Soil Degradation and Restoration in Southwestern Saudi Arabia through Investigation of Soil Physiochemical Characteristics and Nutrient Status as Indicators

: Soil degradation is among the major global concerns resulting in declined soil fertility, loss of soil organic carbon (SOM) and nutrients, and reduced pollinator visitations. The current study was performed to explore soil quality and fertility after restoration in southwestern Saudi Arabia, as new plantation could alter soil properties. A total of 78 soil samples were collected from restored and control (without any restoration) areas from Al-Jenebeen (AJ), Queen Rearing Center (QRC), and Shekiran (SK) from depths of 0–60 cm. Results exhibited that sandy loam was the most dominant textural class in all the studied sites (~60%), followed by sandy clay loam. All the soils were slightly alkaline and nonsaline. Due to restoration practices, the pH was increased in AJ and QRC, while decreased in SK areas. With restoration, EC in AJ and QRC sites decreased, but increased in SK. Restoration practices resulted in reduced SOM in AJ and QRC, while increased in SK. Increased SOM in SK may improve ﬂoral traits after restoration. Overall, restored SK possessed higher SOM and nutrients with reduced pH, and, hence, could be a potential source for honeybee ﬂora. Further in depth analyses of restoration activities are needed to explore the long term effects on land rehabilitation.


Introduction
Soil/forest degradation is one of the major problems of agricultural soils worldwide [1]. Global soil resources are at risk of degradation due to anthropogenic and natural factors, consequently resulting in lower crop yields [2]. According to some estimates, 33% of the world land surface has been degraded, resulting in a decline of about 60% of ecosystem services [3,4]. Soil/forest degradation could be elicited by some chemical, physical, biological, and/or ecological processes, which subsequently deteriorate soil quality and fertility [5]. Therefore, soil quality is of significant importance for human health and the environment, due to its significant implication for ecosystems. Consequently, the degradation of soil is disturbing the natural ecological balance, economic growth, and ecosystem sustainability. Therefore, measures must be taken to protect soil quality and restore the degraded lands to enhance ecosystem services such as food, fiber, water filtration, and elemental cycling.
Soil degradation can be evaluated through investigating the chemical, physical, biological, and hydrological characteristics of soil [6,7]. Variations to these properties could disturb the natural ecosystem balance and soil health. The deterioration of soil structure, aggregates, and pore geometry could generate crusts and compaction, consequently enhancing soil erosion, and, thus, are referred to as physical degradation. On the other hand, soil salinization, acidification, toxification, and nutrient loss could reduce soil fertility and

Study Site Description
The study was carried out in forests of southwest Saudi Arabia (Al-baha Region, Baljurashi district). The landscape constitutes the remainder of the forest stock of the country [14]. Due to the geographical diversity, this land feature has diverse climates, thus favoring the growth and flowering of greatly diversified bee plant genotypes rich in nectar and pollen, including Acacia species. As a result, most of the beekeeping activities of the country are concentrated in this region. The area is categorized as being mid to high land physiographic and climatic conditions. The humidity ranges from 52-67%, with rainfall from 229-581 mm/annum. The mean annual temperature is 22.9 • C. The major land use of the area is characterized by rangeland where free grazing and browsing is a common practice. The rangeland is also comprised of fallow land deserted decades ago.
For current study, 3 areas (Al-Jenebeen (AJ), Queen Rearing Center (QRC), and Shekiran (SK)), where restoration activities have already been practiced, were selected from the study site. The AJ and QRC are relatively flat areas, while the SK is more of hilly landscape. AJ is known for open browsing/grazing land, whereas the QRC and SK possess limited browsing/grazing land in the area despite relatively good plant cover. Similar weather prevails in QRC and SK areas, while AJ differs from these two as it receives less rainfall and is relatively warmer.

