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Radionuclide sheet

Carbon-14 and the environment




Emitting b radiation with a half-life of 5730 years, Carbon 14 follows the cycle of the stable element C, one of the components of the living materials, in which it is diluted. Carbon-14 is indeed around 10-12 times less abundant than stable carbon. The main source of exposure is due to naturally occurring 14C (cosmogenic origin).


With regard to the impact of chronic releases, the general consensus is that 14C behaves in the same manner as the stable 12C isotope (representing 99% of carbon). Carbon-14 transfers between two compartments of the environment are generally evaluated based on the assumption that the isotopic ratio between the radioactive carbon and the stable carbon (considered to be 12C) is maintained, between the organism and the surrounding environment. This assumes that the transfer of the trace radionuclide 14C is identical to that of 12C and that equilibrium between the two compartments is achieved. Under this assumption, the impact on the environment and populations can only be evaluated for environmental releases and concentrations that are constant over time, generally by using average annual values.


The environmental toxicity of 14C is only related to radioactive emissions of the pure, low-energy b type. This toxicity is mainly the result of internalisation, essentially by ingestion.




Chemical characteristics


Carbon-14 (14C) is a radioactive carbon isotope present in infinitesimal quantities in the atmosphere. Carbon-12 and carbon-13 are the stable carbon isotopes and respectively represent 98.9% and 1.1% of the total carbon. Carbon-14 only exists in trace quantities. The chemical forms of 14C vary according to the method of production. In the environment, 14C exists in two main forms:

- as 14CO2, it acts as stable carbon dioxide, which means it can remain in gas form in the air, becoming bicarbonate and carbonate in water

- during photosynthesis, 14CO2 is incorporated in the organic material, forming its carbon skeleton. Equilibrium between the specific activity of atmospheric carbon and that of organic material is then finally reached and maintained by carbon recycling.


In the gaseous effluents of boiling water reactors, 14C is 95% 14CO2, 2.5% carbon monoxide (14CO) and 2.5% hydrocarbon. In the gaseous effluents of pressurised water reactors, it is assumed that 80% of 14C is in organic form (14CH4) whereas 20% is in the form of 14CO2. In the liquid releases, the carbon chemical species are carbonates and various organic compounds, their relative quantities being currently unknown.



Nuclear characteristics


Carbon has 15 isotopes, with masses of 8 to 22. Only isotopes 12 and 13 are stable. The radioactive half-life is higher than a year only for carbon-14, its maximum value for the other isotopes being around 20 minutes.


Carbon-14, a beta- emitter, gives rise to stable 14N with 100% yield.



 (Nucleonica; CE, 2011)









Natural origins


Natural 14C results from cosmic neutrons acting on nitrogen atoms in the stratosphere and in the upper troposphere (14N +n →14C+1p). The annual production level is around 1.40 x 1015 Bq and the atmospheric stock of carbon-14 at equilibrium is around 140 x 1015 Bq (UNSCEAR, 2008). Production fluctuates due to variation in cosmic ray intensity. This fluctuation results from various factors that are not yet well understood, but mainly include the 11-year solar cycle and, on a larger temporal scale, variations in the terrestrial magnetic field that serves as a shield against cosmic rays (Garnier-Laplace et al., 1998).



Artificial origins


  • Fallout from atmospheric nuclear explosions

During nuclear explosions, the emitted neutrons interact with atmospheric nitrogen, as cosmic neutrons do, to form carbon-14, according to the same reaction as above: 14N +n →14C+1p.


Nuclear explosions carried out before 1972 released around 3.5 x 1017 Bq of carbon-14. Later explosions increased this amount by around 1% (UNSCEAR, 2008).


  • Nuclear reactor releases


In nuclear reactors, carbon-14 is produced from reactions in the fuel, the core structural materials and the moderator. The production rate depends on the spectrum and the neutron flux, on cross-sections and on the concentration of the following target elements: uranium, plutonium, nitrogen and oxygen. Water in the primary coolant circuit of pressurised water reactors contains excess hydrogen that combines with oxygen from radiolysis. In this reducing environment, compounds such as methane (CH4) and ethane (C2H6) form. Most of the carbon-14 released in a pressurised water reactor is in the form of alkanes. Various estimations indicate that the annual production rate for a light water reactor (pressurised or boiling water reactor) is between 0.5 and 1.9 x 1012 Bq/GWe/year, with carbon-14 mainly taking organic forms (CH4). The rest is released during reprocessing, or remains in the fuel cladding and is later disposed of as solid waste (Garnier-Laplace et al., 1998).


