English (United Kingdom)

https://curated-unify.zendy.io/wp-json/zendy-region/v1/featured_content/oa?rat=en

https://curated-unify.zendy.io/wp-json/zendy-region/v1/highlighted_journal/

Global: Zendy Plus annual

Presents the access of premium content as premium feature

Premium Content

Presents the keyphrase highlighting as premium feature

Keyphrase Highlighting

Presents the summarisation as premium feature

Summarisation

Insights

Presents the pdf analysis as premium feature

PDF Analysis

Presents the zaia usage as premium feature

ZAIA

Global: Zendy Tools annual

Global: Zendy Free Plan

Global: Zendy Tools monthly

Global: Zendy Plus monthly

La nappe aquifère de Hesbaye, logée dans les craies du Crétacé, est sollicitée à raison de trente millions de mètres cubes par an. Bien que naturellement protégée par une épaisseur de 5 à 20 mètres de limons, de nombreux indices montrent une dégradation de la qualité des eaux souterraines, notamment par les nitrates. Les concentrations en nitrates atteignent 15 à 25 mg.l-1 dans la partie semi-captive de la nappe et sont systématiquement supérieures à 35 mg.l-1 dans la partie libre. Malgré de fortes fluctuations temporelles, les teneurs augmentent en moyenne de 0,35 mg.l-1 à 0,7 mg.l-1 par an selon la situation semi-captive ou libre de la nappe.La détermination des paramètres hydrodynamiques et de transport de la craie par plus de 35 traçages répartis sur 11 sites, a permis de réaliser un modèle local (10 km2) de transport simulant la propagation des nitrates dans la nappe. Le modèle a montré que cette dernière est, malgré une certaine homogénéisation, très sensible aux apports de surface engendrant une très forte variation spatiale des concentrations. La nappe réagit de manière très différente selon que les apports de surface sont d'origine ponctuelle ou diffuse. Pour les pollutions ponctuelles, les concentrations fluctuent rapidement avec des valeurs maximales et minimales observées respectivement en périodes de basses eaux et de hautes eaux. Cette situation est liée à un phénomène de dilution de la pollution par les eaux en provenance de l'amont. En cas de suppression d'une pollution ponctuelle, la qualité de la nappe s'améliore rapidement (délai de 1 à 2 ans). Pour les pollutions diffuses, les concentrations minimales s'observent en période de rabattement de la nappe : le front de nitrates migre plus lentement (environ 1 à 2 m par an) que les vitesses de rabattement de la nappe (jusqu'à 5 m par an) et les intrants restent nuls durant des périodes pouvant aller jusqu'à 3 ans.Différentes simulations mathématiques ont montré que si la quantité d'intrants d'origine diffuse diminue de manière permanente, la nappe mettra une vingtaine d'années pour se rééquilibrer. Ces constatations sont primordiales dans le cadre de la mise en œuvre de mesures de protection puisque, si les résultats de la suppression des pollutions ponctuelles sont rapidement mais localement observés, ceux liés à la diminution des pollutions d'origine diffuse sont observés dans des délais nettement plus longs (une à deux décennies).Ces résultats montrent clairement que toute gestion qualitative des aquifères doit être basée sur des actions à long terme.The Hesbaye area is located in the northeastern part of Belgium. The aquifer formations consist of chalk deposits. Groundwater provides about 80,000 m3 d-1. Despite 5 to 20 meters of superficial loess deposits, the groundwater quality is threatened by increasing nitrate concentrations of 0.35 mg×L-1 per year in the semi-confined part of the aquifer to 0.7 mg×L-1 in the unconfined aquifer. Presently, nitrate concentrations are between 15 and 25 mg×L-1 in the semi-confined part of the aquifer but are more than 35 mg×L-1 (reaching locally 150 mg×L-1) in the unconfined part that covers 95% of the area. Nitrate concentrations have such a high spatial variation that various statistical treatments (such as kriging used to draw iso-concentration maps) have failed. This failure is due to the fact that the concentrations are highly influenced by surface land use (grass land, culture land, villages, point source pollutants, etc.). In addition, nitrate content in the aquifer varies vertically with decreasing values at depth (gradient of 0.7 mg×L-1 ×m-1).Aquifer parameters were determined by 38 pumping and tracer tests conducted in radial convergent or cylindrical flow at 11 sites. Results showed that hydraulic conductivity values ranged from 1 × 10-6 m×s-1 to 4 × 10-2 