Restoration Activities
Despite its relatively good vegetation coverage, the area is severely degraded and only relict woodland patches exist. It was seen that AJ area was relatively more degraded in terms of vegetation cover and composition as compared to QRC and SK. These situations are believed to easily motivate stakeholders in the rehabilitation of the vegetation (apicultural landscapes) of the area, for both environmental and economic reasons. Therefore, some restoration activities have been conducted in the area already. These restoration activities include fencing; plantation of local plants, especially acacia species; and installation of drip irrigation systems. The fencing was developed to avoid interferences, trampling, and overgrazing of new sprouts, while plantation of new plants and drip irrigation installation were performed to enhance vegetation cover.

Site Profiling and Soil Samples Collection
The soil samples were taken from both restored and control sites located in study areas, i.e., AJ, QRC, and SK. From both groups, 3 soil profiles were dug and the samples were collected. Soil profiles were created on different localities in the study areas and samples were collected from various depths, i.e., 0-20 cm, 20-40 cm, and 40-60 cm. Additionally, some surface and composite samples were also collected to increase the possibility of analyzing the samples from different angles. Composite samples were created from each soil profile layer for both treatment groups in each site. In this way, a total of 78 samples were collected from all studied areas, comprising of different land use types, soil depths, and localities, as shown in Table 1.

Soil Samples Processing and Analyses
The collected soil samples were brought to the laboratory, air dried, ground, and passed through 2 mm screen. Thereafter, these samples were subjected to various soil analyses.

Soil Physiochemical Analyses
The pH of the soil was determined in a 1:1 (w/v) ratio suspension of soil to water by using a portable pH meter (pH 315i, WTW, Germany). Likewise, the filtrate of 1:1 suspension was used to analyze soil electrical conductivity (EC) by using a conductivity meter (EC meter: 4510, Jenway, UK). Cations and anions of the soil were measured by using the standard procedures, as reported earlier by [15]. Soil particle size distribution was determined by using the hydrometer method, while the texture was determined with the help of United States Department of Agriculture's textural triangle for soil taxonomy [16]. The soils collected from the study area belong to lithosols and yermosols types. The contents of calcite (CaCO 3 ) in collected samples were analyzed through calcimeter method [17]. Briefly, 2.0 g of soil was reacted with 0.1 N hydrochloric acid (HCl) under an airtight environment and the evolved CO 2 was measured. Then, calcite percentage was determined through comparing the emission of CO 2 from the sample with that of pure CaCO 3 . Soil organic matter was detected by following Walkley and Black (1934) method [18]. Briefly, 0.5 g soil was taken in round neck flask. Then, 10 mL of 1 N potassium dichromate solution was added, followed by 20 mL concentrated sulfuric acid. Sample was allowed to stand for 30 min. Later, 200 mL of distilled water was added to the sample followed by 3-4 drops of diphenylamine indicator. Sample was titrated with 0.5 M ferrous ammonium sulfate solution until the color changed from violet-blue to reddish brown. Additionally, a blank sample was run without soil sample.

Available Nutrients Analyses
Plant available phosphorus (P) and micronutrients, i.e., copper (Cu), iron (Fe), zinc (Zn), and manganese (Mn), in soil were extracted using AB-DTPA (ammonium bicarbonatediethylenetriaminepentaacetic acid) extraction method [19]. Briefly, a mixture of 1 M ammonium bicarbonate and 0.005 M DTPA with pH of 7.6 was used to extract P and micronutrients through 1:2 soil-AB-DTPA (w/v ratio) suspension. The concentration of K in the soil samples was analyzed by using flame photometer. The concentration of P in AB-DTPA extract was measured through colorimetry method by using UV/VIS spectrophotometer (Lambda EZ 150, PerkinElmer, Norwalk, CT, USA). The contents of micronutrients in AB-DTPA extract were determined by using Inductivity coupled plasma optical emission spectrophotometer (ICP-OES, PerkinElmer Optima 4300 DV, Akron, OH, USA).