  • Releases by irradiated fuel reprocessing plants


Spent nuclear fuel 14C is released during the dissolution step in reprocessing plants. Depending on the operating mode, these releases are continuous or discontinuous. In reprocessing plants that use the PUREX process (e.g. the AREVA NC La Hague plant), the 14C is mainly released as CO2. Commissioning of the UP3 and UP2-800 plants at La Hague resulted in increased annual gaseous 14C releases starting in the early 1990s. In 2009, the gaseous releases of carbon-14 at the site corresponded to 1.45 x 1013 Bq and the liquid releases corresponded to 6.12 x 1012 Bq. Carbon-14 in fuel cladding is not released during dissolution and remains trapped. It is disposed of later as solid waste.


At the Sellafield plant in the UK in 2009, the 14C gaseous releases reached 3.8 x 1011 Bq and the liquid releases, 8.2 x 1012 Bq (Sellafield Ltd, 2009).


  • Various sources (medical, industrial, research) 


In research, carbon-14 is widely used in carbonate form for isotopic labelling of molecules. The activities used are greater than 1 GBq. For example, carbon-14 is used to study metabolic dysfunction related to diabetes and anaemia. It can also be used as a marker to track the metabolism of new pharmaceutical molecules. More generally, carbon-14 can be used to uncover new metabolic pathways, and to identify their normal functioning and any departures from it, e.g. for photosynthesis (Calvin and Benson, 1948) or, more recently, for the methylaspartate cycle in halobacteria (Khomyakova et al., 2011).


It is assumed that all 14C used for labelling molecules will be released into the atmosphere as CO2. According to UNSCEAR, the annual production of 14C is equivalent to 3 x 1010 Bq per million inhabitants in developed countries and to 5 x 1013 Bq worldwide. This estimation is based on the results of a 1978 US study. A 1987 British estimation led to values at least twice as high (UNSCEAR, 1993).



Environmental concentrations


  • Carbon-14 background in the environment and changes over the last 60 years


In the terrestrial environment, the consensus (relatively well supported by observations) is that the specific activity, expressed in becquerels of 14C per kilogram of total carbon, is constant in the environmental components and at equilibrium with the specific activity of atmospheric CO2 (Roussel-Debet et al., 2006, Roussel-Debet, 2007, 2009). Uninfluenced by nuclear facilities, the 14C specific activities for the biological compartments of the terrestrial environment reached their maximum values (more than 400 Bq/kg of C) in the mid-1960s, due to fallout from atmospheric nuclear arms testing, then at its height (Figure 1). These activities have slowly decreased since then (by less than 0.5% per year) with the end of testing and the continuous increase in CO2 from fossil fuels (gasoline, coal, gas). The specific activities of terrestrial biological compartments are currently around 238 Bq 14C/kg C (2009 measurements), which is very close to 1950 values (226 Bq/kg C), before atmospheric testing.



Figure 1: Changes in average specific activity of carbon-14 (Bq/kg C) for biological compartments sampled in terrestrial environment, during the last 60 years 


In aquatic environments, the specific activity of 14C varies with its dilution in carbon substances, particularly carbonates from old sedimentary rocks lacking carbon-14. Unlike the terrestrial environment, 14C in freshwater ecosystems is not in equilibrium with atmospheric CO2: freshwater specific activity is then lower, around 200 Bq/kg C.

Based on the specific activity and the total proportion of carbon in the various environmental matrices (air, plants, animals and thus food products), the activity concentration for the 14C in these matrices can be estimated (Figure 2). The more carbon the product contains (sugars, oils, grains, etc.), the higher the activity.



Figure 2: Carbon-14 activity concentration range for food products


Depending on the proportion of carbon per wet mass unit of food product, the activity concentration of these products varies between less than 15 (lettuce, mussels) and more than 80 (grains) Bq/kg wet. Atmospheric activities vary from 3 x 10-2 to 7 x 10‑2 Bq/m3. Carbon-14 thus has the highest environmental activities amongst the radionuclides released from nuclear facilities.


