Differences in the Soil Quality Index for Two Contrasting Mediterranean Landscapes in Southern Spain

: Soil quality indexes (SQIs) are very useful in assessing the status and edaphic health of soils. This is particularly the case in the Mediterranean area, where successive torrential rainfall episodes give rise to erosion and soil degradation processes; these are being exacerbated by the current climate crisis. The objective of this study was to analyze the soil quality in two contrasting Mediterranean watersheds in the province of Malaga (Spain): the middle and upper watersheds of the Rio Grande (sub-humid conditions) and the Benamargosa River (semi-arid conditions). Field soil sampling was carried out at representative sites, and the soils were subsequently analyzed for various edaphic properties in the laboratory. From the resulting data, the mean values have been grouped and reclassified, and, based on a multicriteria evaluation, an SQI for the study region was generated. The results show that there are major differences between the two watersheds, with optimal soil quality values being found in the Rio Grande watershed (very high soil quality— 34.26%), but more unfavorable values occurring throughout most of the Benamargosa River watershed (very low soil quality—63.33%). Thus, these results have been subjected to a validation process in the field.


Introduction
Drylands, defined as regions having an index of aridity (coefficient between rainfall: evapotranspiration) ranging from 0.05 to 0.65, cover approximately 5.2 billion ha worldwide and represent 40% of the global land surface [1]. There is largely consensus on the effects of climate change on dryland systems, including: (i) higher temperatures; (ii) an increase in the degree of aridity; and (iii) shifts in the seasonal rainfall regimes and a greater frequency of extreme events [2,3]. These changes will affect the size, frequency, intensity, and timing of rainfall events, which largely determine the structure and functioning of dryland ecosystems worldwide [3]. To unravel this complexity, there is a need to focus on understanding how biotic attributes interact with abiotic factors to ultimately drive ecosystem functioning [4,5] Climate change in Mediterranean areas is particularly serious, because the effects of anthropogenic activities (tillage on slopes, deforestation, and pasture production) exacerbate the problems of prolonged periods of drought, and intense and irregular rainfall [5][6][7]. These processes lead to reduced soil fertility and soil loss [8,9]. In the short term, it is expected that these systems will be subject to a decrease in soil organic matter because of a reduction in vegetation cover [10]. As a result, the soil clay content will decrease, causing a reduction in soil stability and the size of aggregates [5,11]. In the long term, reduced water holding capacity and permeability, and a higher probability of crust formation are expected [12,13], leading to a dramatic decrease in infiltration rates [13,14]. Consequently, the vegetation will be unable to recolonize in the system because of the absence of available water in the soil profile, and high rates of overland flow and sediment yield will result [8,11]. The seedbank and nutrient content will decline, and a second cycle of decreasing soil organic matter content will be initiated. These positive feedbacks may not be spontaneously reversible, so, when certain thresholds are exceeded, restoration activities will need to be carried out.
In this context, investigating current and future effects of climate change on the regional scale is essential to understanding potential impacts in Mediterranean ecosystems. The monitoring of soil quality parameters will help clarify and raise awareness of the causes and effects of climate change, and the required responses [15]. This is because soil quality is a measure of the capacity of a soil to function within ecosystem and land-use boundaries, sustain productivity, maintain environmental quality, and promote plant and animal health [16,17]. Soil quality indexes are measurement tools providing information about soil properties, processes, and characteristics [15]. According to the purpose of the study, a soil quality index (SQI) must be different; this entails a careful design prior to its formulation. An SQI can provide very diverse information, being a key to determine the level of soil degradation, to evaluate the general quality of an agricultural soil, to identify areas with a higher production potential or, on the other hand, to determine less suitable areas in terms of production [18]. In this sense, the development of a set of readily measurable indicators that describe the condition and health of degraded areas is essential to the protection and sustainable use of terrestrial water resources. Thus, a good set of soil quality indicators should reflect how biotic attributes interact with abiotic factors [19]. The capacity of a soil to function is reflected in measurements of its physical, chemical, and biological properties [11,13,15] and soil quality indicators should reflect these properties and their interactions in soil processes.
Soil quality indicators can be measured over various periods to assess the effects of management on soil functioning. Various soil properties have been used as soil quality indicators [20]. The soil physical quality is associated with the efficient use of water, nutrients, and pesticides [21]. Chemical indicators reflect soil-plant relationships, water quality, soil buffering capacity, and water and nutrient availability [22]. Biological indicators integrate many factors that can affect soil quality, including macroinvertebrate abundance and byproducts [23]. Soil enzyme activities enable assessment of the degree of soil degradation because they are early and sensitive indicators of soil ecological stress [21]; they also reflect microbial activity, which is responsible for producing enzymes involved in many soil functions [24]. However, monitoring soil quality is challenging because of the complexity of soil processes, and the spatial and temporal variability of soil properties [25].
The combination of multicriteria assessment tools (EMCs) and GIS technologies has provided a very useful approach to assessing the agricultural suitability of particular areas and should prove useful for Mediterranean areas subject to climate change effects [26][27]. Kumar and Jhariya [28] used this approach in India to assess the suitability of soils for agriculture. These tools enable the evaluation of various alternatives [29], and identification of the relative importance of selected variables through a decision-making process [30,31]. Thus, these methods have added a degree of objectivity to a process characterized by subjectivity [32] and advanced the development of tools including spatial and geographical analyses [33].
The major objectives of this study were: (i) to develop an SQI for the Mediterranean area of southern Spain, specifically for two watersheds representing contrasting climatic conditions (subhumid and semi-arid); and (ii) to evaluate the quality of the soil in each watershed, identifying landscape units of higher and lower quality, and differentiating areas most susceptible to the effects of climate change.

