of additional reinforced
monitoring as presented in the figure and tablebelow. These investigations are intended inparticular to guarantee and confirm the absenceof any changes to the marking for this zone. This
monitoring programme has already been running
for approximately one year. The report associatedwith these investigations is currently being drawn
up by the ASN.

© IRSN

313

Drinking trough

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /

© DR

314

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

O6
UNDERSTANDING

RADIOACTIVITY
AND THE POSSIBLE
EFFECTS OF EXPOSURE
ON THE HUMAN BODY
6.1. RADIONUCLIDES. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 316
6.2. RADIATION.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 317
6.3. ACTIVITY: THE BECQUEREL (Bq) .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 317
6.4. HALF-LIFE .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 318
6.5. MODES OF EXPOSURE TO ENVIRONMENTAL RADIOACTIVITY. . 318
6.6. DOSE: THE SIEVERT (Sv).  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 320
6.7. RADIATION PROTECTION. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 323

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /

315

O6

UNDERSTANDING
RADIOACTIVITY
AND THE POSSIBLE
EFFECTS OF EXPOSURE
ON THE HUMAN BODY
6.1. RADIONUCLIDES

316

Matter consists of molecules, which are
combinations of the atoms of different chemicalelements: atoms of carbon, hydrogen, potassium,
calcium, iron, lead, uranium, etc. An atom
is composed of a central nucleus consisting
essentially of protons and neutrons, with asurrounding cloud of electrons (cf. figure 1).

Each of the chemical elements may present
different nuclei, some of which are radioactive.
These are radionuclides (or radioactive
isotopes). Hydrogen has one radionuclide:tritium. The radionuclides of carbon include
in particular carbon-14. Caesium-134 andcaesium-137 are two of the 15 known isotopes of
caesium. Certain very heavy chemical elements
such as uranium or plutonium do not have any
stable nucleus, only radioactive nuclei.

Certain atomic nuclei are unstable - radioactive - ,and transform spontaneously into other nuclei: wecall this decay or disintegration.

FIGURE 1 / SCHEMATIC REPRESENTATION OF A CARBON-14 ATOM

Nucleus:
6 protons
8 neutrons

6 electrons/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

UNDERSTANDING RADIOACTIVITY AND THE POSSIBLE EFFECTS OF EXPOSURE ON THE HUMAN BODY / 06
ACTIVITY: THE BECQUEREL (Bq) / 6.3

6.2. RADIATION
When an atom disintegrates it can emit different
types of radiation. This radiation may strip
electrons from the atoms of the matter receiving
it, and in this way ionise this matter. This is why
this radiation is called "ionising".
The main types of ionising radiation deriving fromthe disintegration of radionuclides are as follows(cf. figure 2 and table 1):• alpha radiation consisting of a stream of helium
nuclei (formed by two protons and two neutrons);
they can be stopped by a simple sheet of paper;•beta radiation, consisting of a stream ofelectrons; they can be stopped by a sheet ofaluminium foil;• X and gamma electromagnetic waves; themost energetic can only be stopped by extreme
thicknesses of lead or concrete.

FIGURE 2 / PATH OF DIFFERENT TYPES OF RADIATION

Alphaparticles
X- andgamma rays

Beta
particles

Sheetof paper
Aluminium
sheet

Thick
concreteor leadshielding

6.3. ACTIVITY: THE BECQUEREL (Bq)
The activity of a radionuclide is the number ofnucleus decays it produces per second (1 Bq= 1 decay per second). Since the number ofdecays per second is proportional to the numberof radioactive atoms, the activity of a radionuclide
corresponds to a quantity of this radionuclide.
To quantify the radioactive discharges from anuclear facility, since the becquerel is a verysmall unit, multiples are used: kilo-becquerel
kBq (= 1000 Bq), mega-becquerel MBq (=1,000,000 Bq), giga-becquerel GBq (= 1000 MBq),
tera-becquerel TBq (= 1000 GBq).

In the environment, activity is often stated inrelation to a mass or volume. Activity per unit
volume (Bq/L or Bq/m3) (activity concentration)or activity per unit mass (Bq/kg) (specific activity)of a radionuclide in a sample of material is ameans of expressing the radionuclide content
of the sample. Activity levels in the environment
are often very low, and we use sub-multiples: forexample, milli-becquerel per kilogram mBq/kg(= 0.001 Bq/kg), micro-becquerel per cubic meterµBq/m3 (0.000001 Bq/m3).
By measuring the activity of radionuclides via theradiation that they emit it is possible to detect tinyquantities (masses) of radioactive matter. Hence, aspecific activity of 600 becquerels of caesium-137
per kilogram corresponds to a caesium content
of 0.00000086 gram (0.86 micrograms) of
caesium-137 per tonne.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /317

6.4. HALF-LIFE
The disintegration of an atom generates either theformation of another radioactive atom (anotherradionuclide), or the production of a stable atom
(non-radioactive). This therefore generates a
reduction in the activity of the radionuclide inquestion.

This varies according to the radionuclide froma fraction of a second to billions of years.
Uranium-238 has a half-life of nearly 4.5 billion
years. It is this long half-life which explains
why it can still be found on Earth in its natural
condition. The half-life of uranium-235 is almost
700 million years; this explains why, compared touranium-238, relatively little is still found in nature(it only constitutes 0.7% of natural uranium).

The radioactive period, or half-life, of aradionuclide is the time required for the activity(number of becquerels) of a radionuclide to be
reduced by half (cf. figure 3 and table 1).

FIGURE 3 / GRAPHIC REPRESENTATION OF RADIOACTIVE DECAY

Activity (%)
100

318
50

25
12.5
0

0

1 period

2 periods

6.5. MODES OF EXPOSURE
TO ENVIRONMENTAL
RADIOACTIVITY
A person can be exposed in several ways to theradioactivity present in the environment.
If the person is exposed to a radiation source
external to them, the air or the soil for example,
the exposure is external. This exposure essentiallyconcerns X or gamma-ray emitter radionuclides,
as this kind of radiation travels far through the

3 periods

4 periods

air and can penetrate deep into the body (cf.
figure 2). Exposure is low for pure alpha emitting
radionuclides (without gamma emission, suchas 238Pu or 239+240Pu for example) or for pure,
low-energy beta emitters (such as tritium andcarbon-14) which are stopped by the skin. External
exposure diminishes very quickly as the distanceincreases from the source, and ceases if you are
far enough away.
If the radionuclide penetrates the body throughinhalation or ingestion, exposure is internal.
This exposure will persist until the radionuclide/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

UNDERSTANDING RADIOACTIVITY AND THE POSSIBLE EFFECTS OF EXPOSURE ON THE HUMAN BODY / 06
Modes of exposure to environmental radioactivity / 6.5

disappears through radioactive decay or iseliminated from the body. This elimination can bevery rapid (as with tritium eliminated with water)or very long (as with plutonium, which settles
in particular in the bones). This exposure isparticularly damaging from alpha emitters, whosevery energetic radiation strikes the cells of living
tissues situated in the immediate proximity of theplace in the body where they have settled.

FIGURE 4 / HOW A PERSON IS EXPOSED TO ENVIRONMENTAL RADIOACTIVITY© Chromatiques/IRSN – Source: IRSN

319

Internal exposure
External exposure

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /6.6. DOSE : THE SIEVERT (Sv)By transferring its energy to them, ionisingradiation can damage the body's tissues. Thisdamage and its consequences depend on thenature of the radiation, its energy and what
becomes of the radionuclide when it is ingested
or inhaled.
Furthermore, the different organs differ in termsof their sensitivity to radiation. What is more, theeffects will differ depending on which parts of the
body are struck by the radiation. Estimation of theeffective dose makes it possible to quantify andcompare the different types of exposure to which
a person can be subjected, taking account of thespecific characteristics of the radionuclides, theirradiation and the organs exposed. The effective
dose is expressed in sieverts (Sv). For exposure
resulting from environmental radioactivity, this320

unit is very large, and we use sub-multiples: themillisievert (1 mSv = 0.001 Sv) or the microsievert(1 µSv = 0.000001 Sv). In this radiological report,
the effective doses are estimated for an adultindividual and for an exposure period of one year
(mSv/year or µSv/year).
The dose factor can be used to estimate the dosein sieverts based on the measured environmental
activity levels (Bq/kg in food, Bq/m2 in soils andBq/m3 in the air, in particular). The dose factor
for estimating the dose following ingestion of aradionuclide is expressed as ingested Sv/Bq; forestimating the dose through inhalation as inhaled
Sv/Bq; and the external exposure in Sv/h per Bq/
m3 if the radionuclide is in the air or in Sv/h per
Bq/m2 if it is on or in the soil. Figure 5 showsthat the dose factors differ widely according toradionuclide and exposure mode.

FOCUS
THE EFFECTS OF RADIATIONON HEALTH

Radiation can generate damage in the cells of theorgans exposed to it. In the event of intense
exposure, massive cell death can lead to rapid andcertain effects: various degrees of burning,
necrosis, reduction in white cells, nausea and,in extreme cases, the death of the individual. Radioactivity in the environment can never under
any circumstances lead to this kind of consequence. Exposure to environmental radioactivity
is in the order of a thousand to a million times lower than the exposure likely to produce theaforementioned effects. This exposure can be the source, on a random basis, of pathologies
that may appear years, even decades later: essentially, cancers.
These consequences are akin to those that can result from smoking or the appearanceof skin cancer following repeated exposure to the sun.

