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Cover crops reduce water drainage in temperate climates: A meta-analysis


Cover crops provide many ecosystem services, such as soil protection, nitrate pollution of water mitigation, and green manure effects. However, the impact of cover crops on soil water balance is poorly studied, despite its potential impact on groundwater recharge. Some studies reported a reduction of the water drainage due to an increase of the evapotranspiration by plant cover transpiration. However, there is no real consensus on the intensity of this phenomenon, which highlights the importance to quantify the impact of cover crops on drainage compared to that of bare soil. We performed a meta-analysis of published papers presenting studies on the impact of cover crops on drainage compared to that of bare soil under temperate climates. Of the 436 papers identified, 28 of them were included in the analysis based on criteria required for performing a relevant meta-analysis. The originality of our study lies in two following results: (1) the quantification of drainage reduction with cover crops by a mean effect size of 27 mm compared to that of bare soil and (2) within the large variability of soils, climates, and cropping systems, no main determining factor was found significant to explain the variability of water drainage reduction. The cover crops provide a service of nitrate pollution mitigation, but the drainage reduction could be considered as a disservice, because they can lead to a reduction in groundwater recharge due to a higher evapotranspiration in comparison to bare soil. This highlights the need of research for optimizing trade-offs between services and disservices of cover crops for water balance.


Cover crops are sown during the fallow period between two main cash crops and are grown for 2–8 months, depending on the crop rotation (Fig. 1). When they are destroyed, their biomass is returned to the soil, being either incorporated or left at the soil surface as a mulch. Cover crops are a useful agroecological tool that can provide multiple ecosystem services. Cover crops protect and improve soil physical properties, such as reducing soil erosion (Ryder and Fares 2008), and provide several biological ecosystem services, such as controlling pests, diseases, and weeds, and improving biodiversity (Haramoto and Gallandt 2005; Schipanski et al. 2014). When well-managed, they also reduce nitrate leaching and increase the green manure effect, which increases soil nitrogen content in cropping systems (Tosti et al. 2014; Tribouillois et al. 2015). Cover crops also increase the carbon content of soils (Poeplau and Don 2015; Tribouillois et al. 2018), which helps to mitigate effects of climate change, as highlighted in the international “4 per 1000” initiative (Demenois 2017). While government policies and climate change may therefore increase the use of cover crops, the IPCC reports that the future will have more droughts and greater variability in rainfall (IPCC 2013), which will increase water management challenges.

Fig. 1
figure 1

Comparison of cover crop treatment to that of bare soil. At the top, sorghum, and at the bottom, white mustard, 6 weeks after sowing

The impact of cover crops on water balance is not widely documented in the literature, and its net effect on annual drainage, i.e., water transfer to groundwater below the soil zone explored by crop roots, is debated. Cover crops reduce soil evaporation and increase plant cover transpiration, increasing evapotranspiration compared to that of bare soil (Qi et al. 2011a; Nielsen et al. 2015a). Cover crops also increase water infiltration and reduce runoff (Eshel et al. 2015; Yu et al. 2016). Although studies agree on these effects, the magnitude of effects depends greatly on the climate and soil context. Cover crop residues left as mulch after destruction can reduce evaporation, thus increasing soil water content (Alonso-Ayuso et al. 2014). The impact of cover crops on the factors influencing water balance makes it difficult to reach a consensus on their impact on water drainage. Several studies reported that cover crops reduce water drainage (Meisinger et al. 1991; Justes et al. 2012), while others reported no change (Qi et al. 2011b; Ward et al. 2012).

Several methods are available to measure water drainage, such as drained plots and lysimeters, but they are difficult to set up. Consequently, simulation modeling is frequently used (Gabriel et al. 2012; Constantin et al. 2015) to predict drainage in a variety of soil and climate contexts (Debaeke 2004).

Meta-analysis may better quantify the impact of cover crops on water drainage in a wide range of soil and climate contexts. This method is a quantitative systematic review that makes it possible to study global phenomenon over a wide range of experiments performed under a variety of circumstances (Glass 1976). In agronomy, it facilitates analysis of the variable effects of agricultural practices (Doré et al. 2011; Philibert et al. 2012). However, meta-analyses carried out in agronomy rarely perform sensitivity analysis or estimate publication bias. Philibert et al. (2012) highlighted that only 8% and 16% of them had done so, respectively. Since these analyses are needed to obtain a relevant and robust result, it is recommended to perform them both.

