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Linking Populus euphratica Hydraulic Redistribution to Diversity Assembly in the Arid Desert Zone of Xinjiang, China

  • Xiao-Dong Yang,

    Affiliations College of Ecological and Environmental Sciences, East China Normal University, Shanghai, China, Tiantong National Forest Ecosystem Observations and Research Station, Chinese National Ecosystem Observation and Research Network, Ningbo, China

  • Xue-Ni Zhang,

    Affiliations Institute of Resources and Environment Science, Xinjiang University, Urumqi, China, Xinjiang Key Laboratory of Oasis Ecology, Ministry of Education, Urumqi, China

  • Guang-Hui Lv ,

    ler@xju.edu.cn

    Affiliations Institute of Resources and Environment Science, Xinjiang University, Urumqi, China, Xinjiang Key Laboratory of Oasis Ecology, Ministry of Education, Urumqi, China

  • Arshad Ali

    Affiliations College of Ecological and Environmental Sciences, East China Normal University, Shanghai, China, Tiantong National Forest Ecosystem Observations and Research Station, Chinese National Ecosystem Observation and Research Network, Ningbo, China

Linking Populus euphratica Hydraulic Redistribution to Diversity Assembly in the Arid Desert Zone of Xinjiang, China

  • Xiao-Dong Yang, 
  • Xue-Ni Zhang, 
  • Guang-Hui Lv, 
  • Arshad Ali
PLOS
x

Abstract

The hydraulic redistribution (HR) of deep-rooted plants significantly improves the survival of shallow-rooted shrubs and herbs in arid deserts, which subsequently maintain species diversity. This study was conducted in the Ebinur desert located in the western margin of the Gurbantonggut Desert. Isotope tracing, community investigation and comparison analysis were employed to validate the HR of Populus euphratica and to explore its effects on species richness and abundance. The results showed that, P. euphratica has HR. Shrubs and herbs that grew under the P. euphratica canopy (under community: UC) showed better growth than the ones growing outside (Outside community: OC), exhibiting significantly higher species richness and abundance in UC than OC (p<0.05) along the plant growing season. Species richness and abundance were significantly logarithmically correlated with the P. euphratica crown area in UC (R2 = 0.51 and 0.84, p<0.001). In conclusion, P. euphratica HR significantly ameliorates the water conditions of the shallow soil, which then influences the diversity assembly in arid desert communities.

Introduction

The hydraulic redistribution (HR) is defined as the movement of water from the moist to dry soil portions through roots of deep-rooted plants [1][3]. Through this process, water moves upward or laterally among different soil layers, and subsequently changes the water spatial pattern of soil [3], [4]. Thus, HR improves the fine roots survival rate of deep-rooted plants and protects the shallow-rooted plants growth in extremely dry environments [4][6]. In addition HR plays an important role in positive feedback between plants and soil moisture circulation [1], [7][10], it also benefits the plant rhizosphere nutrient absorption, community stability, and biodiversity maintenance [3], [11][20].

Populus euphratica Oliv., a deciduous plant with high tolerance to drought and saline conditions, and is a dominant species for the Tugai Forest (desert riparian forest) in the Ebinur desert. Pervious research findings have revealed that the water gradient of soil layers determines the occurrence of HR in deep-rooted plants [3], [4], [11], such as when the surface soils are extremely dry and the deeper soils are rich in available water [3], [4], [21]. P. euphratica developed a deep vertical root system for absorbing water in Chinese arid deserts due to effect of high wind [22][24]. Moreover, the annual precipitation of this site is less than 100 mm and the surface soils are extremely dry, whereas the groundwater level is relatively high because of glacial melt waters [22]. Hence, P. euphratica should possess HR.

In our previous study [22] and the one conducted by Hao et al. [23] employed the Ryel model [25], that was used to simulate HR of P. euphratica. According to the research findings of the above mentioned studies that P. euphratica has HR which reached a maximum point at 2∶30 am for a given day, and the total amount of HR decreased with changes in the plant growing season [22], [23]. But, those results were only based on water characteristics (water content and water potential) changes along the various soil layers, which are only obtained from model predictions. The experimental support of P. euphratica possessing HR is lacking. Here we investigate whether oxygen isotope tracking can be used to test whether the plants possess HR [1][4], [11], and this could provide the experimental support to the studies based on model simulations. As oxygen isotope does not fractionate during water transport through xylem vessels, whereas the 18O/16O values varied across the different soil layers [1], [26][28]. For example, the δ18O content continues to increase from deep to shallow soils based on fractionation. Thus, we can predict that if P. euphratica possess HR, P. euphratica roots can lift water containing lower δ18O content from groundwater and deep soils to shallow soils through xylem vessels, which can result in soil having lower δ18O content under the P. euphratica canopy (under community: UC) rather than outside the P. euphratica canopy (outside community: OC).