Data Analyses and Statistics
The soil analyses data were statistically analyzed by using Microsoft Excel and Statistics 8.01 program. Descriptive statistics was used to calculate minimum, maximum, mean, skewness, kurtosis, and coefficient of variation (CV) of the data. Pearson correlations were calculated to explore the relation of various soil properties and nutrients concentrations with each other.

Soil Texture
The variations in soil texture of the different soil samples collected from the control and restored areas of the studied sites are shown in Figure 1. The results exhibited that sandy loam was the most dominant textural class in all the studied sites (~60%), followed by sandy clay loam. Overall, QRC has more samples in the sandy loam textural class, followed by SK and AJ. The loamy sand class was present in QRC-C, QRC-R, and SK-C, while absent in other collected samples.  Likewise, loam can be seen only in QRC-R, AJ-C, and AJ-R, whereas clay loam was present only in QRC-C and AJ-R. It was interesting to notice that the proportion of sandy loam soils was higher in restored areas as compared to the control areas. The restored areas of QRC showed the occurrence of loam soil, which was not present in the control areas. Likewise, clay loam soils were seen in the control of QRC, and absent in its restored areas. The control areas of SK had about 16% samples of loamy sand, which disappeared in restored areas. Similarly, clay loam soils were seen in restored areas of AJ, while these were absent in AJ-C. Therefore, variations in control and restored areas evidenced the effects of restoration efforts on the physical properties of the soils in the studied area. Owing to the significant importance of soil texture, various researchers have used it as an indicator for assessing soil quality [20,21]. Various agricultural practices, especially tillage and plowing, could affect the texture of soils. Likewise, natural processes, as well as irrigation, could move the clays downward and may result in their accumulation in deep soil horizons, subsequently changing the proportions of sand, silt, and clay. Therefore, soil texture is an important parameter to investigate soil type and quality [1,22]. The predominance of sand based texture indicated lower water holding capacity, poor soil structure, and lower nutrient retention. QRC-C and AJ-R possess relatively higher contents of clay, indicating a slightly better soil structure as compared to the rest of the soil types. Therefore, these changes in the distribution of silt, clay, and sand fractions, along with changing the land-use type and locality, indicated the difference in erosion and sedimentation rates. Likewise, loam can be seen only in QRC-R, AJ-C, and AJ-R, whereas clay loam was present only in QRC-C and AJ-R. It was interesting to notice that the proportion of sandy loam soils was higher in restored areas as compared to the control areas. The restored areas of QRC showed the occurrence of loam soil, which was not present in the control areas. Likewise, clay loam soils were seen in the control of QRC, and absent in its restored areas. The control areas of SK had about 16% samples of loamy sand, which disappeared in restored areas. Similarly, clay loam soils were seen in restored areas of AJ, while these were absent in AJ-C. Therefore, variations in control and restored areas evidenced the effects of restoration efforts on the physical properties of the soils in the studied area. Owing to the significant importance of soil texture, various researchers have used it as an indicator for assessing soil quality [20,21]. Various agricultural practices, especially tillage and plowing, could affect the texture of soils. Likewise, natural processes, as well as irrigation, could move the clays downward and may result in their accumulation in deep soil horizons, subsequently changing the proportions of sand, silt, and clay. Therefore, soil texture is an important parameter to investigate soil type and quality [1,22]. The predominance of sand based texture indicated lower water holding capacity, poor soil structure, and lower nutrient retention. QRC-C and AJ-R possess relatively higher contents of clay, indicating a slightly better soil structure as compared to the rest of the soil types. Therefore, these Sustainability 2021, 13, 9169 6 of 19 changes in the distribution of silt, clay, and sand fractions, along with changing the land-use type and locality, indicated the difference in erosion and sedimentation rates.

