Abstract
The impacts of climate change-induced warming on our ecosystems can no longer be neglected, but our understanding of consequences for groundwater ecosystems in general and groundwater quality in particular is alarmingly incomplete. In this review, we therefore provide an overview of the current state of knowledge related to the impact of global warming on our precious groundwater resources. Groundwater warming in shallow aquifers is closely associated with increasing average land surface temperatures and has already reached + 1 K compared to pe-industrial times. Until the end of the twenty-first century, temperature increases in local groundwater of up to + 10 K are possible. Monitoring data, laboratory and field experiments all provide evidence that such temperature increases are sufficient to substantially modify groundwater quality through numerous and interlinked biogeochemical processes, which we have summarized in a conceptual overview. Warming impacts on groundwater are highly site-specific and spatially heterogeneous, which complicates their assessment and prediction. Locally, shallow unconfined and nutrient-rich floodplain aquifers are most susceptible to warming-induced changes. Importantly, processes affecting water quality are not only modified by a long-term rise in groundwater temperatures, but also in the short-term during weather extremes, which is of great relevance for riverbank filtration. At the regional scale, aquifers in cold regions impacted by permafrost thawing are especially vulnerable to warming. As the majority of temperature-sensitive processes affecting groundwater quality are not or only very slowly reversable, we pressingly require comprehensive mechanistic understanding before it is too late to develop suitable countermeasures and management strategies.
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Introduction: the impact of temperature on groundwater quality
Evidence for the consequences of climate change-induced warming on our environment is growing by the day (Ripple et al. 2022), but the resulting impacts on groundwater are still largely unknown (Riedel 2019). The majority of studies and review papers published until now focused on the quantitative impact of climate change on this natural georesource (i.e. changes in groundwater recharge and its implications for management practices) (Costa et al. 2021; Green et al. 2011; Johnson et al. 2022; Kløve et al. 2014; Taylor et al. 2013). On the other hand, climate change-induced influences on physico-chemical and biochemical properties and underlying processes in aquifers have received little attention so far (Bloomfield and Jackson 2013; Green et al. 2011; Hemmerle and Bayer 2020). Without going into details, the sixth assessment report (AR6) of the Intergovernmental Panel on Climate Change (IPCC) states medium confidence that climate change is impacting groundwater quality negatively (Pörtner et al. 2022). As groundwater is the most important source of raw drinking water and for irrigation (Margat and Van der Gun 2013; UN 2022), potential negative impacts of global warming on its quality cannot be ignored.
By groundwater, all forms of subsurface water is included in the following, reaching from the saturated zone near the soil surface down to depths of hundreds of m in thick alluvial or karstic aquifer systems. Defining the term groundwater quality is more challenging, as two only partially overlapping points of views shall be considered here. From the anthropogenic perspective, using groundwater as drinking water and for irrigation, it is primarily a question of the absence of substances hazardous to health (such as heavy metals, organic pollutants or pathogenic germs). Considering drinking water production, other physico-chemical properties are also important, such as pH, salinity and the concentration of dissolved organic carbon (DOC), reduced Fe2+ and Mn2+ that can interfere with raw water treatment and therefore impact on production costs. From an ecological point of view, aquifer systems represent complex ecosystems and habitats for diverse communities of organisms, which are vulnerable to hazardous compounds as well. Moreover, most inhabitants of aquifer ecosystems (i.e. stygobionta) react highly sensitive to changes in physico-chemical parameters such as temperature, dissolved oxygen (DO) concentration or redox conditions (Goldscheider et al. 2006; Hahn 2006; Humphreys 2009).
While the demands of human use on groundwater quality are very clear and legally regulated, the ecological perspective of groundwater systems is often neglected (Griebler et al. 2014). This is even more concerning in regard to the upcoming effects of climate change on groundwater systems, which is likely to affect a number of essential ecosystem services, comprising provision and production of safe drinking water, degradation of pollutants, retention of nutrients or elimination of pathogenic microorganisms (Goldscheider et al. 2006; Griebler et al. 2019).
Impacts of climate change on groundwater quality are already observable in aquifers. The impact of temperature change on abiotic reactions (i.e. individual mineral solubilities, sorption equilibria, reaction kinetics) was largely assessed through laboratory experiments (Jesußek et al. 2013; Partey et al. 2008; Welch and Ullman 2000). However, our understanding of how biogeochemical cycles and processes in aquifers are altered by warming is incomplete (Green et al. 2011). Studies investigating climate change-induced feedbacks on groundwater quality can be generally categorized based on the impact pathway: (1) increasing water temperatures, (2) changing groundwater tables (increases and decreases) and (3) sea water intrusion in the case of coastal aquifers. Whereas (2) and (3) are rather locally constrained, warming of groundwater (1) represents a global phenomenon.
To discuss how warming may affect groundwater quality, it is first important to know how much groundwater temperatures have risen so far and could continue to rise. Published groundwater temperature data from long-term monitoring programs is yet scarce, but several studies consistently described increases in groundwater temperatures along with increasing mean air and land surface temperatures (Kurylyk et al. 2013; Menberg et al. 2014). Groundwater temperatures are being modified by climate change either due to an increase in the temperature of recharge water (Burns et al. 2017) and/or from thermodynamic coupling between the atmosphere and the ground (Hemmerle and Bayer 2020). A detailed overview of documented increases in groundwater temperatures is provided in the following section.
The overarching aim of this review is to summarize the present knowledge on climate change-induced warming on groundwater temperatures and quality. We have therefore applied a systematic literature review by conducting a rigorous literature research based on Clarivate’s™ Web of Science core collection. We used case studies to synthesize the current state of knowledge, which we complement by own reflections wherever appropriate. This work distinguishes itself from previous reviews, which generelly focused on the entire impact of climate change on groundwater systems and considered quality related impacts only briefly, if at all (Amanambu et al. 2020; Earman and Dettinger 2011; Green et al. 2011; Kløve et al. 2014).
The following three main sections are each attributed to a specific research question: How much have groundwater temperatures increased so far and what can we expect for the near future (Sect. 2)? How does climate change-induced warming modify groundwater quality, and which biogeochemical processes are responsible (Sect. 3)? Which aquifers are most vulnerable to groundwater warming and resulting consequences for water quality (Sect. 4)?