Study Areas
Two hydrographic watersheds representative of the mid-mountain landscape in a Mediterranean coastal strip in southern Spain were selected, one on each side of the degradation threshold observed by Ruiz and Romero [34] (500-600 mm). On the one hand, the Río Grande watershed (GR; area: 38.42 km 2 ; annual rainfall: 719.03 mm), which has a subhumid Mediterranean climate and, on the other hand, the Benamargosa River watershed (BE; area: 181.23 km 2 ; annual rainfall: 562.61 mm), which has a dry semiarid Mediterranean climate ( Figure 1).

Soil Sampling
Based on lithological and land-use mapping, the study area was separated into differing landscape units having acid, neutral, or basic sedimentary lithologies, and land uses of either cultivation or natural vegetation [35]. A total of 361 surface soil samples (0-10 cm depth) were collected from sites distributed homogeneously throughout the area, among which 170 were from the Río Grande watershed and 191 were from the Benamargosa River watershed. In the laboratory, the soil samples were air dried and sieved, and fractions having particle sizes < 2 mm were retained of analysis.
The texture was evaluated using diffraction equipment (Coulter LS 230), following the pretreatment method of Marañés et al. [36]. SOC was analyzed using the calcination method at 550 °C [37]. AWC was measured based on the difference between the field capacity (FC) and the permanent wilting percentage (PWP), using a pressure plate extractor [38]. AGS was determined using the wet sieving method [39] for aggregates of 0.053, 0.125, 0.250, 0.5, 1, and 2 mm. Hydrophobicity was analyzed using the ethanol percentage test (EFA) [40], based on the water repellency intensity intervals described by Doerr et al. [41]. EC was analyzed from the saturation extract of a sample paste prepared using a 1:1 ratio with distilled water [42].
For the undisturbed soil samples, BD was determined using gravimetric analysis following drying in an oven at 105 °C for 24 h [43]. Permeability was measured using saturated soil in a permeameter (Eijkelkamp, model 09.02), following the protocol described by the manufacturer and applying the Darcy equation [44].

Other Factors Influencing the Erosion Rate Calculated Using the RUSLE Model
Other soil characteristics analyzed and having potential as degradation indicators included: (i) the slope percentage; (ii) the erodibility factor (K factor) for the revised soil loss equation (RUSLE); and (iii) the plant cover factor (C).
The slopes were obtained from a digital elevation model (DEM) using a mesh pitch of 5 m. The K factor, which is related to various edaphic parameters, was calculated using the following equation [45]: where M is the particle size, calculated as (% silt + % very fine sand) × (100 − % clay); OM is the soil organic matter (%), obtained from SOC; S is the soil structure code (1 = very fine granular, 2 = fine granular, 3 = coarse granular, 4 = massive); and P is the soil permeability class, based on the criteria of Reynolds et al. [46] (1 = fast, 2 = moderate to fast, 3 = moderate, 4 = low to moderate, 5 = low, 6 = very low).
Calculation of factor C was carried out using the normalized vegetation index (NDVI) for a Landsat 8 image obtained from NASA and atmosphere corrected (date: 14 September2017; scene: 201/34) in ERDAS Imagine 2015 software. The NDVI result was converted to values of factor C using the formula of Van der Knijff et al. [47]: where α and β have values of 2 and 1, respectively.