  • Influence of nuclear facilities


With atmospheric releases of around 2 x 1013 Bq/year of 14C, mainly as CO2, the AREVA-NC La Hague plant causes an added carbon-14 activity (above the natural background) regularly detectable in the site's terrestrial environment, leading to specific activities of 500 to 1000 Bq/kg C, and occasionally 2000 Bq/kg C. The corresponding activity concentrations range from 20 to 140 Bq/kg of wet grass or vegetables, compared with a background of around 5 to 20 Bq/kg of wet material in this type of matrix. In milk and meat, this contamination is also significant although much less so, probably due to a feeding component outside the area influenced by the atmospheric releases. Note that the maximum radioactivity in the air at ground level after dispersion, set at 1 Bq/m3 by the French order authorising AREVA-NC La Hague releases, would correspond to specific activity in plants of 5000 Bq/kg C, if attained at all times throughout the year.


The carbon-14 addition around nuclear power plants (atmospheric releases of 0.2 to 1x1012 Bq/year) is extremely limited: the associated specific activity is around 3 Bq/kg C in addition to the 243 Bq/kg of C representing the average background for 1994-2003 (Roussel-Debet et al., 2006), i.e. an added activity of around 1%. This low level is the result not only of low releases, but also of a clear predominance of releases in the form of methane (CH4), which plants cannot assimilate.


In rivers, the carbon-14 released by nuclear power plants is diluted in the dissolved stable carbon from carbonates, which are found in sediment. This significantly decreases the specific activity of carbon-14 in physical components. For semi-underwater aquatic plants, dilution also occurs in the atmospheric CO2 used during photosynthesis; the associated specific activities rarely exceed 400 Bq/kg C. For reasons that remain to be elucidated, fish do not seem to benefit from these dilution phenomena. Their specific activity under the influence of nuclear power plants regularly exceeds 600 Bq/kg C and may reach 1000 Bq/kg C.




Metrology, analytical techniques and detection limits


Carbon-14 in an environmental sample may be quantified by activity measurement or by atom counting. These two destructive techniques require converting the sample to CO2 (Maro et al., 2008).


Activity measurement 


  • Principle

The carbon contained in the test portion is transformed to carbon dioxide from which a sample is prepared for measurement by liquid scintillation (AFNOR, 2006).

Two sample preparation methods are mainly used: combustion by oxydiser and benzene synthesis (Fournier et al., 1999).


Preparation of samples by oxydiser

The sample is placed in a cellulose cone, which is inserted in a platinum filament. The entire unit is placed in a combustion chamber. Voltage applied to the ends of the filament in the presence of O2 causes combustion of the sample. The combustion gases are pushed by nitrogen in a column containing Carbosorb®, which traps CO2 in the form of carbamate. This mixture is eluted from the column by the scintillation liquid and then collected for measurement.


The oxydiser allows to prepare several samples per day for counting. The test portions are generally less than 0.5 g of the dry sample. They must be rich enough in carbon to undergo a complete oxidation.


Combustion yield must be determined on a reference sample labelled for 14C. This reference sample must be as close as possible in nature and composition to the samples to be analysed.


The 14C naturally contained in the combustion cone cellulose contributes to the increase in background and thus in higher measurement uncertainty. Background must thus be determined as precisely as possible.


The expression of the sample's activity in Bq of 14C per kg of carbon also requires measuring its elementary carbon content, generally by gas chromatography.


The measurement uncertainty, around 30 to 40% (k=2) for activities of around 260 of carbon (natural level in the environment), makes it difficult to detect low concentrations with this method. This uncertainty can, however, be reduced by increasing the test portions or by combining the measurements of several test portions from the same sample. 



  • 14C analysis by benzene synthesis


The sample is burned in the presence of under pressure oxygen in a combustion bomb. The CO2 produced is then reduced by a heated reaction with lithium to obtain lithium carbide (Li2C2), the hydrolysis of which produces acetylene (C2H2), which is trimerised by catalysis in benzene (C6H6).


The counting vial is prepared by weighing out synthesised benzene and scintillants. Spectroscopy-quality benzene is added if needed.


The activity of the 14C present in the vial is then measured using liquid scintillation. The result can be directly converted into Bq/kg of carbon.


The test portions consist of 7 to 10 g of finely ground, dry sample. The chemical processing time for one sample is 3 days, 2 more days being necessary for counting. Uncertainty at the level of the environmental background corresponds to 6 to 7% (k=2).