Impact of climate change on groundwater temperatures
Current state of groundwater warming
In general, groundwater temperatures are closely linked to land surface temperatures (Menberg et al. 2014; Taylor and Stefan 2009). For shallow groundwater down to a depth of 60 m below ground level, a near-linear relationship between both has been reported for a global data set with groundwater temperatures ranging from 1 to 31 °C (Benz et al. 2017). Considering the close relationship between land surface and groundwater temperatures, it is not surprising that the impact of global warming is already visible in groundwater temperatures. For example, the regional mean annual air temperature in Bavaria (southern Germany) has increased by + 0.035 K a−1 between the early 1990s to 2015, which was closely followed by temperatures in shallow groundwater with an increase of + 0.028 K a−1 at 20 m and + 0.009 K a−1 at 60 m depth, respectively (Hemmerle and Bayer 2020). Similarly, surface air temperatures in Austria have increased on average by + 0.025 K a−1 from 1994 to 2013, while groundwater temperatures rose by + 0.035 K a−1 (Benz et al. 2018b). Annual warming of groundwater and aquifers in range of + 0.01 to + 0.04 K a−1 since the late 1970s has further been described for the UK (Bloomfield and Jackson 2013; Stuart et al. 2010), the Netherlands (Bense and Kurylyk 2017), Switzerland (Figura et al. 2011) and Germany (Menberg et al. 2014; Riedel 2019). Note that several studies reported accelerating groundwater warming rates since the 1990s (Figura et al. 2011; Menberg et al. 2014), which was especially pronounced in shallow groundwater bodies. Looking at the last three decades, the warming for shallow groundwater totals almost + 1 K, which corresponds to the general regional warming effects.
Thermal signals from changing regional air temperatures arrive damped and delayed in the subsurface (Hemmerle and Bayer 2020; Menberg et al. 2014), which emphasizes vertical aspects of groundwater warming. The faster the groundwater recharge, the faster warming progresses into the subsurface, which is especially pronounced for small, shallow unconfined aquifers as compared to usually larger, deep confined aquifers (Kløve et al. 2014).
It should not go unmentioned that anthropogenic activities may cause additional groundwater warming. In densely populated areas, subsurface energy fluxes are modified through buildings and infrastructure, which amounts to the so-called urban heat island effect (Benz et al. 2018a; Perrier et al. 2005; Taniguchi et al. 2007). Groundwater temperatures can be also affected by managed aquifer recharge (MAR), in which treated waste water or excess water is introduced into receiving aquifers (Dillon et al. 2019). Through aquifer thermal energy storage (ATES), thermal energy is seasonally stored and recovered from aquifers for heating purposes (Dillon et al. 2019; Doughty et al. 1982). More recently, open- or closed-loop ground source heat pump (GSHP) systems (including groundwater heat pump systems, GWHP) are installed for heating and/or cooling purposes, which have lasting effects on shallow groundwater temperatures (Lee and Hahn 2006; Russo et al. 2012). Another important anthropogenic activity affecting groundwater temperatures is riverbank filtration (RBF), which is commonly used in drinking water production. Here, the recharge of near-surface and unconfined floodplain aquifers from river water is forced through targeted pumping in extraction wells (Eckert et al. 2008; Ray et al. 2002; Schubert 2002). While all anthropogenic effects causing groundwater heating overlap with indirect warming through climate change, comparisons with groundwater temperatures in rural and less anthropogenically disturbed areas allow to distinguish between the different warming effects (Taniguchi et al. 2007; Taylor and Stefan 2009).
In summary, global warming is increasing groundwater temperatures, which is already detectable in monitoring data (for an overview of literature documenting groundwater warming, refer to Table 1). Note that the presented studies have a strong spatial focus on regions in Europe, whereas other regions remain largely understudied. However, considering the global increases in surface and air temperatures, it is safe to assume that many shallow porous and fast-recharging fissure aquifers have already suffered increases in groundwater temperatures of + 1 K as compared to pe-industrial times. Larger temperature increases at a local to regional scale are further likely considering the spatially uneven distribution of global warming (Hansen and Sato 2016; Pörtner et al. 2022).
Future trends and regional differences
To tackle the potential impact of warming on groundwater for the near future, it is of great importance to provide robust estimates of water temperature increases at a regional to local scale. Unfortunately, only few modeling-based predictions for groundwater temperatures are currently available. For a shallow aquifer in Minnesota (US), outcomes of a heat transport model suggested an increase in groundwater temperature of + 3 to + 4 K within the next decades (Taylor and Stefan 2009). This estimated range of groundwater warming agrees well with other local and regional modeling studies. For example, based on General Circulation Models (GCM) and different greenhouse gas emission scenarios (Representative Concentration Pathway, RCP), Gunawardhana and Kazama (2012) estimated that aquifer temperatures at 8 m depth in the humid subtropical climate of the Sendai Plain (Japan) will increase by + 1.00 to + 4.28 K until 2080 as compared to 2007 observations. For northern European cold-water springs in Finland and Sweden, a mean water temperature increase of + 0.7 (RCP2.6 scenario) to + 5.9 K (RCP8.5 scenario) was predicted by 2086 (Jyväsjärvi et al. 2015). This is in line with modeling-based estimate of a + 3 K increase for temperature of discharged shallow groundwater in temperate forests of Canada (Kurylyk et al. 2014).
Considering regional model predictions for surface temperatures (see IPCC Interactive Atlas; Masson-Delmotte et al. 2021), greatest warming is expected for the Arctic and midlatitudes in the northern hemisphere (Cogswell and Heiss 2021). Here, the predicted median of mean temperature change in the Russian Arctic Region for the 2081–2100 period (relative to 1850–1900, based on CMIP6 and a pessimistic global warming level of 4°C under SSP5-8.5) is an impressive + 9.6 K. Based on previous observations that show a tight correlation between land surface and groundwater temperatures (Benz et al. 2017), it is reasonable to assume that warming of shallow groundwater in northern regions may reach values close to + 10 K.
Consequences of warming for groundwater quality
Microbial activity, community structure and metabolic pathways
The intensification of microbial metabolic rates represents one of the most important consequences of rising temperatures in groundwater for most aquifers (Brielmann et al. 2011). For example, a higher microbiological activity as indicated by increasing microbial colony counts was reported from an ATES field site at the Netherlands, where 16 °C warm water was seasonally introduced into the aquifer (Bonte et al. 2011). However, linking increasing microbial activities to warming in aquifer systems is extremely difficult because of analytical limitations. Therefore, indirect proxies for microbial activities in groundwater are commonly monitored, such as DOC and NH4+ that are released as by-products during the microbial mineralization of organic matter (OM) (Brons et al. 1991; Du et al. 2020; Rivett et al. 2008).
In order to alter groundwater properties in the long-term under rising temperatures, microbial activities require sufficient supplies with key nutrients, terminal electron acceptors (TEA) and degradable OM (Brielmann et al. 2011; Griebler 2015; Griebler et al. 2016). Degradable OM comprises DOC (e.g. from sewage contamination) or sedimentary OM that is contained within the aquifer matrix. However, the response of microbial activities to warming is complex and non-linear, especially due to the involvement of a vast variety of microorganisms and aquifer properties that may considerably vary at a small scale (Griebler 2015). Generally, eutrophic aquifers are especially vulnerable to warming-induced changes through an intensification of microbial activities as high amounts of degradable OM and nutrients are available (Griebler et al. 2016).