Meta-analysis has been used to examine impacts of cover crops on maize yields (Miguez and Bollero 2005), carbon sequestration (Poeplau and Don 2015), and nitrate leaching (Tonitto et al. 2006; Quemada et al. 2013; Valkama et al. 2015). However, meta-analysis of impacts of cover crops on water balance and drainage is lacking.

We used a meta-analysis approach to quantify the impact of cover crops on water drainage compared to that of fallow bare soil, i.e., without plant cover, under temperate climates, such as in Europe and North America.

Materials and methods

We followed five steps for a high-quality meta-analysis, as recommended and detailed in Philibert et al. (2012): (1) searching for papers in a scientific database, (2) extracting data from the papers’ studies, (3) using weighting to calculate the mean effect size, (4) investigating publication bias, and (5) performing a sensitivity analysis.

Database search

We searched the Web of Science database (27 Sep 2017) for papers written in English using the following query:

“Topic = ((cover crop* OR green manure OR catch crop*) AND (drain*) NOT vine* NOT orchard* NOT banana* NOT microbial* NOT rice NOT residu* NOT grape* NOT greenhouse NOT carbon NOT bacteri*))”

The search identified 436 papers. We then added 18 other papers from a review paper (Justes et al. 2012; Tribouillois et al. 2016) not found in our query but with all the query markers of our study. These papers were not specifically focused on drainage and therefore not found by our query. Based on the title and abstract, we excluded papers that did not study cover crops and water drainage or water balance, leaving 122 papers to be screened by reading the full text.

To be included in the meta-analysis, papers had to fulfill all of the following criteria:

  1. (1)

    Contain data on water drainage, which we defined as water unavailable to plant roots and likely to recharge groundwater, i.e., measured at a depth of 90 cm or more

  2. (2)

    Compare the impact of cover crops to that of fallow bare soil, without plant cover

  3. (3)

    Cover crops sown in summer or autumn after the cash crop harvest and destroyed (soil tillage) or terminated (crushing or herbicide) before sowing the next cash crop

  4. (4)

    Provide drained plot or lysimeter measurements or soil-crop model outputs

  5. (5)

    Perform studies under climates of class B, C, or D of the Köppen-Geiger classification (Peel et al. 2007) in order to represent temperate climates

  6. (6)

    Studies performed at the field scale

We read the 123 papers retained for their potential interest based on key words, and selected only 28 based on their relevance for analyzing our question. Moreover, since four of them compared field measurements to values simulated using soil-crop modeling for the same field and experiment, we divided each of them into two separate cases, resulting in 32 studies.

Data extracted from studies

We extracted the variables available and potential factors explaining the results, from each study, as follows:

  1. (1)

    Method used to obtain drainage: (i) field measurements using lysimeters or drained plots or (ii) simulation model outputs

  2. (2)

    Drainage (in mm) under the cover crop (XCC) for each year or site depending on the study

  3. (3)

    Drainage (in mm) under bare soil (XBS) for each year or site depending on the study

  4. (4)

    Geographic location and climate associated

  5. (5)

    Soil textural class: silt, clay, sand, or loam (Ditzler et al. 2017)

  6. (6)

    Cover crop biomass at destruction classified in two classes (< and > 1.5 t/ha)

  7. (7)

    Annual precipitation (in mm)

  8. (8)

    Season of cover crop sowing: summer or autumn

All data were extracted from the papers’ text, tables, and figures using the web application WebPlotDigitizer (Table 1).

Table 1 Characteristics of the papers selected for the meta-analysis, indicating the country in which they were performed, the method used (field measurements or simulation model), soil texture, seasons of cover crop (CC) sowing, rain level (a: < 750 mm, b: > 750 mm), and CC biomass (t/ha). USA United States, UK United Kingdom

Data analysis

Calculating the mean difference in drainage

In each study, for each year or site experiment, we calculated a difference in drainage (D) between the cover crop treatment (XCC) and the bare soil treatment(XBS):

$$ D={X}_{CC}-{X}_{BS} $$

We calculated individual effect size of each study (Di); it is the mean difference between water drainage under the cover crop and that under bare soil.

$$ {D}_i=\overline{D} $$

The number of replication of the experiment (n) is also extracted for the calculation of the standard deviation of the mean difference in drainage (\( {\sigma}_{D_i}\Big) \).