Soil pH and EC
Soil pH plays a critical role in the dissolution and availability of nutrients as well as for proper microbial activities in soil. Similarly, soil EC is an important factor for plant nutrient availability and optimum crop growth. Therefore, soil pH and EC are considered important indicators to assess the extent of soil quality. The descriptive statistical analyses for pH and EC of the collected soil samples are shown in Table 2. It can be seen that all the soils were slightly alkaline, with a mean pH range of 7.74 to 8.15. Overall, the mean pH values of AJ were higher (8.07-8.15), followed by SK (7.81-8.01) and QRC (7.74-7.99). Results showed that means increased from 8.07 in the control to 8.15 in restored areas and 7.74 in the control to 7.99 in restored areas in AJ and QRC, respectively, whereas, it decreased from 8.01 in the control to 7.81 in restored areas in SK. The increment in soil pH due to restoration processes could be due to the release of saline products by the plant's branches and leaves, as more plants were grown during restoration [23]. Additionally, the recycling of some organic components during the restoration process might have enhanced the soil pH. Contrarily, the pH of restored areas located in SK sites decreased to 7.81 from 8.01 in the control. This decrease in pH could be caused by the addition and mineralization of organic compounds due to restoration activities [24]. This reduction in pH in SK areas after restoration could help in enhancing vegetation growth, which, in turn, could increase floral resources for honeybees. Furthermore, the decrease in pH could be owing to the uptake of exchangeable cations by plant or microorganisms in soil. The degree of variability, as indicated by CV values, was in the range of 1.99 to 3.75. All the pH data was well skewed with lower kurtosis (−1.438-−0.041), indicating a normal distribution. The differences in pH values were statistically significant, except for QRC-R and SK-C which were nonsignificantly different. The pH for AJ-R was significantly higher (8.15) as compared to all the other samples. Similarly, significant differences were also seen in EC results, where AJ-C showed the highest value (0.45 dS m −1 ).
The influence of soil depth on variations in soil pH can be seen in Figure 2A,C,E. Overall, the mean pH values of restored areas were higher than that of the controls for all three sites. However, this was the opposite in the topsoil of QRC and SK, where restored areas had lower pH values than the control areas. The trend for distribution of the soil pH with depth was not uniform. For instance, the mean pH values increased with increasing the depth in AJ-C, while it decreased with depth in QRC-C and SK-C. Meanwhile, this was exactly the opposite in restored areas, where mean pH values decreased with depth in AJ-R, and increased in QRC-R and SK-R. Similar contrasting results were also reported by different researchers. For example, a decrease in soil pH with an increase in soil depth was previously reported by Shukla et al. [25], whereas Zhang et al. [26] reported an increase in soil pH with an increase in the depth, suggesting that this could be due to the addition of organic amendments in the soil. Overall, the results indicated that the effects of soil depth on variations in soil pH were not significant. Table 2 showed that the mean EC values for all the soil samples were in the range of 0.34 to 0.45 dS m −1 , suggesting that EC for all the soil samples was below salinity limits, i.e., 4 dS m −1 [27]. Overall, the samples collected from AJ sites had higher EC values, followed by QRC, and SK. The results exhibited that the EC of the AJ and QRC sites reduced after restoration activities, from 0.45 to 0.36 dS m −1 and 0.43 to 0.38 dS m −1 , respectively, whereas, it increased in the case of SK, from 0.34 to 0.40 dS m −1 . The increase in soil EC could be the result of adding organic matter during restoration activities, while the reduction in EC clearly indicated the significant role of plantation on soil quality [28]. The values of the skewness and kurtosis showed that the distribution was not normal. Figure 2B,D,F shows variations in mean EC with soil depth. The EC values reduced with an increase in soil depth in AJ-C, while increasing with an increase in soil depth in QRC-C and SK-C. This trend was opposite in restored areas, where EC increased with soil depth in the case of AJ-R, and decreased with depth in QRC-R and SK-R. Bezborodov et al. [29] stated that EC increases with soil depth due to the presence of