This method is suitable for solid dry samples containing high carbon and for water matrices in the form of carbonate (e.g. barium carbonate). For water matrices, CO2 is extracted from the sample by acid attack (e.g. addition of orthophosphoric acid) rather than by combustion bomb. The rest of the protocol does not change.


The analysis methods involving oxydiser or benzene synthesis are not well suited for carbon-poor matrices, such as soil and sediment.  



Atom counting


  • Principle


The carbon present in the sample is extracted in the form of ions. The carbon ions are accelerated, sorted by mass in a magnetic field which alters their trajectory. They are then counted.


  • 14C measurement by accelerator (AMS)


After decarbonation and combustion of the sample, the CO2 obtained is reduced by H2 in the presence of powdered iron. The carbon is deposited on the powdered iron and the mixture is pressed into a target to allow for measurement by mass spectrometry. The sample's 14C activity is calculated by comparing 14C, 13C and 12C beam intensities, measured sequentially, with the CO2 reference intensities.


The test portions consist in around 0.10 g of material. Uncertainty at the level of the environmental background corresponds to 2 to 3% (k=2).


Accelerator Mass Spectrometry (AMS) is characterised by high sensitivity, which is obtained by good separation of 14C from other ions having the same mass (particularly nitrogen). It is favoured for low-quantity samples or those containing low levels of organic materials (soil, sediment, sea water, air samples, etc.).


  • Expression of results


The activity concentration results are expressed in Bq/kg of dry material, Bq/kg of wet material or Bq/kg of carbon.



Mobility and bioavailability in terrestrial environments


Carbon-14 data and the models on the fate of this radionuclide in terrestrial environments (Scott et al., 1991; Sheppard et al., 1994; Garnier-Laplace et al., 1998; Fontugne et al., 2004; Tamponnet, 2005a and b) are based on knowledge of the carbon cycle at equilibrium (Ouyang and Boersma,1992). Carbon-14 is integrated in the carbon cycle, which is very complex due to the presence of inorganic and organic carbon, in solid, liquid or gaseous forms (Figure 3).



Figure 3: Carbon cycle in soil-plant-animal systems





The average quantity of carbon in organic material of cultivated soils is in France around 20 g of carbon per kg of dry soil. The soil solution carbon can be in the form of CO2, carbonate (CO32-) or bicarbonate (HCO3-), depending on the pH and the quantity of calcium ions.




The average CO2 quantity of gaseous soil phase varies from 0.5 to 1%. It increases in the presence of plants (due to root respiration, the pH decreases and the dissolved CO2 increases by around 38% per pH unit).


Root absorption of carbon by plants is negligible. Root incorporation from carbonate ions, poorly understood, appears to represent 5% maximum of the total carbon incorporated in a plant. Most of the carbon is assimilated by leaves as CO2 during photosynthesis. Isotopic discrimination, which depends on the plant's photosynthetic cycle, is negligible (14C / 12C ratio less than 5% maximum between the plant and the atmospheric CO2).


CO2 emanation from the mineralisation of organic soil residues and root respiration tends to increase the concentration of CO2 in the air, at the plant cover level. The daily flux of CO2 released by the soil appears to be 2 to 13 g per m2. This flux appears to contribute around 10% to the total carbon assimilated by leaves during photosynthesis (Le Dizès-Maurel et al., 2009).





More than 99% of the carbon incorporated by livestock comes from their feed. Carbon from inhalation is negligible, as is carbon from ingestion of water or soil.



Mobility and bioavailability in continental aquatic environments


Carbon-14 data and the models on the fate of this radionuclide in continental aquatic environments (Sheppard et al., 1994; Garnier-Laplace et al., 1998) are based on knowledge of the carbon cycle at equilibrium (Stumm and Morgan, 1981; Amoros and Petts, 1993).


The 14C organic compounds released by nuclear facilities are incorporated into the organic carbon of the hydrosystem that receives them (Figure 4).



 Figure 4: Carbon cycle in freshwater hydrosystems


The inorganic carbon released by nuclear facilities or present in the hydrosystem takes the form of species in the carbonate system (CO2 aqueous/HCO3-/CO32-), which is one of the main chemical systems involved in controlling freshwater pH. In most running waters, pH varies from 6 to 9, with bicarbonate forms dominating. Carbon-14 in liquid effluents, released as carbonates, is incorporated in the inorganic carbon. Isotopic dilution varies according to atmospheric exchanges, run-off contribution and exchanges with hydrogeological systems. In all cases, the specific activity of inorganic 14C must be considered in terms of the value measured in situ for total CO2, according to the following equation: [CO2]total = [CO2]aq + [HCO3-] + [CO32-].



