CH4 and CO2 emissions from geologic sources, which are devoid of radiocarbon (14C), dilute the atmospheric 14C/C ratio. Observations of 14C/C can be used to estimate fossil fuel-derived CH4 and CO2. However, the atmospheric 14C/C ratio is perturbed by emissions of 14C from nuclear power plants (NPPs) and fuel reprocessing sites, which may affect such 14C/C-based estimation if they are not correctly quantified. We calculate NPP 14C emissions for CO2 and CH4 from 1972–2016 using standard emission factors (14C emitted per unit of power produced) and analyze trends in global and regional emissions. We use available observations of 14C emissions and power generation in Europe to assess emission factors for different reactor types, as well as potential differences related to the age or manufacturer of the NPPs. Globally, nuclear 14C emissions increase until 2005 and then decrease, mostly because of the closure of gas-cooled reactors in the United Kindom and the shutdown of light water reactors after the Fukushima nuclear accident in March 2011. Observed emission factors in Europe show strong variability, spanning values from 0.003 to 2.521 TBq/GWa for PWR and from 0.007 to 1.732 TBq/GWa for BWR reactors, suggesting more information and more sophisticated models are needed to improve estimates of 14C emissions.

Due to an increasing number of nuclear reactors in operation, the radiocarbon (14C) released from nuclear power plants (NPPs) has become an important anthropogenic source of 14C. The examination of seasonal Δ14C and monthly Sr/Ca, Mg/Ca variations in a coral in Daya Bay (China) shows that NPPs located there have an impact on the Δ14C level and sea surface temperature (SST). The Mg/Ca variation was in good correlation with the Pacific Decadal Oscillation (PDO) before the operation of Ling’ao NPP in 2002, but this correlation became weak due to an abnormally higher SST after 2002. As illustrated by the Δ14C variation in the coral, there were two relative increases of Δ14C values in 1994 and 2002 when Daya Bay NPP and Ling’ao NPP began operations, respectively. The 14C released from NPPs, instead of oceanic circulation, is probably the primary factor on the Δ14C variation in Daya Bay during the NPPs’ operation. The relative increase in Δ14C value was ~80‰, which equals to ~18 Bq/kgC in specific activity. The seasonal variability in Δ14C value usually peaked in summer, the real reason of which was unknown. This study sheds light on how the NPPs influence the 14C content and SST in surrounding marine environment.

We performed an Environmental Risk Assessment (ERA) to evaluate the impact on non-humanbiota from liquid radioactive effluents discharged by the Belgian Nuclear Power Plants(NPPs) of Doel and Tihange. A deterministic risk assessment for aquatic and terrestrialecosystems was performed using the ERICA tool and applying the ERICA screening value of 10µGy.h-1. The ERA was performed for the radioactive discharge limits and forthe actual releases (maxima and averages over the last 10 years, 1999-2008). All ERICAreference organisms were considered and depending on the assessment situation, additionalreference organisms were included in the analysis. It can be concluded that the currentdischarge limits for the Belgian NPPs do not result in significant risks to the aquaticand terrestrial environment and that the actual discharges, which are a fraction of theliquid discharge limits, are unlikely to harm the environment.

Dans le domaine des eaux douces, un très grand nombre de travaux ont été réalisés pour caractériser les échanges des radionucléides entre phases solide et liquide constituant les compartimentsphysiques des écosystèmes naturels. Ces échanges dépendent des conditions physiques, chimiques et biologiques régnant dans le milieu. Généralement le concept de Kd ou coefficient dedistribution, est utilisé pour quantifier la répartition du radionucléide entre phase dissoute et particulaire. Les principaux paramètres environnementaux influençant la valeur du Kd sont les suivants : temps de contact, concentration en matières en suspension, nature et granulométrie de la phase solide (plus particulièrement pour le césium, le cobalt, le manganèse, l'argent, l'iode),concentration en isotopes stables des phases solide et liquide (césium, cobalt, manganèse, argent), composition minérale de la phase liquide (césium), pH de l'eau (cobalt, manganèse, argent),conditions d'oxydoréduction des deux phases (césium, manganèse), composés organiques dissous (cobalt, antimoine, iode). Ainsi, en liaison avec l'influence de ces divers paramètres, la gammede variation du Kd est très vaste pour chaque radionucléide. Cette gamme peut être réduite, pour un écosytème à un moment donné de son cycle hydrologique, si les valeurs in situ des paramètresmajeurs influençant les échanges entre phases sont connus. La réalisation d'expériences, en laboratoire et/ou de terrain permet de déterminer la valeur de Kd adaptée à la situation étudiée.