Nitrate pollution of water resources is a global problem (Almasri, 2007). In some regions, the guideline values of groundwater and drinking water regulations are considerably exceeded in surface waters, but also in groundwater (Carrey et al., 2014). Several European Union member states, including Germany, were penalized by the European Court of Justice for non-compliance with the Nitrate Directive (European Court of Justice, 2010Justice, , 2018. However, further infringements and sanctions are to be expected. This contamination results mainly from anthropogenic N fertilizers used to increase agricultural productivity (Hosono et al., 2013). Excess N enters groundwater as NO 3 − . Due to a geogenic NO 3 − degradation capacity of most aquifers (sulfide minerals and organic C), part of the NO 3 − can be degraded (Rivett et al., 2008). Based on sulfide-S and organic C contents of the aquifer, groundwater recharge and NO 3 − concentration, the remaining time until a NO 3 − breakthrough to drinking water production wells may be calculated (e.g., Ortmeyer, Volkova, et al., 2021). Overall, a link between hydrologic and water quality models is important because including transit times can improve understanding of NO 3 − transport in aquifers (Hrachowitz et al., 2016). In the future, considerable increases in NO 3 − concentrations and NO 3 − breakthroughs to raw water wells are expected, as this degradation capacity is decreasing and finite (Knowles, 1982;Schwientek et al., 2017). Climate change is expected to enhance this deterioration of water resource quality and quantity (Fleck et al., 2017;Ortmeyer, Mas-Pla, et al., 2021). In addition to a decrease in groundwater recharge and a drop in water levels, Stuart et al. (2011) point to possible increasing rates of NO 3 − leaching under future climate scenarios. The thickness of the unsaturated zone is crucial for reaching NO 3 − peaks at the groundwater table (Wang et al., 2012). Nitrate storage in the vadose zone is also important, but often not considered in