salts. Therefore, the distribution and extent of soil pH and EC can effectively be used as indicators for assessing soil degradation and restoration. Soil organic matter (SOM) significantly influences the chemical, physical, and biological characteristics of soils [30]. It has been well documented that the depletion of SOM as a result of extensive agricultural practices has subsequently resulted in soil degradation [31,32]. Therefore, SOM is considered as one of the most promising and sensitive factors in assessing soil quality and the extent of its degradation. The descriptive statistical analyses for SOM for the samples collected from selected localities are shown in Table 3. Overall, the mean values of the contents of SOM were lower than 1.5% in all the locations. The samples collected from SK sites possessed higher SOM (0.13-2.56%), as compared to AJ (0.25-2.19%), and QRC (0.13-1.89%). It was noticed that the restoration practices resulted in reduced SOM in AJ (1.27% in AJ-C to 1.02% in AJ-R) and QRC (0.88% in QRC-C to 0.80% in QRC-R), while it increased with restoration practices in SK (1.16% in SK-C to 1.40% in SK-R). This data showed a higher variability, as shown with larger CV values (27.24-68.40). The skewness of the data was in the range of −0.316 to 0.244, while kurtosis was −1.326 to −0.304, indicating normality in the distribution of the data. Further, the changes in the contents of SOM with soil depth are shown in Figure 3A,C,E. The variations in SOM contents with soil depth were inconsistent. For instance, the mean SOM contents increased with an increase in soil depth in AJ-C and SK-R, while reducing with soil depth in the rest of the studied soil profiles. Interestingly, the topsoil of SK (both restored and the control) and AJ-C showed relatively lower SOM contents.   [27]. Overall, the samples collected from AJ sites had higher EC va lowed by QRC, and SK. The results exhibited that the EC of the AJ and QRC sites after restoration activities, from 0.45 to 0.36 dS m −1 and 0.43 to 0.38 dS m −1 , resp whereas, it increased in the case of SK, from 0.34 to 0.40 dS m −1 . The increase in could be the result of adding organic matter during restoration activities, while th tion in EC clearly indicated the significant role of plantation on soil quality [28]. Th of the skewness and kurtosis showed that the distribution was not normal. Figur shows variations in mean EC with soil depth. The EC values reduced with an in soil depth in AJ-C, while increasing with an increase in soil depth in QRC-C an This trend was opposite in restored areas, where EC increased with soil depth in of AJ-R, and decreased with depth in QRC-R and SK-R. Bezborodov et al. [29] st EC increases with soil depth due to the presence of salts. Therefore, the distribu The variations in SOM of the collected soil samples suggested that restoration activities had positive impacts on soil rehabilitation in SK sites, as indicated by increased SOM contents. Contrarily, the SOM contents of AJ and QRC sites reduced as a result of restoration activities. The loss of SOM during restoration activities could be due to higher sand fractions. Generally, the SOM associated with clay fractions is more resistant to degradation. However, our study demonstrated that sandy loam was the most dominant textural class for all the collected samples, indicating a higher portion of sand [33]. Kalinina et al. [34] suggested that the loss of SOM could also be due to higher humus rich arable soils, texture, and mowing. To further understand this, the proportions of soil organic carbon (SOC), according to the soil evaluation criteria, are presented in Figure 4. It can be seen in the figure that none of the samples were in the ranges of high, very high and extremely high SOC contents. Most of the samples were in the extremely low to moderate SOC range. The proportion of samples with moderate SOC contents was higher after restoration in the SK area, while it was reduced to zero in both AJ and QRC after restoration. On the other hand, the samples with moderately low SOC contents increased in AJ and QRC, while reducing in SK after restoration activities. This clearly indicates the loss of SOC and SOM from the soil after restoration activities. It is well known that plants cannot absorb SOM/SOC from the soil, rather, SOC helps plants to uptake nutrients in soil by altering physical, chemical and biological conditions [35]. However, the mineralization of SOM may release nutrients into the soil solution for the plants to uptake; hence, it is an important factor to assess