Calculating standard deviations and confidence intervals

For each study that included several experimental year or site, we calculated standard deviations associated with the difference in drainage.

$$ {\sigma}_{D_i}=\sqrt{\frac{\sum {\left({D}_i-\overline{D_i}\right)}^2}{n}} $$

We then used this standard deviation to calculate a 95% confidence interval.

$$ {CI}_{95\%}=\left[{D}_i-1.96{\sigma}_D;{D}_i+1.96{\sigma}_D\right] $$

Following Hossard et al. (2016), to avoid underestimating the variability, we assigned the maximum standard deviation of our dataset to studies without any.

Calculating mean effect size

Heterogeneity of Di in the database was tested by computing the Q statistics (Hedges et al. 1999). We used a random-effects model to estimate the mean effect size\( \left({\mu}_{est}^{RE}\right) \). With this statistical model, we assumed that the true effect could vary among studies. We selected this approach because studies differed greatly in how they measured or simulated drainage, the duration of experiments/simulations, the precision/accuracy of measurements/predictions, the soil and climate context, and cover crop species. This method required considering two sources of variance: (i) within-study variance (\( {\sigma}_i^2\Big)\kern0.5em \)and (ii) between-study variance (\( {\sigma}_b^2\Big) \) in the effect size, described by a probability distribution (Hedges et al. 1999). Studies were assigned weights (wi) to minimize both sources:

$$ {w}_i=\frac{1}{\sigma_i^2+{\sigma}_b^2} $$

Finally, the weights of the studies analyzed (indicated as P in the equation) were used to calculate mean effect size:

$$ {\mu}_{est}^{RE}=\frac{\sum \limits_{i=1}^P{w}_i{D}_i}{\sum \limits_{i=1}^P{w}_i} $$

We used the “metafor” package, “rma” function, and “REML” method (Viechtbauer 2010) of R software to perform the meta-analysis. Between-study variance was calculated using the maximum and restricted maximum likelihood methods. The standard deviation of mean effect size (σμ) equaled the reciprocal of the sum of the studies’ weights. The 95% confidence interval of the mean effect size was then calculated.

We conducted two separate meta-analysis to calculate the mean effect size: (i) one for field experiment studies and (ii) another for studies based on modeling.

Mean effect size by study factor

In the final step, we estimated the mean effect size (Eq. 6) of studies grouped by factors leading to four independent analyses: (i) soil texture, (ii) sowing seasons of cover crops and, to test the effect of cumulative transpiration on water drainage, (iii) biomass produced by cover crops (greater than or less than 1.5 t/ha), and (iv) precipitation level (greater than or less than 800 mm). We analyzed those factor effects only on field experiment studies since data with modeling were too few. Means were considered to be significantly different from one to another if their 95% CIs were non-overlapping.

Sensitivity analysis and publication bias

Sensitivity analysis

We performed a sensitivity analysis to test the robustness of the random-effects model. We estimated three other mean effect sizes (and their 95% confidence intervals) and then used the Akaike information criterion (AIC), which estimates the relative quality of model parametrization, to select the best statistical model. The model with the smallest AIC is considered best because it minimizes the risk of overparametrization and has the lowest calculation error.

We also evaluated the mean effect size using the mean standard deviation of other studies in the dataset (instead of the maximum) for studies that had not included a standard deviation or number of values. After calculating the between-study variance with the DerSimonian and Laird method, we compared the mean effect size estimated by a fixed-effect model to that of our previous random-effects model. A fixed-effect model is used when it is assumed that all studies share the same mean effect size. We estimated the mean effect size by removing one after the other ten studies with the biggest weight.

Publication bias

Publication bias can be an issue in meta-analysis since significant results are easier to publish than non-significant (Borenstein et al. 2009). We estimated publication bias by analyzing results graphically using a funnel plot, a common representation in meta-analysis (Light and Pillemer 1984). The funnel plot represents the inverse of the standard deviation of each study as a function of its individual effect size. It assumes that the more precise studies (at the top) will lie closer to the mean and that studies with less precision (at the bottom) will be spread around the mean effect size at the bottom. It should result in an inverted V-shape centered around the mean effect size.