m×s-1 and effective porosities from 0.5% to 7%, showing that the aquifer was heterogeneous. Dispersivity values were affected by scale effects and varied according to chalk weathering or fracture zones. They ranged from less than 5 m in fractures to more than 60 m in weathered chalk (as in the upper part of the aquifer) and in the chalk matrix. In the chalk, transport processes were influenced by the immobile water effect due to diffusive transfer from the moving to the non-moving fluid. Non-effective porosity filled by non-moving fluid was estimated between 8 to 42%. The transfer constant ranged from 0.98 × 10-7 s-1 to 10 × 10-7 s-1.The determination of the transport parameters allowed simulation of nitrate transport at a regional scale. The SUFT3D (Saturated and Unsaturated Flow and Transport Model), developed by the Hydrogeology Section of the Georesources, Geotechnologies and Building Materials Department of Liege University was used. The modelled groundwater zone was defined as a 2.0 x 4.5 km rectangle of 10 km2. The aquifer was subdivided into 6 layers of 3350 cells (50 x 50 m wide and 3 to 15 m thick). Boundary flow conditions were defined as a prescribed head (Dirichlet conditions) to the north and the south of the area modelled. As the model simulations run for a time period of 30 years, the northern Dirichlet conditions had to be adapted to the regional and seasonal water table fluctuations that were observed during this period. At the south boundary, as the aquifer is drained by the river Geer, the water table is fixed at the river bed altitude. The eastern and western boundaries were, according to the regional piezometry, assumed to be impermeable. For the transport boundary conditions, prescribed flux (Cauchy conditions) was used for the aquifer top. Elsewhere Neumann conditions were usedSimulations were run for the period from 1963 to 1992. Nitrate inputs were averaged yearly and estimated according to actual input conditions. These conditions were calculated by simulation of nitrate flows through the non-saturated part of the aquifer using the EPIC-Model and taking into account the amount of nitrate fertilisers used by farmers (given by the Belgian government Statistical Institute). Initial conditions were calculated according to the 1963 nitrate inputs.Simulations demonstrated that it is important to distinguish the origin of the pollution as either point or non-point (diffuse) sources. For point source pollutants (such as contaminated infiltration basins), aquifer nitrate concentrations increased during low water level periods due to weaker dilution linked with a poor regional water gradient. During high groundwater levels, dilution is more important and the nitrate concentration decreases. If a point source pollutant is suppressed, aquifer quality is improved within one to two years. This demonstrates the importance of protective actions that could be applied within the framework of the protection zones around collecting galleries and pumping fields.For diffuse contamination the mean input over the area (10 m depth below cropped areas) increased from 1.32 × 10-7 mg×m-2 ×s-1 in 1963 to 5.14 × 10-7 mg×m-2 ×s-1 (i.e., a factor of four). According to these values, concentrations ranged from 11 mg×L-1 to 22 mg×L-1 (i.e., increasing by 0.5 mg×L-1 per year) between 1963 and 1992. Predictive simulations, using 1992 input, show that it will take more or less 30 years for the aquifer to be in equilibrium with the 1992 input. At that time the mean concentration value will be around 30 mg×L-1.The main results of the simulations clearly show that if actions are taken to decrease nitrate inputs, even if the aquifer nitrate contents rapidly react to the new input, nitrate levels will decrease slowly and take about 30 years to be in equilibrium with the new inputs. This long delay is due to the immobile water effect that is characteristic of the chalk aquifer. Thus it is important to inform environmentalists who work on action programs (such as the water directive imposed by the European Community in the vulnerable zones) that the effects of their actions must be based on 10 to 20 year scenarios. To this estimation, based on the reaction time of the aquifer to a new input, one must also add the time transfer of the pollutant through the unsaturated part of the aquifer

Modélisation mathématique de l'évolution, à long terme, des teneurs en nitrates dans la nappe aquifère des craies du Crétacé de Hesbaye (Belgique)