soil fertility. Moreover, SOM is of significant importance for soil structure, aggregate stability, and clay dispersibility [36]. However, the cultivation of crops may disturb larger aggregates, resulting in enhanced SOM degradation. The plantation of local plants might have resulted in the loss of organic matter contents, which can deteriorate soil health and structure. Therefore, SOM needs to be maintained for the sustainable growth and development of the planted plants, so they can be used by honeybees. A recent study demonstrated that the application of SOM enhanced the visitation of bumblebee, as compared to without SOM application [37]. In another study, it was observed that higher SOM attracted 185 pollinators, as compared to 132 pollinators attracted by the soils with lower SOM [38]. This could possibly be due to the release of micro-and macronutrients from SOM mineralization, which improve the quality of flowers via increasing sugar contents and flower longevity, consequently attracting the pollinators towards them.    Nevertheless, due to the fact that SOC is sensitive to various factors, such as agricultural practices, climate, minerals in the soil, topography, and microbial communities, there is a higher spatial and temporal variability in its contents. This makes it difficult to compare the SOC of different sites, despite its extreme importance for soil quality topography [39]. Overall, SK sites have shown the better results of land restoration practices, as compared to QRC and AJ. The retention of SOC in the SK area, as compared to AJ and QRC, could be due to the difference in various factors, such as altitude, slope gradient, and pH. It has been reported that altitude has a significant effect on SOC retention in [40]. SK was a hilly area with a relatively higher altitude, thus, the development of various microhabitats might have facilitated the growth of plant communities, subsequently accumulating the higher C contents [41]. Additionally, the chances of aboveground biomass removal are more at lower altitudes than at higher altitudes. Thus, besides other factors, the higher altitude of SK facilitated the retention of SOC in that area after restoration activities. Therefore, loss of SOC in AJ and QRC during the restoration process in the current study reflects the poor SOC accumulation ability of the soil, and lower nutrient retention due to the sand based soil texture. Hence, complete restoration of these poor textured sites would require longer periods of time under sustainable practices. deteriorate soil health and structure. Therefore, SOM needs to be maintained for the s tainable growth and development of the planted plants, so they can be used by honeyb A recent study demonstrated that the application of SOM enhanced the visitation of bu blebee, as compared to without SOM application [37]. In another study, it was obser that higher SOM attracted 185 pollinators, as compared to 132 pollinators attracted by soils with lower SOM [38]. This could possibly be due to the release of micro-and ma nutrients from SOM mineralization, which improve the quality of flowers via increas sugar contents and flower longevity, consequently attracting the pollinators towa them.  The descriptive statistical analyses for the CaCO 3 of the collected soil samples are shown in Table 3. The mean CaCO 3 contents were in the range of 0.35% to 0.78%, suggesting the soils were not calcareous. It was noticed that CaCO 3 content reduced from 0.62% in the control to 0.35% in restored areas in the AJ sites, whereas the CaCO 3 contents increased from 0.52% and 0.39% in the control to 0.78% and 0.57% in restored areas in the QRC and SK sites, respectively. The lower CV values showed that there was little variability in the data. Likewise, the data was normal, as indicated by the values of skewness (0.533-1.777) and kurtosis (−0.910-2.279). The variations in CaCO 3 content with soil depth, as shown in Figure 3, demonstrated different trends. The CaCO 3 content increased with an increase in soil depth in AJ-C, while decreasing in QRC-C and SK-C. On contrary, the CaCO 3 content decreased with soil depth in AJ-R, whereas it increased in the QRC-R and SK-R areas. As CaCO 3 has a significant role in the stabilization of soil aggregates and SOC, the higher CaCO 3 contents in the QRC-R and SK-R sites showed the positive impacts of restoration activities. Our results are in agreement with those reported by Rowley et al. [42]. However, the elevated CaCO 3 contents in soils may increase the pH, subsequently hindering plant growth.