Results and discussion

Cover crops have variable effects on water drainage

The difference in mean drainage under cover crops compared to that of bare soil varies greatly among the studies, varying from a maximum of 110 mm reduction to a 40 mm increase (Fig. 2). This variability on the effect is not unexpected since the studies cover a large range of soil, climate, and cover crop management and development. Since cover crops increase evapotranspiration (Nielsen et al. 2015b) and can also improve infiltration and reduce runoff (Yu et al. 2016), the range of effect is not surprising. Nevertheless, the vast majority of studies described a reduction in drainage, and more than 50% of studies described a reduction in a narrow range of 10–40 mm. There is a larger variability in data issued of studies based on measurements than of those based on modeling. The lowest variability in modeling could be explained because all processes are not represented in models. For example, the reduction of runoff and the increase of infiltration due to cover crops is usually not taken into account. However, their means are quite close (− 30 mm and − 33 mm, respectively, for studies based on modeling and studies based on measurements) which indicates a robust estimation of the cover crop effect on the reduction of drainage, whatever the method used for its evaluation (Fig. 2).

Fig. 2
figure 2

Histogram of mean water drainage difference between cover crops and bare soil, grouped into 10 mm classes, among the 32 studies. In green, field measurement studies, and in red, modeling studies

Cover crops reduce drainage

Cover crops reduce drainage compared to that of bare soil: the mean effect size of the meta-analysis was − 27 mm for studies based on measurements and − 32 mm for studies based on modeling. The 95% confidence interval of the effect size was very close: 20–34 mm for studies based on measurements and 21–43 mm for studies based on modeling (Fig. 3). It was larger for studies based on modeling because there is less studies to calculate the mean effect size (22 studies versus 10 studies).

Fig. 3
figure 3

Mean effect size (circles) and 95% CI (horizontal lines) of the difference in mean drainage for field measurement studies or modeling studies (at the top) and as a function of certain factors (only for studies done by measurements): (1) soil texture, (2) sowing season, (3) precipitation level, and (4) cover crop biomass. The letter “n” is the number of observations for each group within a factor category

This result is in agreement with the review of Justes et al. (2012) based on field measurements and simulation results using the STICS soil-crop model (Brisson et al. 2003). They reported that cover crops reduce water drainage by 20–50 mm, which represents from less than 10 to 25% of annual drainage under cropping systems depending on the region of France. Water drainage under bare soil among the studies in our dataset varied greatly (0–600 mm) due to the influence of factors such as climate, irrigation, and soil hydraulic characteristics. As a result, the same reduction in millimeters could represent very different proportions on annual drainage and consequently impact on groundwater recharge. In rainy regions, 27 mm represents a small percentage of annual drainage. For example, in Iowa (USA), drainage could reach more than 500 mm in region where rainfall exceeds 800 mm per year (Logsdon et al. 2002; Kaspar et al. 2012). In contrast, in drier regions in temperate climate zones (e.g., southern France), such reduction in drainage could represent most or all of the annual drainage (Plaza-Bonilla et al. 2015). Simulation models tended to predict greater reduction in water drainage than that observed in field measurements (lysimeters and drained plots) (Li et al. 2008; Qi et al. 2011b; Malone et al. 2017). Crop soil models can overestimate cover crop biomass when certain limiting factors are not accurately represented (e.g., water and nutrient limitations) or not represented at all (e.g., pests and diseases).

No significant effect of factors but some trends observed

The meta-analysis clearly highlighted that cover crops reduce water drainage. Conversely, it did not indicate a significant trend for the effects of factors that could explain the variability in reduced drainage. Because so few studies were available, it was difficult to find statistically significant difference. Nonetheless, we observed a few trends in the mean effect size of groups within certain factor categories. Although never significant, those differences in mean effect size between groups within the factor categories were sometimes large and have a clear functional explanation.

The expected relationship between biomass and drainage is not observable on the two levels of biomass. The reduction in drainage is a little bit greater when cover crops had less than 1.5 t/ha of biomass but not significant. This result is surprising because one can think that a bigger cover crop biomass lead to a greater evapotranspiration through an increase of cover transpiration, despite the reduction of soil evaporation. A hypothesis may be that cover crops increase evapotranspiration up to a certain level of biomass, and after this threshold, the reduction of soil evaporation due to the cover becomes predominant. In addition, root biomass is often correlated with aerial biomass, a greater aerial biomass leading to a more develop rooting system. Several authors indicate that cover crop roots may structure the soil, increased water infiltration and soil water availability (Chen et al. 2014; Basche et al. 2016; Yu et al. 2016). The effect of cover crops with high aerial biomass on soil structure with an increase of soil water content may conduct to this result on water drainage compare to cover crops with lower biomass.