Statistical Analysis
Following the analysis of soil properties and the calculation of degradation indicators, a principal component analysis (PCA) was performed to select those properties/indicators that best explained the landscape dynamics in each watershed [48] and were therefore likely to be the most sensitive descriptors of soil quality [49,50]. This analysis was carried out using SPSS version 25 (corporate license of the University of Malaga) for Windows [51].

SQI Formulation
To formulate the SQI, the following operations were carried out consecutively: 1. The properties and factors used to determine the SQI were selected based on the PCA and an expert opinion system [50].

2.
These were reclassified on a scale of 1 to 3, with value 1 representing poor quality, 2 representing medium quality, and 3 representing high quality (Table 1). In addition, these were adjusted to both statistical criteria (quantiles) and theoretical classifications [52]. In this reclassification, the values for both watersheds were considered, to enable formulation that facilitated comparison. 3. The various properties and factors were grouped into three clusters according to their characteristics (water, physical, and biological or organic), groups that would compose the final SQI, and those that could be defined as soil quality sub-indices. 4. A multi-criteria evaluation was carried out individually in each group using a weighted summation (e.g. [27,28,31,34]). For this purpose, each component was given a specific weighting (priority vector), based on the experience of several experts in soil analysis [50] using a decision matrix. The Saaty method, analytical hierarchies, or peer comparison were used to assign weights. This approach is widely used in this type of study [30], and consists of elaborating a square matrix in which the number of rows and columns is defined by the number of variables to be weighted. To validate the method, the value of the consistency of judgment must be <0.1 [30]. In short, the decision matrix is an analytical hierarchy technique (AHP), through which relative weights are assigned to a group of factors in the multi-criteria assessment [27]. 5. The procedure was repeated to achieve the final SQI using the steps described above, but with a reclassification process based on a scale of 1 to 5 (Table 1).   Based on the formulation and to achieve soil quality results for the study area, the SQI equation was developed in ArcGis software version 10.6 (Corporate license of the University of Malaga. The results were reclassified in five classes, based on statistical quantiles (1: very low; 2: low; 3: medium; 4: high; 5: very high). In addition, the equations obtained in each of the clusters were used to evaluate the quality of the soil from each of the perspectives considered (water, physical, and organic).
Field work was undertaken to validate the SQI analysis results.

Soil Quality Index (SQI)
Soils are complex ecosystems within which various factors interact, so it is necessary to evaluate a variety of indicators to determine soil quality [53]. Table 2 shows the indicators that were identified based on the methodology described and selected for formulation of the SQI for the study area; these are grouped according to their relevance to water, physical, or organic factors. Table 2. Soil quality properties and indicators grouped.