Water and sediment


Carbon-14 is integrated in the carbon cycle of continental hydrosystems where the main forms are organic carbon (dissolved organic carbon/DOC, 1 to 3 mg of carbon per litre; and particulate carbon, which is highly variable from one hydrosystem to another) and inorganic carbon (essentially in the form of dissolved bicarbonate, 1 to 120 mg of carbon per litre). Humic and fulvic acids represent from 50 to 75% of the DOC, whilst the colloidal forms represent 20%. The particulate forms are also varied: allogenic detrital forms, living organisms and compounds from their decay.





Transfers to plants are governed by photosynthesis. Photosynthesis is mainly carried out by higher plants, periphytic and planktonic algae, and cyanobacteria. In schematic terms, it can be considered the dominant biological process that influences the concentration of inorganic carbon in the hydrosystem; respiration and bacterial fermentation can be considered negligible. On average, the concentration of total carbon in freshwater plants is 5 x 104 mg of carbon per kilogram of wet material.





Transfers to animals are governed by ingestion. For aquatic organisms, the processes of respiration and osmoregulation that use inorganic carbon are similarly negligible in the animal's carbon balance compared to transfers via food ingestion. Carbon concentration in animals varies from one species to another.



Mobility and bioavailability in marine environments


The mechanisms of 14C transfer in marine and freshwater environments are identical, and the models are based on the assumption that equilibrium is reached due to environmental carbon recycling. Most of the 14C released into the sea is in dissolved inorganic form and is incorporated by organic material. Close to release points, when the variations in the quantities released are rapid and large, equilibrium between the specific activities of the organic material and the sea water is not always reached (Fiévet et al., 2006).



Sea water


In the Channel, the research of Douville et al. (2004) indicates that the 14C in sea water at Cap de La Hague mainly takes the form of dissolved inorganic carbon (dissolved CO2, HCO3-, CO32-), which is the predominant form of carbon in sea water, with activities between 300 and 800 of carbon.





As in the case of freshwater plants, the transfer of 14C to seaweed occurs by photosynthesis. The total carbon concentration in seaweed is roughly equivalent to the freshwater plant concentration. This concentration was found to be 8 ´ 104 mg of carbon per wet kilogram of the brown seaweed Fucus serratus, an example of the algal flora of north-western European coasts. Used as a model compartment for 14C exchanges between sea water and a photosynthetic organism, this alga was used to estimate a biological half-life for 14C of around 5 months. The value of this parameter explains the absence of equilibrium close to the release point (Cap de La Hague), where the variations in seawater 14C concentration are large and rapid, due to the history of releases by the AREVA NC reprocessing plant (Fiévet et al., 2006).





As in the case of the terrestrial and freshwater animals, transfers to marine animals are mainly governed by ingestion. Although cell membranes are permeable to bicarbonates dissolved in water, the quantity of absorbed carbon that they represent is low compared to the carbon incorporated in organic material. The carbon concentration by unit of wet weight in marine animals varies a great deal from one organism to another, especially due to the different water contents (e.g. jellyfish, bivalves, gastropods, echinoderms, crustaceans, fish, etc.). The limpet has been used as a model compartment for 14C exchanges between sea water and a grazing animal, making it possible to estimate a biological half-life for 14C of around 8 months. This half-life integrates all the transfer pathways between the sea water and the gastropod's flesh, including 14C incorporation from the animal's food source. Biological half-life is estimated to be around 1 month in mussels, which are used as a model of filtering organisms (Fiévet et al., 2006). Although there is great variability in the speed of carbon recycling between sea water and the different biological compartments, these half-life values clearly explain why a state of equilibrium is not reached where the sea water 14C concentration may vary rapidly, close to release points for example.



Mobility and bioavailability in semi-natural ecosystems


This section is based on the international literature review conducted for the revision of the IAEA handbook on parameter values for predicting radionuclide transfer in terrestrial and temperate continental aquatic environments (IAEA, 2010).




There is no specific information on the mobility and bioavailability of carbon-14 in forest ecosystems.



Artic ecosystems


There is no specific information on the mobility and bioavailability of carbon-14 in arctic ecosystems.