Annual precipitation in Ebinur desert is very scarce, which is insufficient for the basic physiological activity of plants, while the deep soils and shallow groundwater contains abundant water for plant growth in this region [29]. However root density of most plants decreases with increasing soil depth [22], [30], [31], and only a small number of deep-rooted plants are able to penetrate to the deeper soils or the water table to absorb water which limits water utilization and subsequently, decreases the species richness and abundance in the arid desert [32], [33]. So, if P. euphratica HR lifts water from the deeper soils or groundwater aquifer to shallow soils through its roots, this process can increase the water content of surface soils and afford more water for shallow-rooted shrubs and herbs. In this case, it can induce the plants assembly under P. euphratica canopy and subsequently maintain the biodiversity in arid deserts. Therefore, we hypothesize that, the shallow-rooted shrubs and herbs grow better in UC than in OC and there is a higher species richness and abundance in UC than in OC, because P. euphratica HR significantly improves the soil water content. But, the correlation between P. euphratica HR, plant growth condition and biodiversity in arid desert areas is poorly understood.

The objective of this study was to test for P. euphratica HR and to explain the effect of HR on plants growth condition and species biodiversity maintenance in the Ebinur desert. We predict the following: (1) δ18O content of the shallow soils in UC are higher than in OC; (2) shrubs and herbs of UC have higher growth condition than those of OC; and (3) P. euphratica HR influence species abundance and richness in arid desert.

Materials and Methods

Study site and Ethics Statement

The experimental site is located in the Ebinur Lake Wetland Nature Reserve (ELWNR) in the western margin of the Gurbantonggut Desert in Xinjiang Uygur Autonomous Region of China (44° 30′–45° 09′ N, 82° 36′–83° 50′ E). This site belongs to a tuyere zone of Alashankou, the annual wind days (days with wind speed ≧17 m/s) are more than 164 d, and the annual fresh gale hours are approximately 241 hr. The annual sunshine hours reach approximately 2800 hr, and the annual precipitation is less than 100 mm, whereas the potential evaporation is more than 1600 mm. In addition, the temperature in this area ranges from 44 to −33°C, with an average temperature ranging from 6 to 8°C, and an average temperature of the growing season is roughly 25°C. Due to the extremely dry conditions and sparse rainfall, the climate is classified as typical temperate continental arid [22].

No specific permissions were required for the described field studies in ELWNR. The ELWNR is owned and managed by the local government and the location including the site used for our experiment are not privately owned or protected in any way and thus a specific permit for not for-profit research is not required. The field studies did not involve endangered or protected plant species in this area.

Study plot and samples collection

5×5 km (25 km2) typical plots of P. euphratica were chosen as our experimental plots, where 48 P. euphratica individuals are distributed and the vegetal coverage is 4%. This site has a moderate slope and sandy soil. The distribution of groundwater level in our experimental site ranges from 1.5 to 1.8 m. Moreover, sand dunes are present 3 km north of the site. Based on the terrain of the experimental site, we randomly selected three P. euphratica individuals with no differences in growth conditions (DBH, tree height and crown area) among those trees as the experimental (UC) group. The selected plant individuals were at least 6 m apart from each other to prevent mutual water transfer process among them. For comparison, we randomly selected three plots located closely to the selected three P. euphratica individuals as the control (OC) group, where no P. euphratica were growing and no groundwater table difference with UC group.

To distinguish the difference in water transport from deeper soil layers to surface soil layers between the UC and OC groups, three points in each two types of plots were randomly selected and each point was divided into five soil layers (0 to 10 cm, 10 to 40 cm, 40 to 70 cm, 70 to 100 cm, and 100 to 150 cm, the deepest soil layer is 150 cm, as groundwater appeared approximately at 160 cm when the soil columns were dug out in the above selected OC and UC points). Each soil sample was dug with a soil auger between 4∶30 AM and 5∶30 AM (Xinjiang local time) in the middle of July, 2010. The nine soil samples for each soil layer from three points were mixed to makeup a composite soil samples. Meanwhile, on the periphery of selected plots, well water 3 m beneath ground level was collected from five sites, and subsequently mixed them to obtain a composite sample to replace groundwater. A river water sample was also mixed from three sites at least 1 km apart of the Aqikesu River. Each sample of river water was collected from 1 m beneath river surface. All the soil and water samples were immediately placed into glass bottles, sealed with Parafilm and stored in a mini refrigerator (4°C) and brought to the Xinjiang University Physiological Ecology Laboratory for further experimental analysis.