Becquerel

Sievert/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

UNDERSTANDING RADIOACTIVITY AND THE POSSIBLE EFFECTS OF EXPOSURE ON THE HUMAN BODY / 06
DOSE: THE SIEVERT (Sv) / 6.6

TABLE 1 / CHARACTERISTICS OF THE MAIN RADIONUCLIDES MEASURED IN THE ENVIRONMENTRadionuclide

Radiation

Half-life (years)

Type

SourceEnergy

H

12.3

Beta

Very low energy

1, 2 and 3

C

5730

Beta

Very low energy

1, 2 and 3

Sr-Y

28

Beta

High energy

2 and 3K

1,260,000,000

Beta and gammaHigh energy

1

Ag

0.68

Beta and gammaHigh energy

2

Cs

2.1

Beta and gammaHigh energy

2

Co

5.3

Beta and gammaHigh energy

2

137

Cs-mBa30

Beta and gammaHigh energy

2, 3 and 4

106

Ru-Rh

1

Beta and gammaHigh energy

2

129

I

15,700,000

Beta and gamma

Low to average energy

1 and 2

226

Ra

1600

Alpha and gammaHigh energy

1

210

Po

0.38

Alpha

High energy

1

238

U

4,500,000,000

AlphaHigh energy

1 and 2

238

Pu

88

Alpha

High energy

2 and 3239

Pu

24,000

Alpha

High energy

2 and 3

3

14
90
40

110m
134
60

1: natural* / 2: nuclear facility discharges / 3: persistence from nuclear weapons testing* / 4: persistence from the Chernobyl disaster** Cf. chapter 2.

TABLE 2 / DOSE CALCULATION MODE FOR EXTERNAL AND INTERNAL EXPOSURE BASED ON ENVIRONMENTAL
RADIOACTIVITY

External exposure

Internal exposure=

Surface activity
or activity per unit
volumein Bq/m2 or Bq/m3=

Activity per unit massor activity per unit
volume(air, food)in Bq/kg or Bq/L
for food
and Bq/m3 for air

X

Exposure timein h

X

Dose coefficientin Sv/h per Bq/m2
or Sv/h per Bq/m3

X

Quantity of air inhaled
or food ingested
m3 of air,
L or kg of foodX

Dose coefficientin Sv/Bq inhaled
or ingested

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /321

FIGURE 5 / EFFECTIVE DOSE FOR UNIT INGESTION (µSv/Bq) AND DOSE RATE IN THE AIR BY IRRADIATIONFOR A UNIT SURFACE ACTIVITY (µSv/hour per MBq/m2) FOR THE MAIN RADIONUCLIDES MEASURED IN THE FRENCHENVIRONMENT
For the same radioactivity ingested or the same radioactivity deposited on the soil, the doses generated by the radionuclide are very
different. They depend on the nature of the radiation and on its energy, along with what happens to the radionuclide in the body in thecase of ingestion. On account, in particular, of its very low-energy beta radiation, tritium is almost 10 million times less radiotoxic
through ingestion than polonium-210. It does not produce, moreover, any external irradiation. Generally speaking, alpha-emitterradionuclides (plutonium, radium, polonium and uranium) are the most radiotoxic through ingestion.
On account of their high-energy gamma radiation, silver-110m, cobalt-60, and caesium deposited on the surface of the soil produce
most irradiation in the air.

Effective dose via unit ingestion for an adult(µSv/Bq ingested)
10
1
0.1
0.01
0.001
0.0001322

0.000 013

H

14

C 10m Ag
1

60

Co

40

K

6
10

h m Ba-R
Ru 137 Cs-

4
13

Cs

90

Sr

-Y

23

8

U

9
12

I 238 Pu 26 Ra 210 Po
2
9 u
23 P
u
0
24 P

Annual dose rate in the air via radiation for a unit surface activity in the soil(µSv/hour per MBq/m2)
10
1
0.1
0.01
0.001
0.000 10.000 01
3

H

0
21

Po

14

C 238 Pu

23

8

U 2 39 Pu

90

Sr-Y 226 Ra

9
12

I

40

K

6
10

a
h
-R m B 134 Cs
Ru 137 Cs-/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 201760

Co 110m Ag

UNDERSTANDING RADIOACTIVITY AND THE POSSIBLE EFFECTS OF EXPOSURE ON THE HUMAN BODY / 06
Radiation protection / 6.7

In the case of inhalation, this involves estimating
the activity inhaled by the person (Bq/an) basedon the activity measured in the air (Bq/m3) andfactoring in an average breathing rate (m3/h).

To assess the potential annual effective dose
resulting from ingestion, it is necessary toestimate the quantity of food concerned ingested
per year (cf. table 2). Since the influence of nuclear
facilities is essentially limited to the immediateneighbourhood, this involves estimating the
proportion of local food consumed. Food studies
conducted in France show that the share of local
fruit and vegetables can be very high (greaterthan 70%). However, the consumption of cereal
derivatives (bread, pasta, rice, etc.) produced
locally is most frequently nil. By multiplying thequantity of each local foodstuff consumed annually(kg/year) by the activity of each radionuclide
measured in each of them (Bq/kg) we obtain
the annually incorporated radioactivity (Bq/year)
for each radionuclide. The dose factor then enables
estimation of the effective dose by ingestion(Sv/year) based on this incorporated activity.

The method used for calculating doses is detailed
in chapter 8.

6.7. RADIATION PROTECTION
The purpose of radiation protection is to reduce
the risks linked to ionising radiation by limiting, inparticular, the doses linked to individual exposure.
For the population, the annual exposure limit of
1 mSv applies to the total sum of doses received
excluding natural radioactivity and the medical
use of ionising radiation. The doses calculated inthis report based on activity levels measured in
the environment are in the order of between 100
and more than 10,000 times lower than this limit.
323

FIGURE 6 / REGULATORY EXPOSURE LIMITS AND EXAMPLES OF EFFECTIVE DOSES RECEIVED DURING MEDICAL
EXAMINATIONS (mSv)

Regulatory limit
for workers of the admissible
annual dose of exposure
likely to be received throughtheir professional activity

Order of magnitudeof the annual average doseof exposure caused by discharges
from French nuclear facilities

Regulatory limit for the populationof the admissible annual doseof exposure of artificial origin(except as received as a patient
for medical purposes)▼

0.0001 to 0.01
0.004

Order of magnitude
for a retroalveolar
dental X-ray

Lowest detected
dose level to date
for a provencarcinogenic effect

1
0.02

0.1

Order of magnitude
for a breast scan

Order of magnitude
for a frontal
pulmonary X-ray

20
2

to

9

10

100

mSv

Order of magnitude
for an abdominal/
pelvic scan

Annual average doseof exposure to ionisingradiation of natural
origin in France

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /© Leprieur/IRSN

324/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

O7
INFORMATION SOURCES

ON THE MONITORING
OF RADIOACTIVITY AND
THE DISTRIBUTION OF DATA
7.1. W EBSITES AND PUBLIC INFORMATION RESOURCES .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 326
Web portal of the national network for radioactivity
measurement in the environment (RNM).  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 326
Websites of the main data producers and interested parties.  .  .  .  .  .  .  .  .  .  .  . 327
Information resources of the ASN(French nuclear safety authority). .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 327
The High Committee for transparency andinformation on nuclear safety .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 328"Environment" reports of nuclear facilities .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 328
7.2. D ISTRIBUTING INFORMATION IN THE FRAMEWORK OF
INTERNATIONAL TREATIES OR CONVENTIONS.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 329
Distribution of French data in the frameworkof the Euratom treaty. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 329
Data transmitted to the OSPAR commission .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 329

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /

325

O7

INFORMATION SOURCES
ON THE MONITORING
OF RADIOACTIVITY AND
THE DISTRIBUTION OF DATA

326

Informing the public about radioactivity inthe environment is an essential element inguaranteeing the transparency of nuclear activities.
The TSN Act of 13 June 2006, incorporated in the
French Code of the Environment, states that:"transparency in nuclear matters consists of all
the measures taken to guarantee the public's
right to reliable and accessible information…".

7.1. WEBSITES AND PUBLICINFORMATION RESOURCES

The ASN, IRSN and the nuclear industry
stakeholders in France propose many information
resources to meet legal obligations on the one
hand and public expectations on the other.

The website of the RNM, launched on 2 February2010 (cf. chapter 1), is the main French reference
for the monitoring of environmental radioactivity,offering in particular centralised access to all theenvironmental monitoring results conducted by
all data producers throughout France.

The distribution of environmental radiation
monitoring data extends beyond nationalboundaries. In application of the Euratom treaty
and in the context of the work of the OSPAR
commission, IRSN passes on to the commission
every year the results of the monitoring it conducts
as part of its mission. Likewise, the nuclear
operators also provide OSPAR with their data
concerning liquid radioactive discharges. These
data are then used in studies and publications
available to the public via various information
resources.