Water Factor Physical Factor Organic Factor
Permeability, the percentage of gravel and sand, hydrophobicity, and the AWC were the indicators chosen to evaluate water factors. The slope, soil erodibility value (K Factor, RUSLE), structural stability, and bulk density were the indicators chosen as relevant to physical factors. Indicators considered relevant to organic factors included the organic carbon content of the soil, the vegetation factor (factor C, RUSLE), and the electrical conductivity. Many of these indicators have been used to evaluate soil quality in studies carried out in various areas worldwide [52,[54][55][56]. Their application to the Mediterranean area is evident from their known relevance to ecogeomorphological processes, and more generally in landscape dynamics [48].
Subsequently, based on the criteria of several experts [50] each factor was given a weighting in the weight matrix. Thus, in the final SQI formula, the organic factor had the greatest degree of importance and was given a weighting factor of 0.6. The relevance of this factor was determined by the strong effect of its indicators on the other factors comprising the SQI [52]. The water and physical factors were each given a weighting of 0.2. These factors have been combined into a single factor in other soil quality studies [53,57]. Thus, the overall equation for the SQI was: where W is the water factor, P is the physical factor, and O is the organic factor.
The calculation of each of the components in this formula followed the same procedure for the calculation of the final formula. Thus, for the water factor, AWC had the highest weighting factor (0.393), followed by permeability (0.314), sand content (0.18), gravel content (0.104), and hydrophobicity (0.04). Although all these properties are fundamental, AWC has a key role in the landscape dynamics, especially in semiarid areas [48]. Soil permeability is also a key indicator, as it influences many other characteristics and is a determinant of plant growth and degradation processes [58]. Therefore, the equation for assessing soil quality from a water (W) perspective was formulated as follows: where PE is the permeability, G is gravel, S is sand, H is the hydrophobicity, and AWC is the available water content. Physical characteristics are central to soil quality, particularly as these are difficult to modify [59]. For the physical factor, erodibility (RUSLE) was weighted as having the greatest importance (0.5579), because this indicator combines various properties. The next most important was slope (0.2633), which is fundamental in erosion processes and landscape dynamics in the Mediterranean area, and particularly in the study area [48]. The AGS (0.1219) and BD (0.0569) were assigned lower levels of importance. Therefore, the equation for assessing soil quality from a physical (P) perspective was formulated as follows: where SL is the slope, K is the K factor (RUSLE), AGS is the structural stability, and BD is the bulk density.
For the third factor (organic: O) comprising the SQI, equal weighting (0.4286) was given to SOC and the C factor (RUSLE). SOC is considered a key indicator of soil condition, as it has a strong influence on other soil properties [60]. For example, a decrease in SOC has a marked negative impact on all physical and hydrological characteristics of the soil, resulting in greater sensitivity to degradation processes, thereby decreasing soil quality [52]. The EC indicator was given a weighting of 0.1429. Therefore, the equation for assessing soil quality from an organic (O) perspective was formulated as follows: where SOC is the soil organic carbon, C is the C factor (RUSLE), and EC is the electrical conductivity. In this way, the SQI and specific sub-indices have been formulated, useful for evaluating the specific characteristics of a given area. In addition, the inclusion of two contrasting watersheds suggests that the formula can be extrapolated to the entire rainfall gradient studied by Ruiz-Sinoga and Romero-Díaz [34] in the Mediterranean section of southern Spain.