Oxygen isotope measurement

Methods for extraction of soil water are consistent with Allison et al. [34]. Water isotope content (δ18O) was measured using a DELTA V Advantage Isotope Ratio Mass Spectrometer (Thermo, Waltham, MA, USA) at the Chinese Academy of Forestry Stable Isotope Laboratory. Each sample was measured three times continuously with the third result as the experimental oxygen isotope value. Precision values of continuous measurements for standard sample were as follows: D, <3‰ and 18O, <0.5‰. The isotopic abundance was expressed in delta notation (δ) in parts per thousand (‰) as(1)Where Rsample and Rstandard are the molar ratios of heavy to light isotope of the sample and the international standard (Vienna standard mean ocean water for 2H/1H and 18O/16O) [1].

Plots investigation

48 plots of UC were established having each plot size of 10×10 m (14 plots in June, 17 plots in August and October) in 5×5 km experimental plot from June to October, 2010. Consequently, 34 control plots with 10×10 m of OC (13 plots in June, 15 plots in August and 16 plots in October) were set at the same time. The species identification, richness, abundance, coverage, DBH, and crown area of each plant in each plot were investigated.

Data analysis

To determine whether P. euphratica undergoes HR, a comparison analysis was used to show the difference in δ18O content for the five soil layers between the UC and OC groups. In addition, the paired-sample t-test was used to test the significant difference between above mentioned two groups.

Furthermore, based on the plots investigation data, the growth dominance index (Formulae 2 to 4) was used to show the growth condition, i.e. difference between UC and OC.(2)(3)(4)Where xs, xsc, xsa, xsh and xsf are the standardized value, coverage, abundance, height and frequency for a given species in a given plot respectively. xmax and xmin are the maximum and minimum values for a given species in a given plot while x is the actual investigative value of each individual belonging to the same species in a given plot. DI is the dominance index in a given plot, and GDI is the growth dominance index of all plots. N is the count of plots, and DIi is the dominance index of a given species in i th plot.

Individual size has positive correlations with the amount of HR which can generally represent the water lift capacity of HR. It is well understood that the crown area of arid desert vegetation is significantly linked with adult size (tree height) and root biomass [35], [36]. Thus in this study, we used the individual crown area (CA, Formula 5) to represent water lifting capacity of P. euphratica HR. Maximum vegetation crown diameter (CD1) and its perpendicular diameter (CD2) were measured on each plant individual, which were used to calculate CA as follows (Formula 5).(5)

In order to explain the effects of HR on species richness and abundance in the arid desert community, an independent sample t-test was used between UC and OC to determine the diversity difference for shrubs and herbs. Finally, the logarithmic regression analysis was applied to explore the relationship of HR capacity (CA) to species richness (species number in 10×10 m) and abundance (count of individual plants in 10×10 m) for arid desert community.

All statistical tests were conducted using SPSS 11.5 while related figures were drawn using Origin 8.0. All statistical tests were considered significant at the p<0.05 level.

Results

Comparisons of δ18O values between the UC and OC

δ18O content of the OC were generally higher than that of the UC among five soil layers. In addition, the maximum difference between the two groups were observed in the surface soil layer (0 to 10 cm), and then decreased with soil depth (Fig. 1a). Therefore, a paired-sample t-test exhibited that the mean of five soil layer δ18O contents of OC was significantly higher than that of UC (t = −3.28, df = 4, p<0.05, Fig. 1b). The general comparison showed that δ18O content was the highest in soil, medium in groundwater and the lowest in river (Fig. 1a).

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Figure 1. Difference in δ18O value with soil depth between UC and OC groups.

UC is the community under the P. euphratica canopy, whereas the OC is the community outside the P. euphratica canopy. The soils were divided into five layers (0 to 10 cm, 10 to 40 cm, 40 to 70 cm, 70 to 100 cm, and 100 to 150 cm) based on P. euphratica roots and underground water level distributions. Each point in the Fig. 1a showing δ18O for each soil layer sample, which was measured for three times continuously with the third result as the experimental oxygen isotope value. Nine soil samples for each soil layer from three points were mixed to get one composite soil in each group. 18O contents of river (−11.55‰) and underground water (−10.59‰) are show through vertical dashed and solid lines respectively in Fig. 1a. Fig. 1b shows the mean comparison between UC and OC groups and the data in parenthesis showing the Paired-Sample t-test result. (Mean ± SD) for significance difference between two groups.