Web portal of the national network forradioactivity measurement in theenvironment (RNM)

The RNM database can be accessed by means of an
information system that enables all information to
be retrieved by the general public and by experts,
in particular by means of a cartographic web
portal: www.mesure-radioactivite.fr.
On average, more than 25,000 new measurement
results are added every month. The RNM
therefore offers the most global vision possibleof all radioactivity measurements made in
the environment by the various stakeholders
concerned.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

INFORMATION SOURCES ON THE MONITORING OF RADIOACTIVITY AND THE DISTRIBUTION OF DATA / 07
WEBSITES AND PUBLIC INFORMATION RESOURCES / 7.1

FIGURE 1 / INTERACTIVE MAP OF FRANCE OF THE INSTALLATIONS INSPECTED BY THE ASN

327

Websites of the main data producers andinterested parties
All those involved in measuring radioactivity in theenvironment have websites enabling the public to
obtain additional information about their activities,
and their inspection, monitoring or occasional
expert assessment programmes. Certain websites
also enable consultation of the annual information
report for the public as stipulated by the Code of
the Environment, which contains a section relating
to the nature and results of the measurements ofradioactive and non-radioactive discharges from
nuclear facilities into the environment.

Information documentation of the ASN(French nuclear safety authority)
The ASN has put in place an information policy
based on supplementary resources for making
information accessible to its various audiences. The
www.asn.fr website is the main public information
tool. It presents the latest news on nuclear safety
and radiation protection in France, and thepositions adopted by the ASN across its fields

of competence. Furthermore, the site provides
access to a documentation base on the life-cycleof installations via simplified navigation, improved
access to data and optimised downloading of
selected information or publications. Since 2012,
the ASN has developed on its website a TV page(http://tv.asn.fr/Environnement) dedicated to
topics associated with environment monitoring.
The ASN has provided online since 2017 an
interactive map of France with the facilities it
inspects (cf. figure 1), and which enables general
information to be obtained about these facilities(description of the facility, applicable regulations,etc.), as well as more detailed information about
incidents that have occurred, inspection follow-up
letters, and letters stating the position of the ASN.
The ASN Report on the state of nuclear safety andradiation protection in France, published annually,
constitutes a reference document providing
information about the state of the activities
inspected by the ASN in these two areas. The
ASN publishes four times a year the periodical:
Contrôle ("Inspection"), distributed to more than
10,000 readers in France and abroad.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /328These publications, along with the otherinformation resources of the ASN (Lettre del’ASN ("ASN newsletter"), brochures and news
sheets for the general public) can be consulted
and downloaded at www.asn.fr. They are alsoavailable from the ASN's public information anddocumentation centre.

• representatives of environmental protection
associations and associations mentioned inarticle L.1114-1 of the French Public Health
Code;

The High Committee for transparency
and information on nuclear safety(HCTISN)• persons chosen on account of their scientific,
technical, economic or social skills, orinformation and communication skills, withthree designated by the Parliamentary Office
for assessment of scientific and technologicalchoices, one by the Academy of Sciences and oneby the Academy of Moral and Political Sciences;

Created out of the French Environment Code(article L.125-34), the High Committee fortransparency and information on nuclear safety
is an information, consultation and debating bodyon the risks associated with nuclear activities
and the impact of these activities on the health ofpeople, the environment, and nuclear safety. To
this end, the High Committee can issue a noticeconcerning any question in these areas and on
the inspections and information relating to them.
It can also deliberate on any question relating toaccessibility of information concerning nuclear
safety and propose any measure for guaranteeing
or improving transparency as defined in article
L. 125-12 of the Environment Code.
The committee may also be convened by:• the minister responsible for nuclear safety;• the presidents of the competent commissions of
the Assemblée Nationale and the Senate;• the president of the Parliamentary Office forassessment of scientific and technologicalchoices;• the presidents of the local informationcommissions;• the operators of basic nuclear facilities for any
questions relating to information on nuclear
safety and its inspection.
The HCTISN is composed of members appointed
for six years by decree, of whom there are four for
the Members of Parliament and six for each of theother categories, distributed thus:• two MPs designated by the Assemblée Nationale
and two senators designated by the Senate;• representatives of the local informationcommissions;• representatives of entities responsible fornuclear activities;• employee union representatives;• representatives of the ASN, of the State services
concerned and of IRSN.
The president of the High Committee is appointed
by decree out of its member parliamentarians,
representatives of the local informationcommissions and persons chosen for their skills.

"Environment" reports of the nuclear
facilities
The operators are subject to legal information
obligations: either general (such as theenvironment report stipulated by the Code ofCommerce for joint-stock companies) or specificto the nuclear field.
The Environment Code obliges all nuclear facility
operators to draw up every year a report on
their situation and the actions they undertake, inparticular in terms of the radiological monitoringof their facility's environment. In parallel, theregulations also oblige operators to publish anannual monitoring report in application of thegeneral rules relating to basic nuclear facilities(Order of 7 February 2012): "The operator shalldraw up annually a report presenting the impact
of its facility during the past calendar year. This
report shall characterise the water samples, theeffluent discharges, the environmental monitoring
and the impacts of the pollution generated.
The report shall be transmitted to the nuclear
safety authority (ASN), to the DREAL (Regional
department for the environment, development
and housing), to the regional health agency, to theservice responsible for water policing and to the
local information commission."/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

INFORMATION SOURCES ON THE MONITORING OF RADIOACTIVITY AND THE DISTRIBUTION OF DATA / 07
Distributing information in the framework of international treaties or conventions / 7.2

Every year the ASN conducts an analysis of these
documents and publishes in its annual report themain conclusions relating to the treatment of
the topics subject to legislation, to the strategic
aspects and to the instructional aspects regardingtransparency and the right to access nuclear
information.

Data transmitted to the OSPAR
commission

7.2. DISTRIBUTING INFORMATION
IN THE FRAMEWORK OF
INTERNATIONAL TREATIES ORCONVENTIONSThis commission is composed of representatives
from the governments of the 15 contracting parties(Belgium, Denmark, Finland, France, Germany,
Iceland, Ireland, Luxembourg, Netherlands,
Norway, Portugal, Spain, Sweden, Switzerland
and the UK) and the European Commission, andfrom non-governmental organisations.

IRSN action with regard to information about themonitoring of radioactivity in the environment isalso conducted internationally, in particular in theframework of the Euratom treaty and the OSPAR
convention (Convention for the Protection of the
Marine Environment of the North-East Atlantic).

Distribution of French data in theframework of the Euratom treaty
Every year, IRSN transmits to the European
Commission, in the name of the French State,
several thousand environmental radioactivity
measurement results relating to aerosol
particles, water and milk, to satisfy therequirements of articles 35 and 36 of the Euratom
treaty. This submission is complemented by
the automatic release of the hourly ambient
dose rate averages measured by the sensors of
the Téléray network on the EURDEP platform(EUropean Radiological Data Exchange Platform).
The European Commission regularly publishes
a summary report at European level derivingfrom the processing of data transmitted by
the Member States. A public web portal
http://rem.jrc.ec.europa.eu enables connection
to the various databases of the European
Commission to view the results.

The mission of the OSPAR Convention is to protect
the marine environment of the North-East Atlantic
by preventing and eliminating pollution, protecting
the marine environment against the harmful
effects of human activities, and contributing to thesustainable use of the seas.

"The strategic objective of the OSPAR Commission
with regard to radioactive substances consists inpreventing pollution of the maritime zone fromionising radiation, through the progressive andsubstantial reduction of waste, emissions andlosses from radioactive substances, with theultimate objective of achieving concentrationsin the environment that are close to the ambient
values in the case of radioactive substancespresent in nature, and close to zero in the case ofsynthetic radioactive substances."
IRSN is involved in the work of the OSPAR
Commission and passes on to it radioactivity
data relating to the marine samples taken on the
Atlantic - Manche department seaboard (water,
sediments, fauna and flora), which have beenused for establishing a "baseline", or reference
point, for regularly assessing the progress
made since 1998 in reducing the environmental
marking attributable to human activities. Thesetransmissions of annual data are likely to continue
into the future.
Lastly, France periodically produces a report
also including information relating to theenvironmental monitoring conducted by theoperators of basic nuclear facilities (INBs)(PARCOM 91/4 recommendation).

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /329Sampling underwater sediments© Marine nationale

330/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

O8
APPENDICES
8.1. C ALCULATING THE MEAN AND TAKING ACCOUNTOF NON-SIGNIFICANT VALUES .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 332
Case No. 1: Few measurements below the decisionthreshold and homogeneous data .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 333
Case No. 2: Few non-significant measurements
but heterogeneous data set. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 333
Case No. 3: High percentage of non-significant measurements .  .  .  .  .  .  . 333
8.2. R EPRESENTATION OF INDICATORSIN THE FORM OF A BOX-AND-WHISKER PLOT.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 334
8.3. METHOD USED FOR ESTIMATING DOSES. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 335
Data used for calculating doses .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 335
Integration of background radiation. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 336
Radionuclides and decay series. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 336
Calculated value. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 337
Routes of exposure. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 337
Presentation of exposure scenarios and calculations .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 337
List of references.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 342
8.4. GLOSSARY.  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 343
8.5. EDITORIAL COMMITTEE. .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  .  . 351

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /

331

O8

APPENDICES

8.1. CALCULATING THE MEAN
AND
TAKING ACCOUNT OFNON-SIGNIFICANT VALUES

332

Since the activity levels of certain radionuclides
in the environment are very low, the series ofmeasurement results frequently include results
below the decision threshold (DT, cf. chapters 1.4
and 7). The best-known and most-used statisticalindicator, the arithmetic mean (sum of the valuesof a series divided by the number of values), does
not on its own allow these results to be taken into
account. However, they must not be disregarded,
and when their proportion is too high, it is relevant
to consider them in the statistical calculations.
For the previous Radiological Review, thisintegration was done by calculating an average
weighted against uncertainty or the decisionthreshold value. Application of this method tothe series of measurement results led to theestimation of low averages vis-a-vis the series
they were supposed to represent and, in particular,
vis-a-vis the arithmetic mean. This method has
been abandoned.
The indicator proposed for the present report is anarithmetic mean calculated on the basis of, firstly,
the significant measurements (i.e.: where thevalue is >DT) and, secondly, the non-significant
measurements (i.e.: where the value is <DT) to
which are attributed the DT value when certain
conditions are fulfilled. The different possible
scenarios and the method used for each of theseare explained below.