The intensification of microbial activities may also result in the consumption and depletion of DO, causing a shift from oxic to anoxic conditions. A shift to anoxic conditions has several further important consequences for groundwater ecosystems. A gradual or temporary depletion in DO leads to a decline in the local redox potential, a change in the microbial community structure and also shifts in the dominant metabolic pathways as described in the following. Generally, the consumption of DO succeeds with the reduction of dissolved NO3− (Borch et al. 2010). For example, a depletion in DO during summer at a RBF site in Germany (Flehe Waterworks at the River Rhine, Düsseldorf) showed that microbial communities shifted from aerobic respiration toward anoxic denitrification (Sharma et al. 2012). Increasing groundwater temperatures further enhance microbial NO3− reduction rates if conditions are already anoxic (Cogswell and Heiss 2021). At the same time, NH4+ is released as by-product, which accumulates in groundwater near-proportionally to the decline in NO3− (Cogswell and Heiss 2021). Predominating redox processes may also shift due to different temperature optima of the microbial redox processes involved (Bonte et al. 2013a). For example, microcosm incubations of original groundwater and aquifer material from two ATES sites in the Netherlands showed that an increase in water temperature from 11 °C (natural background) to 25 °C caused a shift from Fe(III)- to SO4-reduction and methanogenesis (Bonte et al. 2013a). Similar observations were made by Jesußek et al. (2013), who incubated Tertiary lignite sand from an aquifer in northern Germany. As a response to warming, redox conditions shifted from NO3−- (10 °C) to NO3−- and Fe(III)-reduction (at 25 and 40 °C).
Increasing groundwater temperatures also cause shifts within the microbial community structure. This was shown for example for an aquifer impacted by a closed-loop GSHP system in New Jersey (USA) (Sowers et al. 2006). Although limited to culturable bacteria, the outcomes from two sampling campaigns (1997 and 2005) suggested pronounced changes in the microbial community structure. Warming-induced shifts in microbial communities and dominant metabolic pathways were further observed for two Quaternary alluvial aquifers in southern Germany (Munich and Freising), representing eutrophic and oligotrophic aquifer systems, respectively (Brielmann et al. 2009, 2011; Griebler et al. 2016). Here, warming resulted in complex changes within the aquifers, comprising the chemical composition (e.g., depletion in DO), the microbial biodiversity and community composition as well as metabolic processes and finally ecosystem functions. Specifically, the diversity of aquifer microbial communities increased with warmer temperatures and the microbial community structure changed. Whereas natural ground water temperatures of 10–12 °C provided ideal living conditions for psychrophile und psychrotolerant microorganisms, warming to 15—20 °C fostered the prevalence of mesophile species. Importantly, microbial biomass and activities were found to additionally depend on the availability of nutrients and substrates (e.g., OM, P). When groundwater temperatures exceeded 20 °C, P limitation occurred due to an increase in metabolic activities and an associated demand in essential nutrients. Thus, not only the relative changes in groundwater temperatures are important in regard to the water quality, but also absolute temperatures that are reached.
Impact on water quality
One major change in groundwater properties arising from an increase in microbial metabolic activity is the shift from oxic to anoxic conditions (Stumm and Sulzberger 1992). In addition to the consumption of DO by microorganisms, warming of groundwater also reduces the solubility of oxygen in infiltrating water. A gradually decreasing O2 saturation (on average − 0.24% a−1) parallel to rising groundwater temperatures (+ 0.012 K a−1) was observed by Riedel (2019) for groundwater in southern Germany. Furthermore, a temporary DO depletion in groundwater was reported for shallow floodplain aquifers used for RBF. For example, an exceptionally hot and dry summer in 2003 caused a temporary temperature increase close to 20 °C in groundwater of the Lower Rhine Valley (Germany), which was accompanied by an approximately four months long decline in DO concentrations to below 1 mg L−1 (Eckert et al. 2008). Similar observations were made in 2003 for the River Thur (Switzerland), where an increase in microbial activity resulted in DO depletion in groundwater near the river (Hoehn and Scholtis 2011). The impact of rising groundwater temperatures on DO during summer months was further observed in shallow groundwater below stormwater infiltration basins (Datry et al. 2004; Foulquier et al. 2009). Thus, temperature-induced changes in surface waters that precede groundwater recharge can further enhance DO depletion in shallow unconfined aquifers, which is particularly important during the summer months.
Note that groundwater warming and an associated shift from oxic to anoxic conditions is highly problematic for groundwater invertebrates. Field observations and controlled experiments showed that species-dependent threshold values exist regarding groundwater temperatures and DO concentrations (Brielmann et al. 2011; Foulquier et al. 2011; Griebler 2015). For example, no invertebrates were found in shallow groundwater of a stormwater infiltration site when the DO declined to below 0.5 mg L−1 (Foulquier et al. 2011).
The enhanced microbial mineralization of OM is accompanied by the release of CO2 as a byproduct, which raises in turn the CO2 partial pressure (pCO2) and causes a subsequent decline in pH (Hoehn and Scholtis 2011). This was observable in southern Germany, where rising groundwater temperatures (on average, + 0.012 K a−1) were found to be negatively correlated with pH values (-0.003 a−1) (Riedel 2019). This observation was further in line with the outcomes of laboratory incubation experiments, which used original aquifer material from an ATES site (Brons et al. 1991). Here, controlled temperature increases resulted in CO2 production from the microbial mineralization of OM, which finally caused a decrease in pH.
A decreasing pH results in turn in the dissolution of calcite and the release of dissolved Ca2+ into groundwater (McDonough et al. 2020). Furthermore, pH-controlled silicate dissolution and an associated release of Si and K+ has been observed in field (Saito et al. 2016) as well as laboratory warming experiments (Arning et al. 2006; Bonte et al. 2013b). Enhanced mineral weathering resulting from a decreasing pH has also been attributed an increase in geogenic contaminants such as F− (Riedel 2019), which can ultimately lead to a deterioration in groundwater quality.
Microbial mineralization of OM may also cause a depletion of TEA and subsequently a decrease in the redox potential. A change in the redox potential toward more reducing conditions is further modifying the mobility of toxic trace elements. Here, Mn2+ is of particular importance as chronic overexposure was found to be associated with neurotoxic health effects in humans (O’Neal and Zheng 2015) as well as negative effects in aquatic organisms (Peters et al. 2011). The removal of Mn2+ during water treatment requires additional efforts and therefore costs (Tobiason et al. 2016). Reduced Mn2+ is easily released into groundwater due to microbial redox reactions as soon as anoxic conditions are reached, which is often associated with shallow aquifers that are prone to warming impacts (Riedel 2019).
Warming-induced Mn2+ releases into groundwater have been well-documented at RBF sites, where the raw water composition is closely monitored. For example, substantial increases in dissolved Mn2+ concentrations from below 0.1 to above 0.6 mg L−1 were observable during the 2015 summer at the Waterworks Dresden-Tolkewitz (East Germany), when river-water temperatures rose to over 20 °C for three months (Paufler et al. 2018). (Paufler et al. 2018). Moreover, Mn2+ concentrations were found to be constrained by sorption as well as (re-)oxidation and precipitation of Mn-oxides along the groundwater flow path due to changing hydrogeochemical conditions. Similarly, Mn2+ concentrations in groundwater at the Lot River (France) were found to be positively correlated to the water temperature (Bourg and Bertin 1994). Here, a threshold groundwater temperature of 10 °C was reported that triggered microbial Mn(IV)-reduction.