https://doi.org/10.1371/journal.pone.0109071.g001

Difference in species dominance index and biodiversity between the UC and OC

Both the shrubs and herbs growth dominance index (GDI) of UC were higher than that of OC in June, August and October (Table 1). This finding indicates that the shrubs and herbs species grew better in UC than that in OC. Furthermore, compared with OC, the shrubs richness and abundance of the UC were significantly higher across three months (p<0.05) (Fig. 2). But for the herbs, this pattern of richness and abundance varies along the plant growing season. Between UC and OC, the species richness and abundance of herbs and shrubs were significantly similar in June and August, while non-significant differences were found in October (Fig. 2). Further, based on all UC plots investigated, the logarithmic regression analysis was used to analyze the relationship of P. euphratica individual HR capacities (individual crown area) with species richness and abundance. The results show that, species richness and abundance exhibited a significant exponent correlation with P. euphratica CA (p<0.05) (Fig. 3).

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Figure 2. Difference in richness and abundance along plant growing season between UC and OC.

UC is the community under the P. euphratica canopy, whereas the OC is the community outside the P. euphratica canopy. Blank and grid boxes indicate shrub and herbage, respectively. The Independent sample t-test is used to analyze the differences of richness and abundance between UC and OC. Different capital letters on each blank box indicate significant differences of shrub richness or abundance between UC and OC. Different lowercase letters on each grid box indicate significant differences of herbage richness or abundance between UC and OC. p<0.05. Numbers in figure are the results of Independent sample t-test. (Mean ± SD) for significance difference between UC and OC.

https://doi.org/10.1371/journal.pone.0109071.g002

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Figure 3. Logarithmic regression of P. euphratica crown areas against species abundance and richness.

In regression line (Fig. 3a), each point indicating the richness of all species (no including P. euphratica) under the P. euphratica canopy. In regression line (Fig. 3b), each point indicating the abundance of all species (no including P. euphratica) under the P. euphratica canopy. The crown area of each sample is the sum of P. euphratica individuals.

https://doi.org/10.1371/journal.pone.0109071.g003

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Table 1. Differences of species growth dominance index between the UC and the OC.

https://doi.org/10.1371/journal.pone.0109071.t001

Discussion

Experimental validation of P. euphratica HR

Oxygen isotope fractionates during water transport between the different soil layers because of physical and chemical adsorption and conduction processes, which changes the 18O/16O values in different soil layers. However, the fractionation of oxygen isotopes does not occur during water transport through the xylem vessels [1], [26][28]. So the water originating from the deeper soils or groundwater in the shallow soils is an indicator for HR occurrence [1][3], [11], [37]. In the present study, the soil samples of UC and OC groups were collected at between 4∶30 AM and 5∶30 AM (local time), during which the fractionation not occur due to soil evaporation. Therefore, if P. euphratica HR does not occur, as the environmental conditions were same between UC and OC groups, the δ18O content of the corresponding soil layers did not differ significantly between UC and OC groups. However, in this study, all δ18O content of UC were lower than those of OC group among five soil layers (Fig. 1a), and the mean of UC was also significantly lower than OC group (Fig. 1b). This overall pattern exhibited that the water of all UC soil layers partially originated from deeper soil or groundwater through plants vessel transport. In other words, the deep-rooted P. euphratica exhibited HR, which transported and lifted water from deeper to shallow soil layers, proof for the experimental support to Ryel model based studies [22].

It is well understood that changes in soil evaporation depends on vegetation coverage, for example, the higher vegetation coverage will has more shade on the soil surface and hence evaporation will decrease, and vice versa [38], [39]. Furthermore, Allison [40] and Kim [41] confirmed that δ18O content of soil samples in UC is lower as compared to OC, because high vegetation coverage decreased the evaporation due to shading. Specifically, higher evaporative demand in OC could easily drive a greater upward movement of water from the groundwater or the deeper soils to surface soils, which then enriched the δ18O content due to evaporative fractionation. However, pan evaporation was not significantly different between UC and OC (UCsoil evaporation = 0.91±0.52 cm·m−2·d−1, OCsoil evaporation = 0.93±0.55 cm·m−2·d−1, t = −1.02, df = 6, p = 0.34, which was tested through paired-sample t-test, and its supportive data was measured by 255 Series Evaporation Stations (EP255, Novalynx Inc, OR, USA) for three paired groups in UC and OC), because the sparse vegetation coverage of P. euphratica community (approximate 4%) has little shading influence on the evaporative demand of UC and OC in Ebinur desert [22]. In addition, this desert is a part of tuyere zone having high wind, and thus other evaporative environmental factors (e.g., air temperature and moisture) homogenously influence soil evaporation, subsequently caused relatively no difference of soil evaporation between UC and OC plots. Hence, soil evaporation not likely differed δ18O content between OC and UC in the Ebinur desert and further proved that P. euphratica HR occurs.