This method was chosen taking account ofrecognised statistical methods. This choicereflects the intention never to underestimate thevalue of the calculated mean without, nonetheless,being too conservative or, indeed, issuingnon-verifiable hypotheses about the measurement
distribution laws. Two parameters determine themode of calculation for the mean:• the number of measurements below the decisionthreshold (DT) with respect to the total numberof measurements: the literature is unanimouson the fact that beyond a certain percentage of
non-significant measurements (around 80%)
there is no reliable method for estimating
the mean of a sample (there would be toohigh an error level). In the case of this report,
we considered that the chosen method was
no longer satisfactory beyond 50% of nonsignificant measurement results (below thedecision threshold);• the presence, for the same set of data, of
heterogeneous measurements (measurements
obtained with very different precision
instruments) and mixing significantly different
decision thresholds (see below, example of caseNo. 2).
Ultimately, three different possible cases wereidentified, with a calculation type specific to eachof them.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

APPENDICES / 08
Calculating the mean and taking account of non-significant values / 8.1

The non-significant measurements (expressed
as <DT) are replaced with the DT value and theindicators are calculated on the basis of thisnew data set. This case can be illustrated by theexample opposite.

8
Activity

In case No. 1, the percentage of non-significant
measurements is below 50% [3], and the data set
is homogeneous.

> Substitution of < DT with DT values
10

6
4
2
0

> Mean calculation: 3.5

Activity

Case No. 1: Few measurements below
the decision threshold andhomogeneous dataNon-significant measurements

2
1.5

333

1

0.5
0

> Mean calculation: 2.4

Activity

Case No. 2 is characterised by a percentage of
non-significant measurements of less than 50%,
but also by the presence of heterogeneous results.
In this case, the measurements below the decisionthreshold are eliminated and the calculation of themean is done on the basis of this new set of data(with fewer data). This case can be illustrated by
the graph opposite.

> Elimination of < DT values
2.5

Activity

Case No. 2: Few non-significant
measurements but heterogeneous
data set

Significant measurements

The percentage of non-significant measurements
is higher than 50%.
In this case, the calculation of the mean is nolonger carried out. The information that will be
provided on this set of measurements will be:• the range of values actually measured (min, max);• the percentage of measurements below thedecision threshold.

Significant measurements

Non-significant measurements

Significant measurements

6
5
Activity

Case No. 3: High percentage of
non-significant measurements

Non-significant measurements

4
3
2
1
0

> Only possible conclusions:• 71% non-significant measurements• Measured min.: 2.2• Measured max.: 4.9

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /8.2. REPRESENTATION OF
INDICATORS IN THE FORM OF A
BOX-AND-WHISKER PLOT
To describe a series of measurement results, andin particular its dispersion, it is possible to supply
the lower and upper bounds, thus determining
the full range of values. However, it so happensthat the upper and lower bounds correspond to
extreme values which give too wide a vision of
the range of values most frequently encountered.
To determine this range, it is possible to calculate
percentiles. Thus, 90% of the data fall between
percentile 5% and percentile 95%; or else 95% of
the results are less than this 95th percentile.

334

The box-and-whisker plot can be used to represent
simultaneously several indicators and obtaina summary and complete view of the distributionof the measurement results. Usually, the box-andwhisker plot provides percentiles and, in particular,a median (50th percentile) to indicate the centreof distribution (50% of the values are below thismedian). This choice of representation was used inparticular in chapter 2 in relation to the reference
environmental background radiation values (in theparticular case of chapter 2, the values below thedecision threshold are not taken into account). The
arithmetic mean as presented previously is added
to these "box-and-whisker" representations.
References[1] Helsel D, Nondetects and Data Analysis:
Statistics for Censored Environmental Data,
Whiley.
[2] Antweiler RC and Taylor HE, Evaluationof statistical treatments of left-censoredenvironmental data using coincident uncensoreddata sets: Summary statistics, Environmental
science & technology, 2008.
[3] 
I RSN 2018 internal report"Méthodes
statistiques pour le traitement de données
censurées - Choix d’indicateur(s) applicables àla surveillance de l’environnement" ("Statisticalmethods for the processing of censored data Choice of indicator(s) applicable to environmental
monitoring").

FIGURE 1 / EXAMPLE OF A BOX-AND-WHISKERS PLOT

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

APPENDICES / 08
Method used for estimating doses / 8.3

8.3. METHOD USED FOR
ESTIMATING DOSES
Data used for calculating doses
The measurement results on which the dose
calculations are based are the activity perunit volume in the air, water and milk, and theactivity per unit mass in solid foodstuffs (plant
production [leafy vegetable, fruit, etc.]), animal
production [meat, eggs, etc.], and sea or riverproduce (fish, crustaceans, molluscs, etc.).
For the radiological report, the activity levels
are averaged out per radionuclide, per matrix(for example, measurement of the activity per unit
volume in the air), and for the entire stated period.
For foodstuffs, these activity levels are expressedas Bq/kg of fresh foodstuff.
In the case of carbon-14, when the activities added
locally around a nuclear facility are too low to be
distinguished from the background radiation via
activity per unit mass measurements expressedas Bq/kg fresh, specific activity measurements
expressed as Bq/kg of carbon enable added
activity levels in the order of several percent of
this background radiation to be quantified. Basedon these added specific activities, it is possible
to deduce the activity per unit mass by means of
the measured or theoretical content of elemental
carbon in the food:In the case of tritium, three types of measurement
in foodstuffs are used in this radiological report:
measurements of total tritium, expressed as
Bq/kg fresh, measurements of organically boundtritium (OBT) expressed as Bq/kg fresh OBT oras Bq/L of combustion water, and free tritium(HTO) activities expressed as Bq/kg fresh of freetritium or as Bq/L of dehydration water (cf. focus
in chapter 1). Since the dose coefficients aredifferent for the OBT and the HTO, it is necessary in
all cases to have separate information concerning
the activity per unit mass of the bound fractions(OBT) and free fractions (HTO) for each foodstuff.
The relations between these various activities are
as follows:
AmH3total,food (i)  =  AmOBT,food (i)  +  AmHTO,food (i)   [2]where:AmTOL,food (i)  =  Av,combwater (i)  .  WE (i)AmHTO,food (i)  =  Av,dryingwater (i)  .  WC (i)335

AmC14,food (i)  =  Aspec.C14,food (i)  .  Ctotfood (i)   [1]TABLE 1 / PHYSICAL QUANTITIES USED IN CALCULATING THE ACTIVITY LEVELS OF CARBON-14 IN FOODSTUFFS

Physical quantity

Unit

Am,food (i)Activity per unit of mass of foodstuff i

Bq/kg fresh

Aspec.food(i)Specific activity of foodstuff i

Bq/kg of carbon

Ctotfood (i)Total elemental carbon content
of foodstuff i

kg of C/kg fresh

Retained value

Reference or explanation/
Measurement in theenvironment/

IAEA [10] or IRSN data

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /TABLE 2 / PHYSICAL QUANTITIES USED IN CALCULATING THE ACTIVITY LEVELS OF TRITIUM IN FOODSTUFFS

Physical quantity

336

Unit

Retained
value

Referenceor explanation

AmH3total,food (i)Activity per unit of mass of total tritium in foodstuff i

Bq/kg fresh/

AmOBT,food (i)Activity per unit of mass of bound tritium in foodstuff i

Bq/kg fresh OBT//

AmHTO,food (i)Activity per unit of mass of free tritium in foodstuff i

Bq/kg fresh HTO//

Av,combwater (i)Activity per unit of volume of combustion water for foodstuff i

Bq/LMeasurement

See Focus chapter 1.

Av,dehydwater (i)Activity per unit of volume of dehydration water for foodstuff i

Bq/LMeasurement

See Focus chapter 1.

WE food (i)Water equivalent content of dry matter in foodstuff i

L/kg fresh

0.6

IAEA [10]and IRSN data

WC foodstuff (i)Water content of foodstuff i

L/kg fresh

Measurement
or reference

IAEA
or IRSN data

Integration of background radiation

Radionuclides and decay series

Added doses attributable to installation discharges
are estimated in the radiological report. When aradionuclide is present in the environment beyond
the influence of the nuclear facility (naturalradionuclides or residual radionuclides fromold fallout, cf. chapter 2), this environmental
background radiation is subtracted from themeasurements before estimating these added
doses. Lastly, in the absence of a backgroundvalue, the "raw" activities measured are directly
used for estimating the doses, which are therefore
overestimated.