Due to the pollution of the river Rhine with degradable dissolved organic substances in the 1970s, connected floodplain aquifers also became extensively anoxic, leading in turn to considerable increases in dissolved Mn2+ as observed from 1968 on at Düsseldorf (Germany) (Kübeck et al. 2009). As the water quality of the Rhine improved, Mn2+ concentrations in shallow groundwater decreased sharply from 1988. Thus, changes in the river water composition can be also relevant regarding the quality of associated groundwater bodies in addition to increasing temperatures (Sprenger et al. 2011). On the other hand, the river water composition, especially DO concentrations, are increasingly impacted by warming (Ducharne 2008; Whitehead et al. 2009), which will in turn impact redox conditions in shallow floodplain aquifers.
Local shifts toward anoxic conditions during summer months reaching Mn(IV)- and even Fe(III)-reducing conditions were reported from stormwater infiltration basins (Fischer et al. 2003; Massmann et al. 2006). The reductive dissolution of Mn(IV)- and Fe(III)-(hydr)oxides may also release other problematic geogenic trace elements such as As or P, which are either sorbed to the mineral surfaces or are incorporated as impurities within the crystal lattices (Borch et al. 2010; Neidhardt et al. 2021).
Furthermore, warming-induced releases of trace elements into groundwater have been observed in several field and laboratory experiments, comprising a wide range of temperatures and elements such as B, Li, As, Mo, V, P, Sb, Ba, Co, Tl, Mn, and U (Bonte et al. 2013a, b, 2011; Lüders et al. 2020; Saito et al. 2016). While the reductive dissolution of Mn(IV)- and Fe(III)-(hydr)oxides was generally considered as principal mobilization mechanism for these elements, several authors argued that temperature-dependent cation exchange as well as anion desorption may have also been involved (Bonte et al. 2013b; Lüders et al. 2020; Saito et al. 2016). The latter is of relevance for all elements that form oxyanions, comprising As, V, Mo and P. Knowledge of the release mechanisms involved is important because some (i.e. the release of cations and anions through adsorption reactions) are reversible if groundwater temperatures should decline (Lüders et al. 2020).
Warming may also provide ideal conditions for the degradation of organic pollutants (Cavelan et al. 2022; Popp et al. 2015). For example, the outcomes of a microcosm experiment using contaminated soil and aquifer material showed that warming did not only result in a shift in the composition and activity of microbial communities, but also in an increased degradation of aromatic hydrocarbons (Zeman et al. 2014).
In addition to the previously mentioned impacts of warming on abiotic processes (e.g., ion exchange, desorption, and solubility of minerals and gases, see Table 2), rising water temperatures also influence various hydrogeological properties like water density and viscosity. While these properties influence groundwater flow velocity and contaminant transport, it can be assumed that their combined effects on groundwater quality are only minor compared to the direct impact of biogeochemical processes.
A summary of groundwater warming and its impacts on biogeochemical processes and water quality in aquifers is provided in Fig. 1 and Table 2. For a detailed overview of publications reporting on impacts of warming on groundwater the reader is referred to Table 3. The studies presented cover a wider range of methodological approaches and are based on groundwater monitoring data from regular aquifers, systems particularly influenced by warming effects (RBF, ATES and MAR sites) and temperature manipulation experiments in the field and in the laboratory. Note that the studies presented all share a pronounced spatial focus on regions in Europe and northern America. However, the consequences of warming on biogeochemical reactions and microbial communities can largely be applied to aquifers in general.
Aquifers affected by groundwater warming
Changing groundwater temperatures at a regional scale
Current and future temperature changes and associated consequences for aquifers are highly variable for different climatic regions. In the vast cold regions of the Arctic and Antarctic tundra as well as in parts of the boreal coniferous forests, increases in surface temperatures already clearly exceed the global average (Anisimov and Nelson 1996; Pörtner et al. 2022; Romanovsky et al. 2019). In the Russian Arctic, Alaska and Arctic Canada, average ground temperatures rose during the last three to four decades with a rate of 0.1–1.4 K decade−1 (Biskaborn et al. 2019; Pörtner et al. 2022; Romanovsky et al. 2019). This regional pattern will further accelerate during the next decades according to modeling predictions. For example, under the business as usual scenario (RCP8.5), GCM projections predict most pronounced temperatures increases in the 2090s for countries with boreal forests (i.e. Canada with 5.44 °C followed by Finland 5.37 °C (Lee et al. 2019)). Due to the close relationship of land surface and groundwater temperatures (Benz et al. 2017), similar regional warming patterns can be expected for shallow groundwater.
Groundwater warming in temperate regions has been documented by some few previously mentioned studies (Hemmerle and Bayer 2020; Riedel 2019). So far, observed temperature increases in shallow groundwater closely followed the average global land surface warming. It is therefore reasonable to expect similar warming patterns for temperate aquifers in the near future. However, temperatures in Europe have increased more than twice the global average during the 1991–2021 period (WMO 2022). Therefore, many temperate aquifers are also likely to be affected by warming above the global average.
In dry regions, the impact of climate change-induced warming on groundwater temperatures should be less and also slower due to a generally lower and more episodic recharge as compared to temperate regions (Opie et al. 2020). However, these considerations only apply to anthropogenically undisturbed catchments. The impact of irrigation on temperatures of shallow groundwater can be severe in dry regions, which artificially increases recharge during summer with warm water (Riedel 2019).
For tropic regions, information on groundwater warming is scarce. Available data mainly originates from densely populated urban areas, showing an additional warming due to anthropogenic heat fluxes (heat island effects, see Taniguchi et al. 2007).
In sum, current and future groundwater warming at a regional scale may largely exceed global average warming, especially in regions of high latitudes, dry regions under irrigation as well as densely populated areas. However, there is a considerable lack of case studies to estimate warming impacts as well associated consequences for groundwater quality at regional scales.
Aquifers vulnerable to warming-induced changes in groundwater quality
The impacts of warming on groundwater resources may vary spatially, in both vertical (local scale) and horizontal (regional scale) extent. At the local scale, shallow and unconfined aquifer systems and fractured rock aquifers respond faster to groundwater warming as deeper and confined aquifers (Cavelan et al. 2022; Hemmerle and Bayer 2020). In addition, from a microbial point of view, organic-rich aquifers are especially sensitive to temperature changes, comprising anthropogenically contaminated urban or agricultural areas as well as natural alluvial floodplains. Here, a temperature increase of only a few K can already lead to an increased turnover of OM and related DO depletion, which strongly affects the local groundwater fauna (Griebler 2015).