P. euphratica HR and water transport direction along soil profile can also be judged by moisture differences among soil layers. In this study, Thetaprobe ML2 soil moisture sensors (Delta-T Devices, Cambridge, UK) were installed respectively in five soil layers of UC and OC to measure the variation in soil volumetric water content (SVWC) along soil depth. The results showed that, (1) SVWCs of 0 to 10 cm, 10 to 40 cm, 70 to 100 cm and 100 to 150 cm layers in UC were significantly higher than those in OC, except in 40 to 70 cm soil layer; (2) SVWC increases with soil depth but decreases with δ18O content in OC, while no significant trend was found in UC; and (3) SVWC of 100 to 150 cm soil layer was a little higher in OC than in OC (Table 2). These results suggested that groundwater supplies soil water, and the water’s table in both UC and OC were similar in Ebinur desert. SVWC increased with soil depth due to the extraction of soil evaporation in OC. But HR can lift water from groundwater and deep soils to shallow soils and then decrease the effect of evaporation on water extracting in UC. Previous studies showed that the location and the amount of HR releasing water were significantly depended on plant fine roots distribution [11], [22], [23]. Also P. euphratica’s fine roots was mainly growing within 0 to 70 cm soil depth in arid area [22], [29]. Thus, HR may cause no change in SVWC across soil depth in UC and SVWC of 40 to 70 cm layer in UC less than that in OC.

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Table 2. Variation in soil volumetric water content across soil depth and δ18O content in UC and OC.

https://doi.org/10.1371/journal.pone.0109071.t002

The greatest δ18O content existed in soil while the intermediate in groundwater and the lowest in river (Fig. 1a). This pattern indicates that river is the initial source of water for arid desert area. Our results were supported by Zhao et al. [42] reported that river largely originated from glacial melting and has the lowest δ18O content in arid desert. Based on oxygen isotope fractionation theory [26][28], [40], initial water resource has lowest δ18O content and then increased with transmittal distance and pathways. In this study, the river is the main source for groundwater and then supply to soil water through water transmittal ways. i.e. underground or surface runoff, evaporation and HR. All of those can led to oxygen isotope fractionation and then resulted in soil having the greatest value of δ18O content.

Effects of P. euphratica HR on species growth condition

The importance value index [importance value index = (relative abundance + relative frequency + relative coverage + relative height)/400] and its deduced dominance index (dominance index = , N is the count of plots and Ni is the importance value of a certain species in i th plot) were traditional ecological methods in generally using to evaluate species growth conditions within a specific community type [43], [44]. Specifically, the importance value is commonly assumed as 1, and then based on individual relative statistical values, such as individual numbers, relative abundance, relative coverage, relative frequency, and relative height. 1 was divided into different components values that show the different species growth conditions within a given community. Nevertheless, many studies also needed to compare the difference of same species growth conditions among environmental sites, such as the same species between UC and OC. According to this situation, considering P. euphratica can account for the largest partition of the importance value in UC, if we used the traditional methods above to evaluate the difference of species growth conditions between UC and OC, a lower importance value could be found in UC than in OC among other species, even these species have the same abundance, coverage, frequency and height between two environmental types.

In this study, the growth dominance index was structured by the actual values of coverage, abundance, height, and frequency of a given species in a given plot to avoid the components influence of importance value, and to compare the difference of species growth conditions between the UC and OC (Formulae 2 to 4). The results showed that UC species grow better than OC along plant growing seasons (Table 1). Additionally SVWC increased with soil depth in OC while no change in UC (Table 2). These suggest that P. euphratica HR increased significantly water content of shallow soils and benefited the growth condition and survival of shallow-rooted plants [16], [17], [24], [37], [45][50].

Relationship between P. euphratica HR and arid desert diversity assembly

Water is the main limitation for arid desert plant communities [1], [51]. Thus, species coexistence pattern in this community directly depends on spatial availability and distribution of water [32], [33]. In this study, the species richness and abundance in the UC were significantly higher than those in the OC (p<0.05), i.e., UC has higher species diversity (Fig. 2).