For each quantified radionuclide, it is also
necessary to consider the daughter isotopes ifthey have been quantified (case in particular of
natural families of uranium).

Furthermore, the background radiation activity
levels of the carbon-14 that are subtracted fromthe activity per mass unit measured around asite, before estimating the doses, are calculated
according to relation 1 with a specific activity valueof the background radiation equal to 227 Bq/kg ofcarbon (cf. chapter 2).
Lastly, the background radiation activity levels of
the tritium that are subtracted from the activity
per mass unit measured around a site, before
estimating the doses, are calculated according to
the previous relation 2 with a background radiation
activity value equal to 1.3 Bq/L of combustion or
dehydration water (cf. chapter 2).

The radionuclides likely to exceed the backgroundradiation and give rise to the calculation of doses
are listed below:• radionuclides measured in the air: 3H, 14C, 51Cr,
54
Mn, 57Co, 58Co, 60Co, 110mAg, 124Sb, 129I, 131I, 137Cs,
230
Th, 234U, 235U, 236U, 238U, 238Pu, 239+240Pu;• radionuclides measured in food or water: 3H, 14C,
58
Co, 60Co, 90Sr, 110mAg, 129I, 137Cs, 234U, 235U, 236U,
238
U, 238Pu, 239+240Pu.
The question of decay series progeny applies to alimited number of radionuclides, to be consideredon a case-by-case basis:• for 90Sr, the de facto equilibrium with its daughter
isotope (90Y) is assumed;• for uranium (234, 235 and 238), it depends on
its age according to the type of industry of eachsite (case of fuel manufacturing sites: Malvési,
Romans-sur-Isère and Tricastin).
In the case of the state of equilibrium with thedaughter isotopes not being known, only thequantified radionuclide will be taken into accountin the dose calculation.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

APPENDICES / 08
Method used for estimating doses / 8.3

Calculated value

Presentation of exposure scenarios andcalculations

To conduct the dosimetric impact calculations forthe population on the basis of the measurements
made in the environment, we opted to calculate
the effective doses. Each dose is expressed as
Sv/year then converted into sub-multiples, mainly
the µSv/year. The doses are calculated for adults.

Calculation of the internal dose received byinhalation of radioactive aerosols or gas
The conservative scenario is considered of a person
breathing the external air with no protection forthe habitat. Such persons are exposed 100% of thetime, or 8760 hours per year.

Routes of exposure

The annual dose received by inhalation ofsubstance i is calculated based on the following
formula [3]:The main routes of exposure to added radioactivity
when a person resides close to a nuclear site are:• internal exposure by inhalation of aerosols orradioactive gas,

Einh(i)  =  Av(i)  .  fr  .  t  .  einh(i)  .  106   [3]• internal exposure via skin absorption for tritiumin the air (in HTO form),• external exposure by immersion in a plume ofnoble gases (case of 85Kr at La Hague),• and, lastly, internal exposure by ingestion of foodand/or water for persons consuming produce of
local origin.

337

TABLE 3 / PHYSICAL QUANTITIES USED IN CALCULATING THE INTERNAL DOSE RECEIVED BY INHALATION

Physical quantity

Retained value

Reference or explanationµSv/year

/

/

Av(i)
Average activity concentration measured
in the air

Bq/m3

Measurement in
the environment/tExposure duration per yearh/year8760

Exposure 100% of the time with no protection
factor for the habitat

fr
Respiratory flow rate

m3/h

0.96

Respiratory flow rate for an average
activity for an adult (taken from publication 66
of the CIPR)

einh(i)Effective dose per unit intake byinhalation of substance i

Sv/Bq

According toradionuclide

Values taken from table 1.2 of the Orderof 1 September 2003 [2]*Einh (i)Annual dose received by inhalationof substance i

Unit* Since no information is available about the form of the aerosols measured in the environment, the type of pulmonary absorption (fast (F),medium (M), slow (S), gas and vapour (V)) used in the calculations has been chosen in accordance with the recommendations in table 1.3 of
the Order [2]. In the case of the Order not providing for any particular form, the form leading to the worst-case effective dose dose intake
is chosen.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /Calculation of the internal dose received via
skin absorption (case of 3H in HTO form)
The conservative hypothesis is chosen whereby
the annual dose received by skin absorption fromthe tritium present in the air in HTO form is equal
to the annual dose received by inhalation of tritiumin HTO form.
Eskin_absorption_3H(HTO)(i)  =  Einh_3H(HTO)   [4]TABLE 4 / PHYSICAL QUANTITIES USED IN CALCULATING THE INTERNAL DOSE RECEIVED BY SKIN ABSORPTION FOR
TRITIUM IN HTO FORM

Physical quantity

338

Unit

Eskin_absorption_3H(HTO)
Annual dose received by skin absorptionµSv/yearEinh(i)Annual dose received by inhalation of tritium HTOµSv/yearCalculation of the external dose received byimmersion in an atmosphere where there isa noble gas present (case of 85Kr in La Hague)
The conservative scenario is considered of aperson exposed 100% of the time to a noble gas
with no protection for the habitat. In this case,only external exposure via immersion is to beconsidered. The annual dose received by external
exposure through immersion in substance i is:
Eextimmersion(i)  =  Av(i)  .  t  .  eimmersion(i)  .  106   [5]TABLE 5 / PHYSICAL QUANTITIES USED IN CALCULATING THE EXTERNAL DOSE RECEIVED BY IMMERSION IN A NOBLE GAS

Physical quantity

Retained value

Reference or explanationµSv/year

/

/

Av(i)
Average activity concentration measured in the air

Bq/m3

Measurement in theenvironment/tExposure duration per yeard/year365

Exposure 100% of the time withno protection factor for thehabitateimmersion(i)Effective dose coefficient of substance i(Sv/d)/ (Bq/m3)

According toradionuclide

Values taken from table 2.2 of
the Order of 1 September 2003
[2]

Eext_immersion (i)Annual dose received by immersion
in substance i

Unit/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

APPENDICES / 08
Method used for estimating doses / 8.3

Calculation of internal dose received byingestion of foodstuffs

The annual effective dose received by ingestion offoodstuffs for substance i is calculated based on
the following formula:

For this exposure scenario, only adults will be
studied.

Eing_food (i) =eing(i) Σfood_j (Am, food_j(i) . qfood_j . Rscfood_j) . 106  [6]Diets may vary according to geographical zone. In
light of the dosimetric assessments conducted in
the previous radiological report, three types of dietwere used. The first derived from the food survey
conducted by CREDOC [8] in North Cotentin andwould be used for the La Hague site. The second
derived from the food survey for the Marcoule [7]site and would be used for the Marcoule site. For
the other sites, we proposed to use an average
diet for the whole of France based on data derivingfrom the INCA 3 food survey [3]. By way of asensitivity analysis, other diets might be taken into
account to assess doses due to particular practices(heavy consumers of fish, etc.).

Furthermore, to estimate as fully as possible thedoses due to tritium, the tritium activity levels forfood around the site can also be deduced fromthose of the HTO measured in the air, basedon the previous formulations. This calculation,
based on the assertion of tritium equilibrium inall components of the overground environment,
can lead for different reasons to a potential
overestimation of the doses for the population.
In particular, the tritium activity for a foodstuff
of animal origin (milk, meat or egg) is linked tothe average activity of the feed consumed by the
animal. This feed may only be partially of local
origin.

For the calculation, the proportion of food produced
locally is also taken into account, with the notion ofself-consumption rate. This rate varies according
to the food in question and the survey carried out.
For the first two studies (CREDOC [8] and Marcoule[7]), the self-consumption rate value was available.
However, for the INCA 3 survey, no data were
supplied. The values available in the INSEE [5]study for the agricultural population living in ruralcommunities would be applied.

339

TABLE 6 / PHYSICAL QUANTITIES USED IN CALCULATING THE INTERNAL DOSE RECEIVED BY INGESTION OF FOODSTUFFS

Physical quantity

Unit

Retained value

Reference or explanationµSv/year//As, foodstuff_j(i)Specific activity of substance i in foodstuff j

Bq/kg fresh

Measurement in
the environment/

qfoodstuff_j
Quantity of foodstuff ingested per year

kg freshweight/year

Depends onthe foodstuff andthe chosen foodsurveyDiet associated with the studied
siter (La Hague or Marcoule) or
diet for the whole of France forthe other sites

eing(i)Effective dose per unit intake by ingestion ofsubstance i

Sv/Bq

According toradionuclide

Values taken from table 1.1 of
the Order of 1 September 2003

Depends onthe foodstuff andthe chosen foodsurveyThis concerns the percentage
of locally-produced foodstuff.
This value depends on the study
in question. For the INCA 3
study these are the data of the
INSEE 1991 study

Eing_foodstuffs (i)Annual dose received by ingestion of foodstuffs
for substance i

Rs-c_foodstuff_j
Self-consumption rate of foodstuff in question-

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /3.4

Leafy vegetables/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

3.6

Shellfish/molluscs-

Wheat (cereals)

Wine

Wild mushrooms

0.37

0.40

0.37

0.75

0.54

0.354

0.100

0.112

0.100

0.574

0.540

0.633

0.440

0.242

-

-

-

-

-

-

-

-

-

-

0.182

0.148

Self-consumption
rate

1: diet for a person residing in North Cotentin and whose main breadwinner is a fisherman.
2: average diet for someone living around the Marcoule site (between 5 and 10 km away).
3: average self-consumption rate.
4: average diet for mainland France.
5: self-consumption rate representative of an agricultural population living in a rural community.