At the regional scale, groundwater systems in continental northern latitudes or alpine regions (e.g. Canada, Scandinavia, Russia) are especially sensitive to warming, where aquifers are heavily impacted by thawing permafrost (Haldorsen et al. 2012). Assuming a + 2 K global warming under the RCP8.5 scenario, about one-third of the permafrost will disappear during the next decades (Kong and Wang 2017; Wang et al. 2019), which fundamentally alters the local hydrology by modifying for example recharge and groundwater tables (Haldorsen et al. 2012; Walvoord and Kurylyk 2016; Walvoord and Striegl 2007). Consequently, entire aquifer systems are being (re-)activated (Bense et al. 2009), facilitating microbial activities and associated biogeochemical redox processes (Cochand et al. 2019; Pi et al. 2021). For example, the microbial mineralization of the often considerable OM stocks results in a rapid depletion in DO triggering in turn anoxic biogeochemical reactions, which release nutrients (P) and toxic trace elements into the groundwater (Bonte et al. 2013b; Pi et al. 2021). Permafrost thawing and (re-)activation of dormant groundwater systems may also feedback on surface waters, increasing for example the export of DOC and DON (dissolved organic nitrogen) into rivers (Walvoord and Striegl 2007). Despite the pronounced consequences of permafrost thawing for groundwater quality, only few field studies provided detailed insights into the underlying processes and spatial extent so far (Cochand et al. 2019).
Aquifers in temperate and humid regions may also react fast to changing land surface temperatures as observed for several aquifers in Europe (Bense and Kurylyk 2017; Bloomfield and Jackson 2013; Hemmerle and Bayer 2020). Here, temperature thresholds can be locally reached that lead to a shift in microbial communities and associated redox processes (Griebler et al. 2016). However, further field-based verification is required to assess the spatial extent of the aquifers affected.
A schematic overview of the estimated vulnerability of aquifers to warming within different climatic regions is provided in Fig. 2. Here, the aspect “cold” comprises regions at high altitudes as well as high latitudes, whereas “dry” includes regions with an aridity index of < 0.65 (Middleton and Thomas 1997). “Shallow” and “deep” refer to the depth below ground (< 60 and > 60 m, respectively). “Unconfined” conditions usually apply to shallow and porous floodplain aquifers or fractured aquifer systems, whereas “confined” aquifers are often found in floodplains and river deltas, where clayey and loamy deposits form confining layers. The properties “eutrophic” (i.e. nutrient-rich) and “oligotrophic” (nutrient-poor) are related to groundwater quality. For example, shallow oligotrophic aquifers are sensitive to increasing water temperatures, but warming has only little impact on the water quality as microbial activities are limited by a low nutrient availability. Eutrophic but confined aquifers are only minor susceptible to warming and warming-induced quality changes due to slow recharge.
In sum, aquifers can be considered vulnerable either due to (i) pronounced absolute increases in groundwater temperatures (e.g. organic-rich unconfined shallow alluvial aquifers), or (ii) significant changes that arise even from small temperature increases (as for example in permafrost regions).
Conclusion
The effects of climate change-induced warming on groundwater temperature (Sect. 2) and groundwater quality (Sect. 3) are already visible in groundwater monitoring data sets. So far, groundwater temperatures have risen by up to + 1 K compared to pre-industrial times and will likely rise up to + 10 K on a local to regional scale by the end of the twenty-first century.
Changes in groundwater quality due to rising temperatures are driven by a number of closely interrelated, temperature-sensitive biogeochemical processes, with microbial activity playing a central role. From the perspective of water work operators, resulting changes in groundwater quality are not (yet) problematic, but the transition from oxic to anoxic conditions marks a critical threshold for all groundwater organisms that depend on the availability of oxygen.
There is also a pronounced temporal aspect to warming-related impacts on groundwater. In addition to gradual long-term warming trends, short-term impacts on shallow alluvial aquifers become increasingly important as the frequency of weather extremes and especially dry spells increases globally. The resulting short-term impacts are especially relevant regarding the operation of RBS systems as well as MAR sites.
Importantly, not all groundwater bodies are equally vulnerable to warming and resulting quality changes (Sect. 4). Deep, confined and/or nutrient-poor aquifers are far more robust to warming and associated water quality deteriorations as compared to shallow, unconfined and nutrient-rich groundwater bodies. In addition, some regions are more vulnerable to groundwater warming than others. For example, large areas in the northern latitudes are currently affected by the thawing of permafrost, which has a strong impact on the groundwater systems there. Warming-induced impacts on groundwater quality may also overlap with other environmental changes such as water table fluctuations (induced by changing recharges, pumping activities or land use changes) or sea-water intrusion.
Knowledge gaps and future challenges
The importance of understanding and predicting ongoing changes in groundwater systems cannot be overstated. However, there is a pronounced lack of studies that evaluate long-term monitoring data sets in terms of warming-induced impacts. The scarce amount of published studies contrasts with the meticulously collection of data over often decades by many authorities, waterworks or environmental protection agencies. To identify and tackle upcoming changes in groundwater quality, we require solid baseline data. Furthermore, the studies published so far had a strong regional focus on Europe and northern America. Thus, there is a systematic lack of information on main aquifer types in different climatic regions. Finally, we generally lack knowledge regarding the impact of warming on microbial communities and the complex biogeochemical interactions they maintain in groundwater ecosystems.
To tackle these knowledge gaps, we suggest:
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1.
Consequent evaluation of long-term monitoring data sets, ideally following the principles of open data.
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Installation and operation of international monitoring sites, especially in remote areas.
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Combination of remote sensing products with groundwater monitoring data and spatial modeling approaches.
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4.
Truly interdisciplinary research approaches that cover basic physico-chemical properties of groundwater as well as microbiological parameters.
Since most of the temperature-dependent processes affecting groundwater quality are not or only very slowly reversable, we urgently need comprehensive knowledge about the changes currently taking place before it is too late to develop appropriate countermeasures and management strategies.
Data availability
All necessary data are presented in the document.