Alpine ecosystems


There is no specific information on the mobility and bioavailability of carbon-14 in alpine ecosystems.



Environmental dosimetry


The effects of exposure to ionising radiation depend on the quantity of energy absorbed by the target organism, expressed by a dose rate (µGy/h). This dose rate is evaluated by applying dose conversion coefficients (DCCs, µGy/h per Bq/unit of mass or volume) to radionuclide concentrations in exposure environments or in organisms (Bq/unit of mass or volume).


The characteristic 14C DCCs were determined without considering decay products and without RBE weighting. Version 2.3 of EDEN software (Beaugelin-Seiller et al., 2006) was used, taking into account shape, dimensions and chemical composition of the organisms and of their environments, as well as their geometrical relations. The modelled species were chosen as examples.


Except in the particular case of the fescue (10-3 µGy/h per Bq/kg wet), internal exposure is generally characterised by DCCs of around 10-5 µGy/h per Bq/kg wet.


External exposure is characterised by lower DCCs that vary according to the organism, within a range of 10-10 and 10-5 µGy/h per Bq/kg.


For more details on how to calculate DCC, see the Environmental Dosimetry Sheet.



Environmental toxicity


Element chemotoxicity


Not applicable



Radiotoxicity of the radioactive isotope 14C


Carbon-14 is a low b emitter, with a low penetrating power which causes radiation stress mainly due to internal irradiation, if the 14C is incorporated. Carbon-14 is interesting from a radiobiological standpoint because it is integrated in cellular components (proteins, nucleic acids), particularly cellular DNA (Le Dizès-Maurel et al., 2009). The resulting DNA damage, involving molecular breaks, may lead to cell death or induce potentially inheritable mutations.


However, there is currently not enough data to determine whether the ecosystem protection threshold criterion of 10 µGy/h is relevant for 14C (Le Dizès-Maurel et al., 2009). This criterion is consensual in Europe relative to chronic exposure to external gamma radiation.