-

Game

2.5

Meat (rabbit)-

1.5

Meat (lamb)--

Meat (pork)

8.8

Meat (poultry)

Meat (beef)

3.3

Crustaceans

Freshwater fish

16.8

4.8

Jams

Sea fish

25.6

Fruits

-

2.4

Honey

Fruiting vegetables

39.3

Root vegetables

6.2

Egg

-

2.5

9.4

Animal fats (butter)

Goat's cheese

Cow's cheese

37.8

-

Milk (sheep)

Yoghurt and fromage blanc

-

54.2

Milk (goat)

Milk (cow)

Diet1(kg fresh weight/year
or L/year)

La Hague site

3.10

51.87

18.8

9.87

26.16

1.50

5.56

14.37

16.90

2.02

2.02

1.37

14.66

4.60

93.40

0.53

120.03

28.00

40.56

12.65

3.30

3.62

11.92

33.85

0

0

60.51

Diet2
(kg fresh weight/year
or L/year)

0.69

0.94

0

0.954

0.008

0.19

0.028

0.16

0.006

0

0

0.63

0

0.42

0.76

0.64

0.89

0.75

0.75

0.52

0

0.12

0

0

0

0

0

Self-consumption
rate3

Marcoule site

2.5

26.71

30.96

0.4

29.5

2.20

7.79

16.30

12.99

0.93

0.76

0.59

10.88

4.75

52.37

2.37

60.28

24.01

37.96

4.60

3.29

1.13

12.92

38.13

0

5.50

21.99

Diet4
(kg fresh weight/year
or L/year)

0.97

0.23

0.015

0.89

0.24

0.93

0.49

0.74

0.38

0

0

0.16

0.16

0.52

0.21

0.11

0.35

0.71

0.75

0.63

0.05

0.05

0.016

0.058

0.43

0

0.43

Self-consumption
rate5

Other site

TABLE 7 / QUANTITIES CONSUMED ANNUALLY FOR EACH TYPE OF FOODSTUFF AND SELF-CONSUMPTION RATE (FRACTION OF FOODSTUFFS OF LOCAL ORIGIN)
USED TO ESTIMATE THE DOSES VIA INGESTION340

APPENDICES / 08
Method used for estimating doses / 8.3

Calculation of internal dose received byingestion of drinking water
To assess the impact of the presence ofradionuclides in certain watercourses orunderground water, the conservative hypothesis
is chosen whereby the water is used as drinking
water. Consequently, certain hypotheses
considered for calculating the indicative dose (ID)(formerly total indicative dose (TID)) are used,as presented in the Order of 12 May 2004 [5].
We therefore consider a regular consumption by
adults of 2 L of water per day, i.e.: 730 L of water
per year. The chosen activities per unit volume are
the values measured in filtered water.
The annual dose received by ingestion of water for
substance i is calculated as follows:

In the case of the water analysed not being
destined for consumption (e.g., water from a canalor a stream), and you wish to assess its impact on
health, we propose calculating a unit dose throughingestion of a litre of water. Depending on theavailable data, the calculation will be made basedon measurement results for unfiltered or filteredwater. In this case, the calculation should bebased on unfiltered water to be representative ofwater that would be drunk by immersing a waterbottle directly in the watercourse. However, mostof the time analyses of water samples are madeon filtered water.
In all cases, the calculation is identical to theformula [5], with only the quantity of consumed
water being rounded to 1 L and the unit expressed
as µSv/L.

Eing_water (i)  =  Av(i)  .  qing-water  .  eing(i)  .  106   [7]TABLE 8 / PHYSICAL QUANTITIES USED IN CALCULATING THE INTERNAL DOSE RECEIVED BY INGESTION OF WATER

Physical quantity

Unit

Retained value

Reference or explanation

/

/

/

Eing_water (i)Annual dose received by ingestion of water
for substance iµSv/yearAv(i)Activity by unit of volume measured in filteredwater for radionuclide i

Bq/L

Measurementin the environment

qing-water
Quantity of water consumed per year

L/year730

Order of 12 May 2004

eing(i)Effective dose per unit intake by ingestion ofsubstance i

Sv/Bq

According toradionuclide

Values taken from table 1.1 of
the Order of 1 September 2003

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /341

List of references[1] R adiological report of the French environment
from June 2011 to December 2014.
[2] O rder of 1 September 2003 defining themethods of calculating effective doses andequivalent doses resulting from the exposureof people to ionising radiation.
[3] ANSES (2017). Étude individuelle nationale desconsommations alimentaires 3 (INCA 3) - Avis del’Anses Rapport d’expertise collective.
[4] G RNC (1999) Modèles de transfert desradionucléides dans l’environnement, Volume
3, Annex VIII-2, Chapter 8.
[5] I NSEE (1991) Enquête
alimentaire des ménages.

Consommation[7] P arache, V. (2011) Enquête alimentaire
autour du site nucléaire du CEA de Marcoule(2010) : méthodologie et résultats. IRSN/DEI/SESURE/2011-07 report.
[8] Département Prospective de la consommation(1998) Enquête sur la consommation alimentairedans le Nord Cotentin pour la COGEMA CREDOC.
[9] Parache-Durand V. (2014). Enquête alimentaire
sur la zone OPE du centre Meuse/Haute-Marnede l’ANDRA : méthodologie et résultats. IRSN/
PRP-ENV/SESURE/2014-08 report.
[10] IAEA: Handbook of parameter values for theprediction of radionuclide transfer in terrestrial
and freshwater environments. Technical reportseries 472. International Atomic Energy Agency.

[6] O rder of 12 May 2004 determining the methods
for inspecting the radiological quality of water
for human consumption.
342/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

APPENDICES / 08
Glossary / 8.4

8.4. GLOSSARY

Alpha (α symbol)
Radiation composed of helium-4 nuclei, strongly
ionising but with low penetration. A simple sheetof paper is enough to halt its propagation. See
chapter 6.

A
AASQA
Association agréée de surveillance de la qualité del’air (Certified air quality monitoring association).
ACRO
Association pour le contrôle de la radioactivité
dans l’Ouest (Association for the inspection ofradioactivity in the west of France).
Actinide
Family of chemical elements with an atomic
number equal to or greater than actinium (atomic
number 89). Four actinides exist in the naturalstate:actinium (89), thorium (90), protactinium(91) and uranium (92). There are also artificial
actinides: these are the transuranic elements(plutonium, americium, neptunium and curium).
Activation
Process whereby atomic nuclei are maderadioactive under the action of a flow of neutronsor other particles.

α global (alpha global)
Radioactivity index representative of the activity ofalpha emitter radionuclides.
ANCCLI
Association nationale des comités et commissions
locales d’information (National association of
local information committees and commissions)
ANDRA
Agence nationale pour la gestion des déchets
radioactifs (National agency for the managementof radioactive waste).
ANSES
Agence nationale de sécurité sanitaire del’alimentation, de l’environnement et du travail(National health and safety agency for food, theenvironment and the workplace)
ARS
Agence régionale de santé (Regional healthagency).

Activation product
Artificial radionuclide produced by capturing aneutron from a stable or unstable atom.

ASN
Autorité de Sûreté Nucléaire (Nuclear Safety
Authority)

Activity
Number of spontaneous disintegrations of atomic
nuclei per unit of time. The unit of activity is thebecquerel (Bq). See chapter 6.

AS station
Fixed aerosols sampling station.

Aerosol
Suspension, in a gaseous medium, of solid or
liquid particles, or both, with a slow settling
speed. In the air and under normal conditions, thiscorresponds to particles with diameters of lessthan 100 micrometres, with the finest measuring
only several fractions of a nanometre.
AFCN
Agence fédérale de contrôle nucléaire (Belgianfederal nuclear inspection agency).
AFNOR
Association française de normalisation (French
standardisation association).

Atom
Basic constituent of matter. It consists of a nucleus(neutrons + protons) around which electrons orbit.
See chapter 6.

B
Becquerel (Bq)
Legal and international unit of measurement
used for quantifying radioactivity. The becquerel(Bq) is equal to one disintegration per second. See
chapter 6.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /343

Beta (β symbol)
Radiation composed of negative or positive
charged electrons. A screen of several metres of
air or a single sheet of aluminium is enough to halt
it. See chapter 6.
β global (beta global)
Radioactivity index representative of the activity ofbeta emitter radionuclides.
BNEN
Bureau de normalisation d’équipements
nucléaires (Nuclear facilities standardisation
bureau). The BNEN is one of 31 sectoral
standardisation bureaus making up the national
standardisation system run by AFNOR.