Abbreviations
- a− 1 :
-
Per year
- ATES:
-
Aquifer thermal energy storage
- °C:
-
Degree celsius
- CMIP6:
-
Coupled Model Intercomparison Project Phase 6
- DO:
-
Dissolved oxygen
- DOC:
-
Dissolved organic carbon
- DON:
-
Dissolved organic nitrogen
- E h :
-
Redox potential
- GCM:
-
General Circulation Models
- GSHP:
-
Ground source heat pump
- GWHP:
-
Groundwater heat pump
- IPCC:
-
Intergovernmental Panel on Climate Change
- LNAPL:
-
Light non-aqueous phase liquids
- LST:
-
Land surface temperature
- MAR:
-
Managed artificial recharge
- MAT:
-
Mean annual air temperature
- OM:
-
Organic matter
- pCO2 :
-
CO2 partial pressure
- RBF:
-
Riverbank filtration
- RCP:
-
Representative Concentration Pathway
- SSP:
-
Shared Socioeconomic Pathways Scenario
- TCE:
-
Trichloroethene
References
Amanambu AC, Obarein OA, Mossa J, Li L, Ayeni SS, Balogun O, Oyebamiji A, Ochege FU (2020) Groundwater system and climate change: present status and future considerations. J Hydrol 589:125163
Anisimov OA, Nelson FE (1996) Permafrost distribution in the Northern Hemisphere under scenarios of climatic change. Global Planet Change 14:59–72
Arning E, Kölling M, Schulz H, Panteleit B, Reichling J (2006) Einfluss oberflächennaher Wärmegewinnung auf geochemische Prozesse im Grundwasserleiter. Grundwasser 11:27–39
Bense VF, Kurylyk BL (2017) Tracking the subsurface signal of decadal climate warming to quantify vertical groundwater flow rates. Geophys Res Lett 44:12,244-212,253
Bense V, Ferguson G, Kooi H (2009) Evolution of shallow groundwater flow systems in areas of degrading permafrost. Geophys Res Lett 36:L22401
Benz SA, Bayer P, Blum P (2017) Global patterns of shallow groundwater temperatures. Environ Res Lett 12:034005
Benz SA, Bayer P, Blum P, Hamamoto H, Arimoto H, Taniguchi M (2018a) Comparing anthropogenic heat input and heat accumulation in the subsurface of Osaka, Japan. Sci Total Environ 643:1127–1136
Benz SA, Bayer P, Winkler G, Blum P (2018b) Recent trends of groundwater temperatures in Austria. Hydrol Earth Syst Sc 22:3143–3154
Biskaborn BK, Smith SL, Noetzli J, Matthes H, Vieira G, Streletskiy DA, Schoeneich P, Romanovsky VE, Lewkowicz AG, Abramov A (2019) Permafrost is warming at a global scale. Nat Commun 10:1–11
Bloomfield JP, Jackson CR, Stuart ME (2013) Changes in groundwater levels, temperature and quality in the UK over the 20th century: an assessment of evidence of impacts from climate change. https://nora.nerc.ac.uk/id/eprint/503271/1/1%20Groundwater%20levels%2C%20temperature%20and%20quality.pdf
Bonte M, Stuyfzand P, Van den Berg G, Hijnen W (2011) Effects of aquifer thermal energy storage on groundwater quality and the consequences for drinking water production: a case study from the Netherlands. Water Sci Technol 63:1922–1931
Bonte M, Röling WF, Zaura E, van der Wielen PW, Stuyfzand PJ, van Breukelen BM (2013a) Impacts of shallow geothermal energy production on redox processes and microbial communities. Environ Sci Technol 47:14476–14484
Bonte M, van Breukelen BM, Stuyfzand PJ (2013b) Temperature-induced impacts on groundwater quality and arsenic mobility in anoxic aquifer sediments used for both drinking water and shallow geothermal energy production. Water Res 47:5088–5100
Borch T, Kretzschmar R, Kappler A, Cappellen PV, Ginder-Vogel M, Voegelin A, Campbell K (2010) Biogeochemical redox processes and their impact on contaminant dynamics. Environ Sci Technol 44:15–23
Bourg AC, Bertin C (1994) Seasonal and spatial trends in manganese solubility in an alluvial aquifer. Environ Sci Technol 28:868–876
Brielmann H, Griebler C, Schmidt SI, Michel R, Lueders T (2009) Effects of thermal energy discharge on shallow groundwater ecosystems. FEMS Microbiol Ecol 68:273–286
Brielmann H, Lueders T, Schreglmann K, Ferraro F, Avramov M, Hammerl V, Blum P, Bayer P, Griebler C (2011) Shallow geothermal energy usage and its potential impacts on groundwater ecosystems. Grundwasser 16:77–91
Brons H, Griffioen J, Appelo C, Zehnder A (1991) (Bio) geochemical reactions in aquifer material from a thermal energy storage site. Water Res 25:729–736
Burns ER, Zhu Y, Zhan H, Manga M, Williams CF, Ingebritsen SE, Dunham JB (2017) Thermal effect of climate change on groundwater-fed ecosystems. Water Resour Res 53:3341–3351
Cavelan A, Golfier F, Colombano S, Davarzani H, Deparis J, Faure P (2022) A critical review of the influence of groundwater level fluctuations and temperature on LNAPL contaminations in the context of climate change. Sci Total Environ 806:150412
Cochand M, Molson J, Lemieux JM (2019) Groundwater hydrogeochemistry in permafrost regions. Permafr Periglac 30:90–103
Cogswell C, Heiss JW (2021) Climate and seasonal temperature controls on biogeochemical transformations in unconfined coastal aquifers. J Geophys Res Biogeosci 126:e2021JG006605
Costa D, Zhang H, Levison J (2021) Impacts of climate change on groundwater in the Great Lakes Basin: a review. J Great Lakes Res 47:1613–1625
Datry T, Malard F, Gibert J (2004) Dynamics of solutes and dissolved oxygen in shallow urban groundwater below a stormwater infiltration basin. Sci Total Environ 329:215–229
Dillon P, Stuyfzand P, Grischek T, Lluria M, Pyne R, Jain R, Bear J, Schwarz J, Wang W, Fernandez E (2019) Sixty years of global progress in managed aquifer recharge. Hydrogeol J 27:1–30
Doughty C, Hellström G, Tsang CF, Claesson J (1982) A dimensionless parameter approach to the thermal behavior of an aquifer thermal energy storage system. Water Resour Res 18:571–587
Du Y, Deng Y, Ma T, Xu Y, Tao Y, Huang Y, Liu R, Wang Y (2020) Enrichment of geogenic ammonium in quaternary alluvial-lacustrine aquifer systems: evidence from carbon isotopes and DOM characteristics. Environ Sci Technol 54:6104–6114
Ducharne A (2008) Importance of stream temperature to climate change impact on water quality. Hydrol Earth Syst Sci 12:797–810
Earman S, Dettinger M (2011) Potential impacts of climate change on groundwater resources—a global review. J Water Clim Change 2:213–229
Eckert P, Lamberts R, Wagner C (2008) The impact of climate change on drinking water supply by riverbank filtration. Water Sci Technol 8:319–324
Figura S, Livingstone DM, Hoehn E, Kipfer R (2011) Regime shift in groundwater temperature triggered by the Arctic Oscillation. Geophys Res Lett 38:L23401
Fischer D, Charles EG, Baehr AL (2003) Effects of stormwater infiltration on quality of groundwater beneath retention and detention basins. J Environ Eng 129:464–471
Foulquier A, Malard F, Barraud S, Gibert J (2009) Thermal influence of urban groundwater recharge from stormwater infiltration basins. Hydrol Process 23:1701–1713