Results and Discussion
The evaluation and application of the method described in this study was used to identify the areas having better soil quality and those requiring more attention because of their susceptibility to degradation. Those areas having soil providing optimal conditions for plant development and lower susceptibility to erosive processes were rated as being of higher quality.
The equation related to the water factor was applied to both watersheds and used to generate a soil quality map based on characteristics related to water (Figure 2). This shows that the GR watershed had higher quality soil (soil health) than the BE watershed; this was mainly related to differing lithologies and the generally greater degree of vegetation cover in the GR watershed than the BE watershed ( Figure 1). The highest quality areas were associated with basic sedimentary lithologies and areas having the most vegetation [48]. Thus, the results obtained identify the importance of the vegetation cover in the hydrological state of the soil, where the presence of more vegetation is related to higher quality [61]. In contrast, the poorer quality areas were those having bare soil and where cropping has been abandoned, particularly the central and southern BE watershed areas. The abandonment of cropping often favors erosion processes [62], especially in the most arid areas, where the vegetation cover does not regenerate and water retention is more difficult [63], resulting in greater soil degradation and lower quality soils.
Acid lithologies directly affect soil fertility, and affected soils are generally less productive and of poorer quality [64]. In this study, the lowest-quality soils corresponded to acid lithologies and low permeability levels. Poor permeability results in low levels of infiltration and poor retention of water in the soil, and enhanced surface runoff processes [65]; in some areas, the slope factor was an important additional factor.
The equation formulated to assess soil quality from a physical perspective was applied to both watersheds ( Figure 3). The results also show higher soil quality in the GR watershed than the BE watershed, although, for both watersheds, the areas of higher edaphic quality corresponded to areas of natural vegetation and basic sedimentary lithology. The K, BD, and AGS parameters reflect the role of vegetation cover, with more vegetation resulting in higher AGS values, lower BD values, and consequently less erodibility [66]. The best soil quality in the GR watershed was in the northern and southwest areas. In contrast, the poorest quality was in the southeast of the watershed, consistent with the occurrence there of large areas of bare soil [48]. In the BE watershed, the best soil quality was limited to the northernmost area, while, in the areas near Riogordo, the soil quality was lower and coincided with very high values of erodibility associated with the presence of agricultural areas (olive groves, fruit trees, and other tree crops) [35]. In relation to organic or biological factors (Figure 4), the results generally show low soil quality in both watersheds, although the values were lower in the BE watershed, which was mostly of very poor quality. The GR watershed includes great spatial variability, with substantial land, forest, and agricultural use diversity in the northernmost and southwestern areas associated with the best soil quality, and lowest soil quality corresponding to the areas most devoid of vegetation, predominantly in the southeast and west of Yunquera. These contrasts are consistent with the suggestion by Sillero-Medina et al. [48] that the GR watershed reflects a double evolution; areas having positive trends in the quantity of biomass had greater SOC and factor C (areas of higher soil quality), whereas other areas where vegetation cover has been lost (and consequently there has been an increase in the area of sealed and unprotected surfaces) had low and very low soil quality. An increase in SOC as a result of revegetation has been demonstrated in several studies in the Mediterranean basin [67,68], along with a loss of organic quality in areas occupied by rainfed crops. In contrast, the BE watershed had generally very low soil quality throughout, except in the northern fringe and in some scattered areas in the southern half. As in the GR watershed, a negative trend in terms of biomass content was evident throughout most of the BE watershed, corresponding to a loss of SOC and soil quality, although moderate soil quality areas occur, corresponding to small areas of natural vegetation (wooded areas and sclerophyll vegetation) [35]. Analysis of the SQI in the study area showed quite contrasting results, but comparable to the ecogeomorphological or landscape dynamics identified in recent years in the same area [35,48,69] ( Figure 5). The SQI was very high in 34.26% of the GR watershed area (Table 3) because of the high index values for the water, physical, and organic factors in the north and west of the basin. However, there were low SQI areas in 24.78% of the watershed, corresponding to agricultural uses and the associated low values for the organic component.  For the BE watershed, where climatic indicators show greater aridity, there were very heterogeneous results. Only 2.51% of the area had high-quality soils (Table 3), corresponding to small areas of sclerophyll vegetation where soil−water−plant relationships occur throughout the year [35]. Extremely low-quality areas occupied 63.33% of the total area of the watershed, corresponding to low values for the organic factor associated with the predominant agricultural uses. However, the low quality was exacerbated in the southern sector by water limitations, and in the northern and eastern areas of Riogordo by high levels of soil erosion.
The results obtained reflect trends observed in the two watersheds. In the GR watershed, areas of high soil quality typically correspond to areas where revegetation processes have occurred from 1956 to the present [35], facilitated by the high levels of annual rainfall [70] associated with the subhumid Mediterranean climate in this area. This climatic factor has clearly been essential to the increase in biomass, which leads to a greater supply of organic matter to the soil [71]. Field work for validation of the SQI ( Figure 6) showed evidence for these processes in the GR watershed, which has extensive areas of fertile soil and few areas subject to erosive processes. In contrast, no increase in biomass has occurred in recent decades in the BE watershed [35]. The dry Mediterranean climate of this area reflects its greater fragility because of the low availability of water [34]. Thus, factors related to water largely control the landscape dynamics in the BE watershed [48], and result in low edaphic quality, especially in the southern half.
The field work enabled the validation of the SQI formula proposed for the Mediterranean area, with areas classified as poor quality according to the SQI having compact soils and a shallow horizon, and sparse and poor vegetation cover ( Figure 6).

Conclusions
As major findings of the study, the indicators selected for the formulation of the SQI reflected the current landscape dynamics of the area of study, and field work validated the state of the soil as indicated by the SQI. Thus, this index provides a useful tool for assessing the quality and health of soil in the Mediterranean area in a specific time frame. Furthermore, in the study area, SQI reproduced the evolution of vegetation cover in the GR watershed, where, high soil quality was common as a result of the optimal values for organic factors in the soil. On the other hand, the SQI for the BE watershed highlighted the importance of water, the relative absence of which was manifest in this area having lower soil quality than in the GR watershed. This study clearly demonstrates the need to take specific measures to remediate areas of poor soil quality by designing and implementing strategies that favor and improve its quality. In this regard, preserving seasonal vegetation, building infrastructures to mitigate erosion processes and reducing the use of fertilizer may be some of these actions.