C
344

Caesium (Cs, atomic number 55)
Rare and toxic metal whose chemical
characteristics are comparable to those ofpotassium. Isotopes 134 and 137 are radioactive
fission products with a half-life of 2.2 years for the
first 30.17 years for the second.
CEA
French Alternative Energies and Atomic Energy
Commission
CLI
Commission locale d’information
information commission)(Local

CNPE
French abbreviation for a nuclear power plant.
COFRAC
Comité français d’accréditation
accreditation committee).

(FrenchCombustion water
Water obtained by burning dry matter in thepresence of oxygen and the absence of othersources of water during combustion.

COMURHEX(Conversion Métal URanium HEXafluorure)
Subsidiary of ORANO, this company operates
two industrial sites in France. The COMURHEX
Malvési industrial site handles the first stageof conversion of uranium concentrates derivingfrom the uranium tetrafluoride (UF4) mining
sites for electricity companies the world over.
This transformation is continued on the industrialsite of COMURHEX Pierrelatte (Drôme), whichtransforms the uranium tetrafluoride into
uranium hexafluoride (UF6), the last stage before
enrichment.
CRIIRAD
Commission de recherche et d’informationindépendantes sur la radioactivité (Independent
research and information commission onradioactivity).
CSP
Code de la santé publique français (French codeof public health).

D
DDCSPP
Direction départementale de la cohésion sociale
et de la protection des populations (Departmental
directorate for social cohesion and the protectionof the population).
DDPP
Direction départementale de la protection despopulations (Departmental directorate for theprotection of the population).
Decay or deactivation
Natural diminution of the nuclear activityof a radioactive substance by spontaneous
disintegration.
Decision threshold (DT)The decision threshold is the minimum valuethat a sample needs to have for the metrologist
to be able to “decide” that this activity is present
and therefore measured. Below this value, theactivity of the sample is therefore too low to beassessed. This decision threshold depends on theperformance of the metrological resources used
and the ambient radiation. See chapter 1.4.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

APPENDICES / 08
Glossary / 8.4

DeclineSloping path via which you descend to access amineral zone for mining extraction.
Decommissioning
Comprises the operations aimed at evacuating
radioactive materials and waste, removing theequipment present, cleaning up and disassembling
the buildings of a nuclear facility at end-of-life orupon definitive shutdown. It is a industrial projectextending over a very long duration, with a security
examination for each stage, to ensure effective
risk management of the operations.
Dehydration water
Water obtained after drying the sample (mostoften by freeze-drying) for analysing the freetritium.
DGAL
Direction générale de l’alimentation (Directorate
general for food).
DGCCRF
Direction générale de la concurrence, de laconsommation et de la répression des fraudes(Directorate general for competition, consumption
and the repression of fraud).
DGPR
Direction générale de la prévention des risques(Directorate general for risk prevention). The
DGPR consists of a technological risks department(in charge in particular of radiological risks), a
pollution prevention and environmental quality
department, and a natural and water-related risks
department.
DGS
Direction générale de la santé (Directorate
general for health).
Discharge authorisation(“Autorisation de Rejet”)
This determines, for each nuclear facility, thedischarge limits for liquid and/or gaseous
effluents and their monitoring conditions. Thisauthorisation is granted by Interministerial Order,
upon submission of a file to the Ministries forindustry, health and the environment.
Dose coefficient
See chapter 6.

Dose rate
Intensity of exposure to ionising radiation (energy
absorbed by matter per unit of mass and time).
The legal unit is the Gray per second (Gy/s).
DREAL
Direction régionale de l’environnement, del’aménagement et du logement (Regional
directorate for the environment, development andhousing).

E
EDF
Électricité de France.
Effective dose
See chapter 5.
Effluent
Any gas or liquid, which may or may not beradioactive, issuing from nuclear facilities.
ElectronElementary particle charged with negativeelectricity. It is part of the composition of atoms.
See chapter 6.
EMM
Staff office of the French Navy.
Environmental background radiation
See chapter 2.
EuratomThis treaty, signed in Rome in 1957, establishedthe European Atomic Energy Community, whose
mission consists in contributing, through thedevelopment of nuclear energy, to the poolingof know-how, infrastructures and financing,and ensuring secure supply in the framework ofcentralised control.
EURODIF
European gaseous diffusion uranium enrichment
plant.
Exposure
Exposure is the condition of being exposed toionising radiation (external exposure if the sourceis situated outside the body, internal exposure
if the source is situated inside the body, etc.).
See chapter 6.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /

345

F

G

FBFC
Société Franco-Belge de Fabrication de
Combustibles (Franco-Belgian fuel manufacturing
company).

Gamma (γ symbole)
Electromagnetic radiation that is very penetrative
but weakly ionising, emitted by the disintegrationof radioactive elements. Shields of concrete orlead offer protection from it. See chapter 6.

FissileRefers to an atomic nucleus in which fission canbe induced by capturing a single neutron. Fissile
nuclei have an energy configuration very close tospontaneous fission.
FissionSplitting of an atom's nucleus under the actionof neutrons. This reaction is accompanied by theemission of neutrons, ionising radiation and apowerful release of heat. It is the latter this is used
to create electrical power in a nuclear power plant.

346

Fission productRadionuclide produced by the nuclear fission ofa heavy nucleus or by the radioactive decay of a
nuclide formed by this process.
FNR
Fast-neutron reactor.
Fruiting vegetables
Vegetables whose fruiting parts are consumed(tomato, aubergine, bell pepper, pea, bean, etc.).
Fuel cycle
All industrial operations to which the nuclear fuelis subject. These operations include in particular
the extraction and treatment of the uranium ore,conversion, enrichment of uranium, manufacturing
fuel, processing used fuels, recycling fissile
materials recovered for manufacturing new fuels
and management of radioactive waste.
FusionFormation of a heavy nucleus from two lightnuclei. This reaction is accompanied by a releaseof energy. Research is underway into using theenergy released by fusion for producing electricity.

Gray (Gy)
Unit of energy transmitted to matter per unit ofmass (joules per kg) during absorption of theradiation dose.
GSIEN
Groupement de scientifiques pour l’information
sur l’énergie nucléaire (Association of Scientists
for Information on Nuclear Energy)

H
Half-life (radioactive period)
Time at the end of which the activity of theradionuclide has diminished by half. The halflife varies from one radionuclide to the next. See
chapter 6.
Helium 4
Nucleus formed by two protons and two neutrons.
Constituting a particularly stable arrangement, it
can be emitted by heavy nuclei seeking stability.
It is then called an alpha ray.

I
ICPEInstallation classée pour la protection del’environnement (Installation classified for theprotection of the environment).
ILL
Laue – Langevin Institute. International researchbody based in Grenoble. It possesses a research
reactor, the high-flux reactor (RHF, INB No. 67)
with thermal power of 58 MW, used for producing
neutron beams.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

APPENDICES / 08
Glossary / 8.4

INB
Installation nucléaire de base (Basic nuclear
facility).

L

INBS
Installation nucléaire de base secrète (Secretbasic nuclear facility).

Leafy vegetables
Vegetables of which we consume all of part of theleaves and stems (lettuce, spinach, cabbage, leek,etc.).

InclineSloping path via which you ascend to access amineral zone for mining extraction.
InVS
Institut de veille sanitaire (Health monitoring
institute).
Iodine (I, atomic number 53)
A simple structure whose radioactive isotopes arepresent in fission products. All radioactive iodine(129, 131, 132, 133, etc.) has a short half-life (e.g.,
isotope 131 has a half-life of 8.02 days), except
for iodine-129 whose half-life is nearly 16 million
years.
Ionising radiation
Radiation with the propensity to strip electrons
from matter. See chapter 6.
IRSN
Institut de radioprotection et de sûreté nucléaire
(Institute of radiation protection and nuclear
safety).
Isotopes
Elements whose atoms possess the same numberof electrons and protons but a different number ofneutrons. They have the same name and the samechemical properties. We currently know of around325 natural isotopes and 1200 artificially-createdisotopes.

M
MatrixSub-part of a compartment (atmospheric,overground, continental aquatic or marine).
Examples: rainwater, soil, plant produce,
sediments, molluscs, etc.
Measurement uncertainty
Margin of inaccuracy for the measurement valueof a physical quantity.
Metrological background radiation
See chapter 1.3.
Mining residues
Designates the products remaining after
extraction of the uranium contained in ore via
static or dynamic processing. They contain thedaughter isotopes of uranium-238, in particularradium-226.
MOX (Mixed Oxide)
Mixture of uranium and plutonium oxides used in
the manufacturing of certain nuclear fuels.
MW
Megawatt.

K

N

K
Symbol of the element potassium. It is expressed
generally as mg/L or mg/kg (milligrams per litre
or per kilogram). 1 gram of natural potassium has
an activity (β/γ) of 31 Bq due to the decay of thenatural radioactive isotope of mass 40 (40K).

Neutrinos
Elementary particles with no known electricalcharge or mass emitted during weak interactions.
NeutronElectrically neutral fundamental particle making
up, with protons, the composition of an atom’s
nucleus. It is the neutron that generates thefission reaction in nuclei whose energy is used innuclear reactors.