An observable trend is the influence of precipitation level on the reduction of water drainage. Indeed, there is a greater reduction in studies with more than 800 mm of precipitation per year than studies with low precipitation (around 10 mm) (Fig. 3). In dry regions with low drainage, cover crops can cancel all drainage. If the drainage was more important, maybe the reduction would be so. However, the confidence interval 95% of the group with high precipitation is too wide that it is not possible to be conclusive regarding this factor. It also seems to have a larger reduction in water drainage in silt and clay soils than in loam soils. However, their confidence intervals are quite wide and this trend is hard to understand if it is not just random. The season of sowing cover crops did not influence reduction in water drainage. This result is also surprising because, in summer, cover crop development and low rainfall may reduce soil water content and thus water drainage later in autumn and winter. In contrast, autumn rainfall can compensate for the water used for cover crop transpiration when they are sown at this season.

The lake of impact of these different factors suggested that there are probably confounding effects since the database did not cover all the possible combinations between soil type, climate characteristics, cover crop species, period of sowing, and destruction. Indeed, the impact of cover crops on water drainage certainly results from the interaction of climate, soil, and cover crop management (i.e., density and date of sowing and destruction). However, the low numbers of references studying drainage do not allow to give a large-scale answer on the impact of cover crops on drainage compare to that of bare soil and particularly on the determining factors conditioning this effect.

Qualitative analysis of the meta-analysis: the result obtained is robust

The test of heterogeneity was significant and the AIC of the random-effect model was lower than other tested models, and then the homogeneity was not demonstrated. Varying the methods used to construct the random-effects model had little influence on the result. Mean effect size in the sensitivity analysis always indicates a reduction in water drainage, ranging from 32 to 26 mm, concluding to a robust estimate. The result of our meta-analysis does not change when removing the data with the highest weigh from the database (Fig. 4a). This figure shows that when removing the four more weighed studies, the effect is approximately the same even if the standard deviation increase. Beyond that, the mean reduction of drainage tend to slightly increase until − 42 mm when 10 studies are removed. Obtaining the same effect when removing studies proves that the results on drainage reduction are not dependent on one or two dominant studies which strengthen its robustness.

Fig. 4
figure 4

a Sensitive analysis of data done by measurements. The x-axis represents the mean size effect of reduction in water drainage and y-axis shows the number of studies removed according their standard deviation, the study with the lowest standard deviation being removed. b Funnel plot representing the inverse of the standard deviation as a function of the study’s individual effect size. Only studies reporting standard deviations were considered (28 differences in drainage out of 32). The dashed line represents the mean effect size of the meta-analysis

The funnel plot assessing publication bias shows studies distributed symmetrically on both sides of the mean effect size (Fig. 4b). Studies with the lowest variability lay closest to the mean effect size (at the top of the graph). It is important to note that this observation is valid for data issued from studies based on measurements and on modeling.

The many tests of robustness and sensitivity analysis applied allow us to conclude that the effect of cover crops on drainage reduction obtain in this meta-analysis is robust. The reduction of approximately 30 mm of drainage is found throughout the different analysis, even if the main factors could not be identify.

The lack of available references on the relationship between cover crop management and water balance

Despite reducing annual water drainage, cover crops are known to decrease efficiently nitrate leaching, providing an ecosystem service of nitrate capture or catching (catch crop function) that decreases water pollution (Tonitto et al. 2006). Cover crops also provide multiple services, such as protecting soil from erosion, green manure effect, or carbon sequestration (Justes 2017). However, and in addition to drainage reduction impacting groundwater resources, cover crops may also reduce soil water content at sowing of the subsequent cash crop, which may decrease its emergence rate and early growth, particularly if they are destroyed close to its sowing date (Unger and Vigil 1998; Mitchell et al. 2015; Nielsen et al. 2015b). Irrigation can compensate for a lack of soil water but means higher costs for farmers and is not always available on farm. In addition, not all fields can be irrigated, and in certain regions in the world, more droughts and less water mean that irrigation is not a viable solution. If we were not able in this meta-analysis to point out the main factors driving the intensity of these negative effects on water dynamics, it would be useful to study relationships between cover crop management and soil water balance in various pedoclimatic conditions, such as the effects of (i) choice of species and cultivar, (ii) sowing date, (iii) destruction date, and (iv) method of destruction (tillage, frost, or herbicide) on biomass production and the associated evapotranspiration. It is highly likely that cover crop growth, cover crop duration, and water drainage interact. A better understanding of those relationships would allow to adapt cover crops’ management to maximize positive effect (e.g., N and C balances) while limiting the negative ones on water, according to the pedoclimatic conditions.