Foulquier A, Malard F, Mermillod-Blondin F, Montuelle B, Dolédec S, Volat B, Gibert J (2011) Surface water linkages regulate trophic interactions in a groundwater food web. Ecosystems 14:1339–1353
Goldscheider N, Hunkeler D, Rossi P (2006) Review: microbial biocenoses in pristine aquifers and an assessment of investigative methods. Hydrogeol J 14:926–941
Green TR, Taniguchi M, Kooi H, Gurdak JJ, Allen DM, Hiscock KM, Treidel H, Aureli A (2011) Beneath the surface of global change: impacts of climate change on groundwater. J Hydrol 405:532–560
Griebler C, Malard F, Lefébure T (2014) Current developments in groundwater ecology—from biodiversity to ecosystem function and services. Curr Opin Biotechnol 27:159–167
Griebler C, Brielmann H, Haberer CM, Kaschuba S, Kellermann C, Stumpp C, Hegler F, Kuntz D, Walker-Hertkorn S, Lueders T (2016) Potential impacts of geothermal energy use and storage of heat on groundwater quality, biodiversity, and ecosystem processes. Environ Earth Sci 75:1–18
Griebler C, Avramov M, Hose G (2019) Groundwater ecosystems and their services: current status and potential risks. In: Schröter M, Bonn A, Klotz S, Seppelt R, Baessler C (eds) Atlas of ecosystem services: drivers, risks, and societal responses. Springer, Cham, pp 197–203
Griebler C (2015) Auswirkungen thermischer Veränderungen infolge der Nutzung oberflächennaher Geothermie auf die Beschaffenheit des Grundwassers und seiner Lebensgemeinschaften: Empfehlungen für eine umweltverträgliche Nutzung. Umweltbundesamt. https://www.umweltbundesamt.de/sites/default/files/medien/378/publikationen/texte_54_2015_auswirkungen_thermischer_veraenderungen_infolge_der_nutzung_obenflaechennaher_geothermie_0.pdf
Gunawardhana LN, Kazama S (2012) Statistical and numerical analyzes of the influence of climate variability on aquifer water levels and groundwater temperatures: The impacts of climate change on aquifer thermal regimes. Global Planet Change 86:66–78
Hahn HJ (2006) The GW-Fauna-Index: a first approach to a quantitative ecological assessment of groundwater habitats. Limnologica 36:119–137
Haldorsen S, Heim M, van der Ploeg M (2012) Impacts of climate change on groundwater in permafrost areas: case study from Svalbard, Norway. In: Treidel H, Martin-Bordes JL, Gurdak JJ (eds) Climate change effects on groundwater resources: a global synthesis of findings and recommendations. CRC Press, pp 323–340
Hansen J, Sato M (2016) Regional climate change and national responsibilities. Environ Res Lett 11:034009
Hemmerle H, Bayer P (2020) Climate change yields groundwater warming in Bavaria, Germany. Front Earth Sci 523
Hoehn E, Scholtis A (2011) Exchange between a river and groundwater, assessed with hydrochemical data. Hydrol Earth Syst Sci 15:983–988
Humphreys WF (2009) Hydrogeology and groundwater ecology: does each inform the other? Hydrogeol J 17:5–21
Jesußek A, Grandel S, Dahmke A (2013) Impacts of subsurface heat storage on aquifer hydrogeochemistry. Environ Earth Sci 69:1999–2012
Johnson T, Butcher J, Santell S, Schwartz S, Julius S, LeDuc S (2022) A review of climate change effects on practices for mitigating water quality impacts. J Water Clim Change 13:1684–1705
Jyväsjärvi J, Marttila H, Rossi PM, Ala-Aho P, Olofsson B, Nisell J, Backman B, Ilmonen J, Virtanen R, Paasivirta L (2015) Climate-induced warming imposes a threat to north European spring ecosystems. Global Change Biol 21:4561–4569
Kløve B, Ala-Aho P, Bertrand G, Gurdak JJ, Kupfersberger H, Kværner J, Muotka T, Mykrä H, Preda E, Rossi P (2014) Climate change impacts on groundwater and dependent ecosystems. J Hydrol 518:250–266
Kong Y, Wang C-H (2017) Responses and changes in the permafrost and snow water equivalent in the Northern Hemisphere under a scenario of 1.5 C warming. Adv Clim Change Res 8:235–244
Kübeck C, Hansen C, Bergmann A, Kamphausen S, König C, van Berk W (2009) Model based raw water quality management–manganese mobilization induced by bank filtration. Clean: Soil, Air, Water 37:945–954
Kurylyk BL, Bourque C-A, MacQuarrie KT (2013) Potential surface temperature and shallow groundwater temperature response to climate change: an example from a small forested catchment in east-central New Brunswick (Canada). Hydrol Earth Syst Sci 17:2701–2716
Kurylyk BL, MacQuarrie KT, Voss CI (2014) Climate change impacts on the temperature and magnitude of groundwater discharge from shallow, unconfined aquifers. Water Resour Res 50:3253–3274
Lee J-Y, Hahn J-S (2006) Characterization of groundwater temperature obtained from the Korean national groundwater monitoring stations: implications for heat pumps. J Hydrol 329:514–526
Lee JY, Kim H, Gasparrini A, Armstrong B, Bell ML, Sera F, Lavigne E, Abrutzky R, Tong S, Coelho MdSZS (2019) Predicted temperature-increase-induced global health burden and its regional variability. Environ Int 131:105027
Lüders K, Dahmke A, Fiedler M, Köber R (2020) Temperature influence on mobilization and (re) fixation of trace elements and heavy metals in column tests with aquifer sediments from 10 to 70° C. Water Res 169:115266
Margat J, Van der Gun J (2013) Groundwater around the world: a geographic synopsis. CRC Press, Boca Raton
Massmann G, Greskowiak J, Dünnbier U, Zuehlke S, Knappe A, Pekdeger A (2006) The impact of variable temperatures on the redox conditions and the behavior of pharmaceutical residues during artificial recharge. J Hydrol 328:141–156
Masson-Delmotte V, Zhai P, Pirani A, Connors SL, Péan C, Berger S, Caud N, Chen Y, Goldfarb L, Gomis M (2021) Climate change 2021: the physical science basis. Contribution of working group I to the sixth assessment report of the intergovernmental panel on climate change, 2
McDonough LK, Santos IR, Andersen MS, O’Carroll DM, Rutlidge H, Meredith K, Oudone P, Bridgeman J, Gooddy DC, Sorensen JP (2020) Changes in global groundwater organic carbon driven by climate change and urbanization. Nat Commun 11:1–10
Menberg K, Blum P, Kurylyk BL, Bayer P (2014) Observed groundwater temperature response to recent climate change. Hydrol Earth Syst Sci 18:4453–4466
Middleton N, Thomas D (1997) World atlas of desertification, 2nd edn. Hodder Headline, PLC, Arnold
Neidhardt H, Rudischer S, Eiche E, Schneider M, Stopelli E, Duyen VT, Trang PTK, Viet PH, Neumann T, Berg M (2021) Phosphate immobilization dynamics and interaction with arsenic sorption at redox transition zones in floodplain aquifers: insights from the Red River Delta, Vietnam. J Hazard Mater 411:125128
O’Neal SL, Zheng W (2015) Manganese toxicity upon overexposure: a decade in review. Curr Environ Health Rep 2:315–328