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /347

Noble gases
Gases with no chemical affinity and producing nocompounds. These are argon, helium, krypton,neon, xenon and radon. Certain noble gas
isotopes are products of fission and are therefore
radioactive.
Nuclear fuelFissile material constituting the active part ofa reactor’s core. For a fission chain reaction
to be possible, the natural uranium, a mixture
comprising 0.7% uranium-235 – fissile – and99.3% uranium-238 – non fissile –, must havebeen previously enriched to 4% uranium-235.
This uranium is used in the form of uranium oxide,
which is particularly chemically stable.
NucleusCentral part of the atom, positively charged.
10,000 times smaller than the atom, it accounts
nonetheless for practically all the mass. The
nucleus is an assembly of protons and neutrons
bound by strong interaction.
348

O
OPERA-AIR
IRSN permanent observatory for monitoring theenvironmental radioactivity in the air comprising
the stations “AS” (80 m3/h) and “TGD” (“very highvolume”: 700 m3/h). See chapter 1.
Orano
French industrial group involved in particular in
the fuel cycle and the manufacturing of nuclear
facilities, formerly called AREVA.
Ore
A rock containing useful minerals in sufficiently
substantial proportions to justify exploitation.

P
Photons
Elementary particles with no charge or mass,
triggering the electromagnetic interaction.
Pit head
Surface installation of a mine.
Plutonium (Pu, atomic number 94)
Transuranic chemical element; isotope 239 has a
half-life of 24,110 years.
Potential alpha energy concentration (PAEC)
The potential alpha energy concentration (PAEC)
is a parameter used for physically quantifying theenergy that can potentially be deposited in the
respiratory tracts by the disintegration of radon
progeny (cf. chapter 1.2). It is used for monitoring
workers and mining sites. It is expressed as J/m3
(joules per cubic metre).
Processing of spent fuelAll operations relating to the extraction of fissile
and fertile materials (uranium and plutonium)from spent fuels, their reuse, and the packagingof the various types of waste in a form suited totemporary and long-term storage.
ProtonPositively-charged elementary particle, constituting
the nucleus with the neutron.
PWR
Pressurised water reactor. Designates a nuclear
reactor using uranium or mixed uraniumplutonium oxide as fuel and ordinary water
maintained at high pressure (155 bar, to avoid
its vaporisation) as coolant. The French fleet of
nuclear power plants is based on the use of thisreactor system, accounting for the largest numberof units in service in the world.

Ores
Rocks containing useful minerals in sufficiently
substantial proportions to justify exploitation.
Outfall
Outlet of effluents discharged from a nuclear
facility.

R
Radiation
Transfer of energy in the form of electromagnetic
waves (gamma) or particles (alpha, beta, neutrons)
emitted during the disintegration of radionuclides.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

APPENDICES / 08
Glossary / 8.4

Radiation protection
A set of measures designed to protect the healthof the population and workers against exposure toionising radiation.

RNM
Réseau national de mesures de la radioactivité
de l’environnement (National network forradioactivity measurement in the environment).

Radioactive waste management
Set of provisions and operations (regulatory or
technical) relating to radioactive waste, fromproduction through to and including storage,
designed to protect people and the environment.

Root vegetables
Vegetables whose roots, tubers or bulbs are
consumed (carrot, potato, onion, radish, etc.).

Radioactivity
Property of certain elements whose nuclei
disintegrate spontaneously to form other elements
while emitting ionising radiation.
Radionuclide
Radioactive isotope of an element. Examples:3
H: tritium, radioactive isotope of hydrogen; 14C:
carbon-14, radioactive isotope of carbon.
Radiotherapy
Use of the destructive power of ionising radiation
for destroying sick cells, while minimising damage
to the surrounding healthy cells.
Radon (Rn)Radioactive gas omnipresent on the surface of
the Earth. It has three natural isotopes (219Rn,
220
Rn, 222Rn), progeny of the radionuclides present
in the soil (235U, 232Th and 238U). 222Rn is often themost important one to take into account due to its
longer half-life: 3.8 days.
Reactor system / type
Term used for designating a given type of nuclear
reactors capable of producing energy. It is definedby a set of common specifications such as thenature of the fuel, the moderator, the coolant, etc.
Such types include the UNGG (uranium naturelgraphite-gaz) reactor, light-water reactors, fastneutron reactors (FNR), etc.
Reference group (of the population)
As defined by the Euratom 96/29 Directive of 13
May 1999: “Group comprising individuals whose
exposure to a source is reasonably uniform andrepresentative of that of the individuals in the
population who are the more highly exposedto that source.” This notion is replaced by thenotion of “Representative Person” defined in the
Euratom 2013/59 Directive of 5 December 2013:“Individual receiving a dose that is representativeof the more highly exposed individuals in the
population, excluding those individuals having
extreme or rare habits.”

RPL dosimeter
Passive radio photo luminescent dosimeterS
SCL
Service commun des laboratoires (Common
laboratories service, formerly the laboratoriesof the DGCCRF). Since 1986, the date of theChernobyl disaster, the SCL has carried out
regular inspections of the radioactivity levels
present in consumer products.
SET
Subsidiary of AREVA, Société d’Enrichissement
du Tricastin (Tricastin Enrichment Company) is
the works contracting authority and operator of
the Georges Besse II plant. It is installed on the
Tricastin site.
Sievert (Sv)
Legal unit for dose equivalent or effective dose fordetermining the biological effect produced by agiven absorbed dose on a living organism. The dose
equivalent is not a measurable physical quantity
but is obtained by calculation. It depends on theenergy transmitted to the tissues, the type ofradiation and the tissue traversed. See chapter 6.
Significant (significant measurement or result)Measurement result greater than the decisionthreshold. See "Decision threshold" and chapter
1.4.
SOCATRI
Subsidiary of Orano (ex-AREVA), SOCiété Auxiliairedu TRIcastin (Tricastin auxiliary company)
comprises a basic nuclear facility (INB 138) anda uranium decontamination and recovery plant(ARU).

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /

349

Specific activity
Activity of a radionuclide expressed in Bq/kg
for the corresponding chemical element. In thisreport, it is used for carbon-14, for which themeasurement results are expressed in Bq/kg ofcarbon. See chapter 2.
Spectrometry
Analysis of the intensity of radiation emitted
by a source as a function of its energy level.
This method enables both identification of theradionuclides and quantification of their "activity".
SPRA
Service de protection radiologique des armées(Radiological protection service of the French
Armed Forces). The SPRA operates under the
responsibility of the central director of the French
Armed Forces health service.

350

Strontium (Sr, atomic number 38)
Alkaline earth metal, certain isotopes of which arehighly abundant in fission products, in particularisotope 90, which is sequestered in bony tissue
and has a half-life of 28.15 years.

T
Tailings
Mining waste discarded as unprofitable on accountof low ore concentration.
Temporary storage
Provisional storage of radioactive waste.
TGD station
IRSN “very high rate” aerosols sampling station.

U
U by weight
Mass content of uranium in a matrix, with nodistinction of the isotopic composition. It can bemeasured or deduced from the activity (expressedas Bq) of each of the isotopes (in which case werefer to “U equivalent by weight”).
UNGG
Natural uranium / gas / graphite reactor. This
type of reactor has been in operation on the
nuclear power plant sites of Bugey, Chinon andSaint-Laurent-des-Eaux. They are currently being
decommissioned.
Uranium
Chemical element with atomic number 92 andsymbol U, possessing three natural isotopes:
uranium-234, uranium-235 and uranium-238.
Uranium-235 is the only natural fissile nuclide, aquality that explains its use as an energy source.

W
Waste
Any residue from the process of production,transformation or use; any substance, material,
product or, more generally, any goods that areabandoned or that their owner wishes to abandon
as they no longer serve any precise purpose.
WHO
World Health Organisation.

TLD dosimeter
Passive thermoluminescent dosimeterTransuranic elements
Family of chemical elements heavier than uranium(atomic number 92). The main transuranicelements are neptunium (93), plutonium (94),americium (95) and curium (96).
TTS
Total suspended solids.

/ RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017

APPENDICES / 08
Editorial committee / 8.5

8.5. EDITORIAL COMMITTEE
Editorial coordination and production
Institut de Radioprotection et de Sûreté Nucléaire
Health and Environment Division
Environment Department
Coordinator
Philippe Renaud
Authors
Christelle Antonelli
Miriam Basso
Magalie Beguin-Leprieur
Pascale Blanchart
Valérie Bruno
Pedro Caldeira Ideias
Philippe Calmon
David Claval
Bruno Cessac
Catherine Cossonet
Céline Couvez
Donato D’Amico
Christophe Debayle
Claire GreauJérôme Guillevic
Olivier Masson
Gregory Mathieu
Jean-Michel Métivier
Nathalie Michielsen
Maxime Morin
Michael Petitfrère
Olivier Pierrard
Laurent Pourcelot
Philippe Renaud
Lionel Saey
Laure Tardieu
Damien Tournieux

351

Proofreading
The members of the RNM

RADIOLOGICAL REPORT OF THE FRENCH ENVIRONMENT FROM 2015 TO 2017 /For any additional information, please contact:
Institut de Radioprotection et de Sûreté Nucléaire
Direction de l’Environnement
31, avenue de la Division Leclerc
92260 Fontenay-aux-Roses
Emailcontact@irsn.fr

Report No.:IRSN DG/2018-00006
IRSN all rights reserved
November 2018

Cover photo:Landscape of the former open-pit uranium mine at Villeret-en-Lozère, now flooded. © IRSN
Graphic design & production:
Agence Kazoar
www.kazoar.fr

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