Furthermore, based on the hypothesis of this study that a tree with a larger crown area has higher root biomass and transports more water from the deep to shallow soils, the logarithmic regression was used to analyze the relationship between the P. euphratica HR capacity (CA) and the species richness and abundance in the UC. The results showed that the P. euphratica CA was significantly logarithmically correlated with richness (R2 = 0.51) and abundance (R2 = 0.84) (p<0.001) (Fig. 3). These results indicated that species diversity was influenced significantly by HR. Similarly, this conclusion was also reflected in other studies. For example, herbaceous plants under tree canopies have higher abundance and richness [46], [52], and the presence of trees promoted the survival of shrubs and seedlings grown under tree canopies [37], [45], [48][50], [53].

Shallow-rooted herbs and shrubs that absorb water from P. euphratica HR provided more organic matter and mineral elements to the soil of the UC than to those of the OC because of the “fertile island” effect. It implies that more individuals of the UC are intercepted and sequester larger amounts of organic matter and minerals from surface winds because of increased total crown area [54][59]. Meanwhile, the more numerous individuals also produced more litter into the UC soils than OC soils. Thus, these processes contributed to the nutrient absorption and growth of P. euphratica, which further increased its HR capacity. In turn, these processes also increased the shading in understory plants, which can decrease the transpiration of herbs and shrubs, and further improve its survival. Therefore, there appears to be a species coexistence pattern of water sharing and resource complementation between the deep-rooted P. euphratica and other shallow-rooted species, as well as positive feedback between P. euphratica HR and biodiversity maintenance in arid deserts community.

Acknowledgments

The authors thank Yang jun, Sun Jingxing, Tian Youhua, Sun Lijun, Zhang Xuemei, Li Changjun, He Xueming, Qin Lu, Luo Chong, Ren Manli, Zhu Ya for their help in the field and laboratory. The authors also thank Qao Qiang and Dearlyn Fernandes for English grammar checking of the manuscript.

Author Contributions

No other contributions. Conceived and designed the experiments: XDY GHL. Performed the experiments: XDY XNZ. Analyzed the data: XDY. Contributed reagents/materials/analysis tools: XDY GHL. Wrote the paper: XDY AA.