If field experiments are useful to gather knowledge on those interactions, they are costly and time-consuming and may experience large variability in weather over time. Also, it may not be possible to extrapolate results from one soil and climate context to another due to strong dynamic interactions between cropping and pedoclimatic conditions. Simulation modeling is another approach to understanding soil × climate × crop interactions and their impact on water balance (Meisinger et al. 1991; Basche et al. 2016). Modeling offers many opportunities to investigate selection and management of cover crops in cropping systems over several years with soil and climate variability (Qi et al. 2011b; Malone et al. 2014).

An impact on groundwater recharge to assess at a larger scale

To increase the use of cover crops to mitigate nitrate pollution in nitrate-sensitive areas, recycle nitrogen in the system, and provide other ecosystem services, cover crop management must optimize the compromise between services and disservices for water groundwater recharge. The meta-analysis indicates a mean reduction in groundwater recharge of 270 m3/ha (i.e., 27 mm), which represents most of the groundwater recharge in certain regions in dry years (Constantin et al. 2010; Plaza-Bonilla et al. 2015; Martinez-Feria et al. 2016). Then, a wider use of cover crops could pose a problem at the watershed scale if groundwater is shallow. According to the IPCC (2013), which predicts more droughts, extreme events, and a greater variability in rainfall in certain temperate regions, this reduction could become a crucial issue, as Tribouillois et al. (2018) have shown. Consequently, for shallow groundwater that is recharged mainly by drainage under soils of arable cropping systems, the reduction in drainage caused by cover crops could decrease groundwater reserves, which provide water for cities and irrigation, sustain the base flow of rivers, and support aquatic biodiversity. Studies at the field scale are not sufficient to assess the effect of cover crop on hydrology at a watershed scale. Since watersheds have agricultural as well as non-agricultural lands, such as forests or grasslands, in various proportion, it is hard to predict the impact on hydrology based on field-scale result. To do so, one would need to use agro-hydrological models to be able to quantify the impact of cover crops on water dynamics at this scale, such as the SWAT model or the MAELIA platform (Garg et al. 2012; Therond et al. 2014). It would also be useful to develop tools to find a compromise between cover crop-targeted services (e.g., nitrate capture, green manure effect) and disservices (impact on soil water availability for the subsequent cash crop and groundwater recharge).


The impact of cover crops on annual water drainage varies according to the soil and climate context. Our meta-analysis indicated a reduction in drainage in 90% of the studies analyzed and a mean weighted reduction between 32 and 27 mm compared to that of bare soil. The sensitivity analysis and assessment of publication bias indicated that the meta-analysis is robust and insensitive to individual studies. However, we were unable to determine the key factors that explained the variability in reduced drainage. This is mainly due to the low number of published studies usable for the analysis and also due to strong interactions between soil, climate, cover crop used, and cropping system in relation to the dynamics of processes. More field experiments with cover crops and water balance measurements and simulation studies using validated dynamic soil-crop models are then needed. This may help assessing the impacts of various factors such as soil, climate, cover crop biomass, and management, and their interactions on water balance and drainage.


References of the meta-analysis

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Thanks go to Michelle and Michael Corson for proofreading and correcting the English. The authors also thank François Brun and David Makowski for advice on performing the meta-analysis and Delphine Burger-Leenhardt for proofreading the manuscript.


This study was funded by the Adour-Garonne water agency (BAGAGES project) and the Occitanie region (CLE BAGAGES-Cisol project).

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Meyer, N., Bergez, JE., Constantin, J. et al. Cover crops reduce water drainage in temperate climates: A meta-analysis. Agron. Sustain. Dev. 39, 3 (2019).

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  • Catch crops
  • Review
  • Groundwater recharge
  • Water balance
  • Pedoclimatic factors
  • Biomass