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14C environment sheet

The others radionuclides sheets


Revision in 2010



  • Terrestrial ecosystem

Séverine Le Dizès-Maurel


  • Continental aquatic ecosystem

Frédéric Alonzo


  • Marine ecosystem

Bruno Fiévet


  • Metrology

Béatrice Boulet

Jeanne Loyen

Jean-Louis Picolo


  • Concentrations in the environment

Philippe Renaud





Dominique Boust

Karine Beaugelin-Seiller

Christian Tamponnet

Selected bibliography

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  • Amoros C and Petts GE (1993). Hydrosystèmes fluviaux. Collection d’écologie, Masson, Paris.
  • Beaugelin-Seiller K, Jasserand F, Garnier-Laplace J, Gariel JC (2006). Modelling the radiological dose in non-human species: principles, computerization and application. Health Phys, 90 : 485-493.
  • BIOPROTA (2010). C-14 Long-Term Dose Assessment: Data Review, Scenario Development, and Model Comparison, WORKSHOP REPORT, L. Limer & M. Thorne (Eds), April 2010.
  • Calvin M and Benson AA (1948) .The Path of Carbon in Photosynthesis. Science 107: 476-480
  • Ciba-Geigy (1981). “Units of measurement, body fluids, composition of the body, nutrition”, Geigy Scientific Tables, Vol. 1, 8th edn, Ciba-Geigy Ltd., Basel (1981).
  • CE - Commission Européenne (2009). Nucleonica...web driven nuclear science. (page consulted 6 June 2011).
  • Douville E, Fiévet B, Germain P, Fournier M (2004). Radiocarbon behaviour in seawater and the brown algae Fucus serratus in the vicinity of the COGEMA La Hague spent fuel reprocessing plant (Goury) - France. J Environ Radioactiv 77: 335-368
  • Fiévet B, Voiseux C, Rozet M, Masson M, Bailly du Bois P (2006). Transfer of radiocarbon liquid releases from the AREVA La Hague spent fuel reprocessing plant in the English Channel. J Environ Radioactiv 90: 173-196
  • Fontugne M, Maro D, Baron Y, Hatté, Hébert D, Douville E (2004). 14C sources and distribution in the vicinity of La Hague nuclear reprocessing plant: Part 1. Terrestrial environment. Radiocarbon, 46 : 827-830.
  • Fournier M, Henry A, Loyen J (1999). Oxidiser et benzène : deux méthodes de mesurage du. 14C, Journées Techniques CETAMA « Mesures et analyses dans les matrices environnementales et biologiques ».
  • Galeriu D, Melintescu A, Beresford NA, Crout NMJ, Peterson R, Takeda H (2007) Modelling 3H and 14C transfer to farm animals and their products under steady state conditions. J Environ Radioactiv, 98:205-217
  • Garnier-Laplace J, Roussel-Debet S, Calmon P (1998). Modélisation des transferts du carbone 14, émis par les réacteurs à eau pressurisée en fonctionnement normal, dans l'environnement proche du site. Rapport IPSN/DPRE/SERE 98/007, IRSN, Cadarache.
  • IAEA (2010). Handbook of Parameter Values for the Prediction of Radionuclide Transfer in Terrestrial and Freshwater Environments, Technical Reports, Series No.472, IAEA, Vienna.
  • Khomyakova M, Bükmez Ö, Thomas LK, Erb TJ, Berg IA (2011) A Methylaspartate cycle in Haloarchaea. Science 331:334-337.
  • Le Dizès-Maurel S, Maro D, Lebaron-Jacobs L, Masson M (2009). « Carbone 14 », in Chapitre 31, Toxicologie nucléaire environnementale et humaine. Ménager M.T., Garnier-Laplace J., Goyffon M. (Coord). Editions Tex&Doc – Lavoisier., 603-618.
  • Maro D, Masson M, Fiévet B, Bailly du Bois P, Connan O, Boust D, Germain P (2008). Analyse critique des données disponibles de carbone 14 et de tritium dans le nord Cotentin et en Manche. IRSN, rapport DEI/SECRE 2008-006.
  • Ouyang Y and Boersma L (1992). Dynamic oxygen and carbon dioxide exchange between soil and atmosphere. Soil Science Soc Am J, 56: 1695-1710.
  • Roussel-Debet S (2007). Evaluation of 14C doses since the end of the 1950s in metropolitan France. Radioprotection, 42 (3): 297-313.
  • Roussel-Debet S. (2009). Bilan des mesures OPERA terrestre 2007-2008. IRSN, rapport DEI/SESURE 2009-19.
  • Roussel-Debet S, Gontier G, Siclet F, Fournier M (2006). Distribution of carbon 14 in the terrestrial environment close to French nuclear power plants. J Environ Radioact 87(3): 246-259
  • Roussel-Debet S, Claval D (2010). Constat radiologique régional -Étude prototype « Val de Loire ».IRSN, rapport DEI/SESURE 2010-22.
    Sellafield Ltd ( 2009). Monitoring our Environment. Discharges and Monitoring in the United Kingdom. Annual Report 2009. (Consulted 17 November 2010).
  • Scott EM, Baxter MS and McCartney M (1991). Considerations on the modelling of environmental radiocarbon. BIOMOVS. Symposium on the validity of environmental transfer models. Stockholm (Sweden). SSI. 498 Swedish Radiation Protection Institute, Stockholm (Sweden), pp. 107-123.
  • Sheppard S.C., Amiro B.D., Sheppard M.I., Stephenson M., Zach R., Bird G.A. (1994). Carbon-14 in the biosphere: Modeling and porting research for the Canadian Nuclear Fuel Waste Management program, Waste-Management, 14 (5) 445-456
  • Stumm W and Morgan JJ (1981). Aquatic Chemistry. John Wiley, New-York.
  • Tamponnet C (2005a) Dynamics of Carbon 14 in soils: A review, Radioprotection 40: 465-470.
  • Tamponnet C (2005b) Modelling Tritium and Carbon in the environment: A biomass-oriented approach, Radioprotection 40: 713-719.
  • United Nations Scientific Committee on the Effects of Atomic Radiation (UNSCEAR) (1993). Report of the general assembly, with annexes. United Nations publications, New York.
  • United Nations Scientific Committee on the Effects of Atomic Radiation (UNSCEAR) (2008). Sources and effects of ionizing radiation. Report Vol. I: sources. United Nations publications, New York.



Modelling transfers of carbon 14 emitted by pressurised water reactors under normal operating conditions, in continental ecosystems (05/06/2002)

S. Roussel-Debet, J. Garnier-Laplace, C. Mourlon and P. Calmon Actes du congrès ECORAD, 3-7 sept 2001, Aix en Provence, France Radioprotection - Colloques, volume 37, C1-141 / C1-146.


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