Opie S, Taylor RG, Brierley CM, Shamsudduha M, Cuthbert MO (2020) Climate–groundwater dynamics inferred from GRACE and the role of hydraulic memory. Earth Syst Dyn 11:775–791
Partey F, Norman D, Ndur S, Nartey R (2008) Arsenic sorption onto laterite iron concretions: temperature effect. J Colloid Interface Sci 321:493–500
Paufler S, Grischek T, Benso MR, Seidel N, Fischer T (2018) The impact of river discharge and water temperature on manganese release from the riverbed during riverbank filtration: a case study from Dresden, Germany. Water 10:1476
Perrier F, Le Mouël JL, Poirier JP, Shnirman M (2005) Long-term climate change and surface versus underground temperature measurements in Paris. Int J Climatol 25:1619–1631
Peters A, Lofts S, Merrington G, Brown B, Stubblefield W, Harlow K (2011) Development of biotic ligand models for chronic manganese toxicity to fish, invertebrates, and algae. Environ Toxicol Chem 30:2407–2415
Pi K, Bieroza M, Brouchkov A, Chen W, Dufour L, Gongalsky KB, Herrmann A, Krab E, Landesman C, Laverman AM (2021) The cold region critical zone in transition: responses to climate warming and land use change. Annu Rev Environ Resour 46:111–134
Popp S, Beyer C, Dahmke A, Bauer S (2015) Model development and numerical simulation of a seasonal heat storage in a contaminated shallow aquifer. Energy Procedia 76:361–370
Pörtner HO, Roberts DC, Adams H, Adler C, Aldunce P, Ali E, Begum RA, Betts R, Kerr RB, Biesbroek R (2022) Climate change 2022: impacts, adaptation and vulnerability. IPCC Sixth Assessment Report. https://www.ipcc.ch/report/ar6/wg2/
Ray C, Grischek T, Schubert J, Wang JZ, Speth TF (2002) A perspective of riverbank filtration. J Am Water Works Assoc 94:149–160
Riedel T (2019) Temperature-associated changes in groundwater quality. J Hydrol 572:206–212
Ripple WJ, Wolf C, Gregg JW, Levin K, Rockström J, Newsome TM, Betts MG, Huq S, Law BE, Kemp L, Kalmus P, Lenton TM (2022) World scientists’ warning of a climate emergency 2022. Bioscience 1149–1155
Rivett MO, Buss SR, Morgan P, Smith JWN, Bemment CD (2008) Nitrate attenuation in groundwater: A review of biogeochemical controlling processes. Water Res 42:4215–4232
Romanovsky V, Smith S, Isaksen K, Shiklomanov N, Streletskiy D, Kholodov A, Christiansen H, Drozdov D, Malkova G, Marchenko S (2019) Terrestrial permafrost [in “State of the Climate in 2018”]. Bull Am Meteorol Soc 100
Russo SL, Taddia G, Verda V (2012) Development of the thermally affected zone (TAZ) around a groundwater heat pump (GWHP) system: a sensitivity analysis. Geothermics 43:66–74
Saito T, Hamamoto S, Ueki T, Ohkubo S, Moldrup P, Kawamoto K, Komatsu T (2016) Temperature change affected groundwater quality in a confined marine aquifer during long-term heating and cooling. Water Res 94:120–127
Schubert J (2002) Hydraulic aspects of riverbank filtration—field studies. J Hydrol 266:145–161
Sharma L, Greskowiak J, Ray C, Eckert P, Prommer H (2012) Elucidating temperature effects on seasonal variations of biogeochemical turnover rates during riverbank filtration. J Hydrol 428:104–115
Sowers L, York KP, Stiles L (2006) Impact of thermal buildup on groundwater chemistry and aquifer microbes. Proc Ecostock 1–7
Sprenger C, Lorenzen G, Hülshoff I, Grützmacher G, Ronghang M, Pekdeger A (2011) Vulnerability of bank filtration systems to climate change. Sci Total Environ 409:655–663
Stuart M, Jackson C, Bloomfield J (2010) Preliminary analysis of trends in UK groundwater temperature measurements from England and Wales. British Geological Survey Internal Report IR/10/033
Stumm W, Sulzberger B (1992) The cycling of iron in natural environments: considerations based on laboratory studies of heterogeneous redox processes. Geochim Cosmochim Acta 56:3233–3257
Taniguchi M, Uemura T, Jago-on K (2007) Combined effects of urbanization and global warming on subsurface temperature in four Asian cities. Vadose Zone J 6:591–596
Taylor CA, Stefan HG (2009) Shallow groundwater temperature response to climate change and urbanization. J Hydrol 375:601–612
Taylor RG, Scanlon B, Döll P, Rodell M, Van Beek R, Wada Y, Longuevergne L, Leblanc M, Famiglietti JS, Edmunds M (2013) Ground water and climate change. Nat Clim Change 3:322–329
Tobiason JE, Bazilio A, Goodwill J, Mai X, Nguyen C (2016) Manganese removal from drinking water sources. Curr Pollut Rep 2:168–177
UN (2022) The United Nations world water development report 2022. United Nations Paris
Walvoord MA, Kurylyk BL (2016) Hydrologic impacts of thawing permafrost—a review. Vadose Zone J 15:1–20
Walvoord MA, Striegl RG (2007) Increased groundwater to stream discharge from permafrost thawing in the Yukon River basin: potential impacts on lateral export of carbon and nitrogen. Geophys Res Lett 34:L12402
Wang C, Wang Z, Kong Y, Zhang F, Yang K, Zhang T (2019) Most of the northern hemisphere permafrost remains under climate change. Sci Rep 9:1–10
Welch SA, Ullman WJ (2000) The temperature dependence of bytownite feldspar dissolution in neutral aqueous solutions of inorganic and organic ligands at low temperature (5–35 C). Chem Geol 167:337–354
Whitehead PG, Wilby RL, Battarbee RW, Kernan M, Wade AJ (2009) A review of the potential impacts of climate change on surface water quality. Hydrol Sci J 54:101–123
WMO (2022) State of the climate in Europe 2021 (WMO-No. 1304). Geneva, Switzerland
Zeman NR, Irianni Renno M, Olson MR, Wilson LP, Sale TC, De Long SK (2014) Temperature impacts on anaerobic biotransformation of LNAPL and concurrent shifts in microbial community structure. Biodegradation 25:569–585
Acknowledgements
The authors would like to thank Hannah Lemke for graphic design support, Martina Adamek for internal review, and the two anonymous reviewers and the handling editor, Enrico Drioli, for their helpful comments. We are further grateful for financial support from the German Research Foundation (DFG) and the Open Access Publication Fund of the University of Tübingen.
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Open Access funding enabled and organized by Projekt DEAL. This review paper was funded by the German Research Foundation and the Open Access Publication Fund of the University of Tübingen. WS was further supported by the CSC-Tübingen PhD Program. Note that the funders had no role in the study design, literature research and analysis, decision to publish, or preparation of the manuscript.
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Neidhardt, H., Shao, W. Impact of climate change-induced warming on groundwater temperatures and quality. Appl Water Sci 13, 235 (2023). https://doi.org/10.1007/s13201-023-02039-5
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DOI: https://doi.org/10.1007/s13201-023-02039-5