References

  1. 1. Armas C, Padilla F, Pugnaire F, Jackson R (2010) Hydraulic lift and tolerance to salinity of semiarid species: consequences for species interactions. Oecologia 162: 11–21.
  2. 2. Haase P, Pugnaire FI, Fernández EM, Puigdefábregas J, Clark S, et al. (1996) An investigation of rooting depth of the semiarid shrub Retama sphaerocarpa (L.) Boiss. by labelling of ground water with a chemical tracer. Journal of Hydrology 177: 23–31.
  3. 3. Richards JH, Caldwell MM (1987) Hydraulic lift: substantial nocturnal water transport between soil layers by Artemisia tridentata roots. Oecologia 73: 486–489.
  4. 4. Caldwell MM, Dawson TE, Richards JH (1998) Hydraulic lift: consequences of water efflux from the roots of plants. Oecologia 113: 151–161.
  5. 5. Hacker SD, Bertness MD (1995) Morphological and physiological consequences of a positive plant interaction. Ecology 76: 2165–2175.
  6. 6. Vetterlein D, Marschner H (1993) Use of a microtensiometer technique to study hydraulic lift in a sandy soil planted with pearl millet (Pennisetum americanum [L.] Leeke). Plant and Soil 149: 275–282.
  7. 7. Filella I, Penuelas J (2003) Indications of hydraulic lift by Pinus halepensis and its effects on the water relations of neighbour shrubs. Biologia Plantarum 47: 209–214.
  8. 8. Franco A, Nobel P (1990) Influences of root distribution and growth on predicted water uptake and interspecific competition. Oecologia 82: 151–157.
  9. 9. Kurz-Besson C, Otieno D, do Vale RL, Siegwolf R, Schmidt M, et al. (2006) Hydraulic lift in cork oak trees in a savannah-type Mediterranean ecosystem and its contribution to the local water balance. Plant and Soil 282: 361–378.
  10. 10. Williams DG, Ehleringer JR (2000) Intra-and interspecific variation for summer precipitation use in pinyon-juniper woodlands. Ecological Monographs 70: 517–537.
  11. 11. Burgess SS, Adams MA, Turner NC, Ong CK (1998) The redistribution of soil water by tree root systems. Oecologia 115: 306–311.
  12. 12. Dawson TE (1993) Hydraulic lift and water use by plants: implications for water balance, performance and plant-plant interactions. Oecologia 95: 565–574.
  13. 13. Lee J-E, Oliveira RS, Dawson TE, Fung I (2005) Root functioning modifies seasonal climate. Proceedings of the National Academy of Sciences of the United States of America 102: 17576–17581.
  14. 14. Lehto T, Zwiazek JJ (2011) Ectomycorrhizas and water relations of trees: a review. Mycorrhiza 21: 71–90.
  15. 15. Neumann RB, Cardon ZG (2012) The magnitude of hydraulic redistribution by plant roots: a review and synthesis of empirical and modeling studies. New Phytologist 194: 337–352.
  16. 16. Prieto I, Martínez-Tillería K, Martínez-Manchego L, Montecinos S, Pugnaire FI, et al. (2010) Hydraulic lift through transpiration suppression in shrubs from two arid ecosystems: patterns and control mechanisms. Oecologia 163: 855–865.
  17. 17. Warren JM, Brooks JR, Dragila MI, Meinzer FC (2011) In situ separation of root hydraulic redistribution of soil water from liquid and vapor transport. Oecologia 166: 899–911.
  18. 18. Zou C, Barnes P, Archer S, McMurtry C (2005) Soil moisture redistribution as a mechanism of facilitation in savanna tree–shrub clusters. Oecologia 145: 32–40.
  19. 19. David TS, Pinto CA, Nadezhdina N, Kurz-Besson C, Henriques MO, et al. (2013) Root functioning, tree water use and hydraulic redistribution in Quercus suber trees: A modeling approach based on root sap flow. Forest Ecology and Management 307: 136–146.
  20. 20. Sardans J, Peñuelas J (2014) Hydraulic redistribution by plants and nutrient stoichiometry: Shifts under global change. Ecohydrology 7: 1–20.
  21. 21. Horton JL, Hart SC (1998) Hydraulic lift: a potentially important ecosystem process. Trends in Ecology & Evolution 13: 232–235.
  22. 22. Yang XD, Lv GH (2011) Establishment and analysis of Populus euphratica'root Hydraulic redistribution model. Chinese journal of Plant Ecology 35: 816–824 (in Chinese with English abstract).
  23. 23. Hao XM, Li WH, Guo B, Ma JX (2013) Simulation of the effect of root distribution on hydraulic redistribution in a desert riparian forest. Ecological research 28: 653–662.
  24. 24. Yu T, Feng Q, Si J, Xi H, Li Z, et al. (2013) Hydraulic redistribution of soil water by roots of two desert riparian phreatophytes in northwest China’s extremely arid region. Plant and soil 372: 297–308.
  25. 25. Ryel R, Caldwell M, Yoder C, Or D, Leffler A (2002) Hydraulic redistribution in a stand of Artemisia tridentata: evaluation of benefits to transpiration assessed with a simulation model. Oecologia 130: 173–184.
  26. 26. Dawson TE, Mambelli S, Plamboeck AH, Templer PH, Tu KP (2002) Stable isotopes in plant ecology. Annual review of ecology and systematics 33: 507–559.
  27. 27. Ehleringer J, Dawson T (1992) Water uptake by plants: perspectives from stable isotope composition. Plant, Cell & Environment 15: 1073–1082.
  28. 28. Ellsworth PZ, Williams DG (2007) Hydrogen isotope fractionation during water uptake by woody xerophytes. Plant and Soil 291: 93–107.
  29. 29. Zhao F, Jin HL (2011) Study on characteristics of groundwater and its impact on Populus euphratica along the banks of Aqikesu River. Journal of Arid Land Resources and Environment 8: 156–161 (in Chinese with English abstract).
  30. 30. Hamblin AP (1985) The influence of soil structure on water movement, crop root growth and water uptake. Advances in Agronomy 38: 95–158.
  31. 31. Jackson R, Canadell J, Ehleringer J, Mooney H, Sala O, et al. (1996) A global analysis of root distributions for terrestrial biomes. Oecologia 108: 389–411.
  32. 32. Li XR, Tan HJ, He MZ, Wang XP, Li XJ (2009) Patterns of shrub species richness and abundance in relation to environmental factors on the Alxa Plateau: Prerequisites for conserving shrub diversity in extreme arid desert regions. Science in China Series D: Earth Sciences 52: 669–680.
  33. 33. Xia Y, Moore DI, Collins SL, Muldavin EH (2010) Aboveground production and species richness of annuals in Chihuahuan Desert grassland and shrubland plant communities. Journal of arid environments 74: 378–385.
  34. 34. Allison GB, Hughes MW (1983) The use of natural tracers as indicators of soil-water movement in a temperate semi-arid region. Journal of Hydrology 60: 157–173.
  35. 35. King DA (1996) Allometry and life history of tropical trees. Journal of tropical ecology 12: 25–44.
  36. 36. Poorter L, Bongers F, Sterck FJ, Wöll H (2003) Architecture of 53 rain forest tree species differing in adult stature and shade tolerance. Ecology 84: 602–608.
  37. 37. Callaway RM (1992) Effect of shrubs on recruitment of Quercus douglasii and Quercus lobata in California. Ecology 73: 2118–2128.
  38. 38. Monteith JL (1965) Evaporation and environment. Symposia of the Society for Experimental Biology 19: 205–234.
  39. 39. Raz-Yaseef N, Rotenberg E, Yakir D (2010) Effects of spatial variations in soil evaporation caused by tree shading on water flux partitioning in a semi-arid pine forest. Agricultural and Forest Meteorology 150: 454–462.
  40. 40. Allison GB, Barnes CJ, Hughes MW (1983) The distribution of deuterium and 18O in dry soils 2. Experimental. Journal of Hydrology 64: 377–397.
  41. 41. Kim K, Lee X (2011) Isotopic enrichment of liquid water during evaporation from water surfaces. Journal of hydrology 399: 364–375.
  42. 42. Zhao L, Xiao H, Cheng G, Song Y, Zhao L, et al. (2008) A preliminary study of water sources of riparian plants in the lower reaches of the Heihe basin. Acta Geoscientica Sinica 29: 709–718.
  43. 43. Zhang JT (2004) Quantitive Ecology. Beijing: Science Press (in Chinese).
  44. 44. Numata M (1979) Methods for Ecological Study. Kokin Shou-in, Tokyo (in Japanese).
  45. 45. Barchuk A, Valiente-Banuet A, Díaz M (2005) Effect of shrubs and seasonal variability of rainfall on the establishment of Aspidosperma quebracho-blanco in two edaphically contrasting environments. Austral ecology 30: 695–705.
  46. 46. Belsky A, Amundson R, Duxbury J, Riha S, Ali A, et al. (1989) The effects of trees on their physical, chemical and biological environments in a semi-arid savanna in Kenya. Journal of Applied Ecology 26: 1005–1024.
  47. 47. Belsky AJ (1994) Influences of trees on savanna productivity: tests of shade, nutrients, and tree-grass competition. Ecology 75: 922–932.
  48. 48. Franco A, Nobel P (1989) Effect of nurse plants on the microhabitat and growth of cacti. The Journal of Ecology 77: 870–886.
  49. 49. Maestre FT, Bautista S, Cortina J (2003) Positive, negative, and net effects in grass-shrub interactions in Mediterranean semiarid grasslands. Ecology 84: 3186–3197.
  50. 50. Shumway SW (2000) Facilitative effects of a sand dune shrub on species growing beneath the shrub canopy. Oecologia 124: 138–148.
  51. 51. Huxman TE, Snyder KA, Tissue D, Leffler AJ, Ogle K, et al. (2004) Precipitation pulses and carbon fluxes in semiarid and arid ecosystems. Oecologia 141: 254–268.
  52. 52. Weltzin JF, Coughenour MB (1990) Savanna tree influence on understory vegetation and soil nutrients in northwestern Kenya. Journal of Vegetation Science 1: 325–334.
  53. 53. Rousset O, Lepart J (1999) Shrub facilitation of Quercus humilis regeneration in succession on calcareous grasslands. Journal of Vegetation Science 10: 493–502.
  54. 54. Armas C, Pugnaire FI (2005) Plant interactions govern population dynamics in a semi-arid plant community. Journal of Ecology 93: 978–989.
  55. 55. Jackson L, Strauss R, Firestone M, Bartolome J (1990) Influence of tree canopies on grassland productivity and nitrogen dynamics in deciduous oak savanna. Agriculture, Ecosystems & Environment 32: 89–105.
  56. 56. Reynolds JF, Virginia RA, Kemp PR, de Soyza AG, Tremmel DC (1999) Impact of drought on desert shrubs: effects of seasonality and degree of resource island development. Ecological Monographs 69: 69–106.
  57. 57. Schade JD, Hobbie SE (2005) Spatial and temporal variation in islands of fertility in the Sonoran Desert. Biogeochemistry 73: 541–553.
  58. 58. Segoli M, Ungar ED, Shachak M (2012) Fine-Scale Spatial Heterogeneity of Resource Modulation in Semi-Arid “Islands of Fertility”. Arid Land Research and Management 26: 344–354.
  59. 59. Walker LR, Thompson DB, Landau FH (2001) Experimental manipulations of fertile islands and nurse plant effects in the Mojave Desert, USA. Western North American Naturalist 61: 25–35.