Phosphorus and Potassium
The descriptive analyses for available P and K in the collected soil samples are shown in Table 4. The mean P concentration in all the samples ranged from 1.09 to 2.57 mg kg −1 , suggesting poor soil fertility. The mean P concentrations in AJ and QRC are comparable, whereas, the mean P concentrations were lower in the SK sites. There was a huge variability in the data, as suggested by the larger CV values (72. 55-112.36). However, the values of the skewness (−0.115-1.788) and kurtosis (−1.560-2.917) indicated normality in the data. The variations in mean P concentrations due to restoration activities were inconsistent. It was noticed that the mean P concentrations reduced from 2.27 mg kg −1 in the control to 1.21 mg kg −1 in restored areas in AJ. However, P concentrations increased from 1.09 mg kg −1 in the control to 2.57 mg kg −1 in restored areas in QRC, whereas a very slight decrease (0.02 units) was observed in the case of SK, due to the restoration process. The overall decline in available P in AJ and SK, due to restoration, could be due to the conversion of soil texture to sandy loam and variations in vegetation composition [43]. Whereas, the increased P concentrations in QRC after restoration was probably due to the mineralization of soil nutrients, variations in microbial composition and activities [44,45], as well as an uptake in nutrient uptake by plants [46]. Soil P is affected by the parent material, land-use type, and other biological as well as chemical processes, therefore, variations in these properties could result in different P retention in soil [47]. The variations in available P concentrations with soil depth are represented in Figure 5A,C,F. The highest P concentration was found in the 0-20 cm deep soil layer, as compared to the topsoil and deeper soil layers in AJ-C, AJ-R, and SK-C, while the other soil samples showed a decrease in P concentration with soil depth up to 40 cm, and then increases up to 60 cm. Similar results were also reported by Xu et al. [47], stating that >60% of the total P was detected in the upper soil layer. Moreover, the surface soil is largely influenced by climatic factors, microbial activities, and plant litter accumulation, which result in higher nutrient retention [48].
The descriptive analysis for available soil K showed a larger variability in the data (CV = 52.96-104.21), with a range of 33.23 mg kg −1 to 81.26 mg kg −1 . It can be seen that the restoration activities resulted in an increment in available K concentrations. The K concertation was 56.36 mg kg −1 in the control of the AJ site, which increased to 75.58 mg kg −1 in restored areas. Likewise, it increased from 33.23 mg kg −1 in the control to 81.26 mg kg −1 in restored areas in the QRC sites, while no significant change was observed in the SK sites after restoration. The improved K in soil in all the restored areas could be due to the changes in soil structure and addition of fertilizers [39]. The variations in mean K concentrations with soil depth are shown in Figure 5B,D,F. The mean K concentrations did not follow any specific trend. For example, K concentration increased to the highest value (85.33 mg kg −1 ) in the 0-20 cm layer, decreased to 24.46 mg kg −1 in the 20-40 cm layer, and then increased to 54.13 mg kg −1 in the 40-60 cm layer, in AJ-C. A similar trend was seen in AJ-R and SK-C, while an opposite trend was observed in QRC-C and QRC-R. Therefore, these variations in P and K concentrations in soil with restoration activities could be due to the accumulation of organic compounds and the cultivation of plants [49]. However, in depth data is required to investigate the long term effects of the restoration activities.

Soil Micronutrients
The descriptive statistical analyses for the available soil micronutrients (Cu, Fe, Zn, and Mn) are shown in Table 5. Overall, the concentration of Fe was higher in all the soil types, followed by Mn, Cu, and Zn. The estimated CV values indicated a higher variability in the concentration of all the micronutrients, whereas the values of skewness and kurtosis suggested normality in the data. The effects of the restoration activities on micronutrients concentrations were not clear.

Soil Micronutrients
The descriptive statistical analyses for the available soil micronutrients (Cu, Fe, Zn, and Mn) are shown in Table 5. Overall, the concentration of Fe was higher in all the soil types, followed by Mn, Cu, and Zn. The estimated CV values indicated a higher variability in the concentration of all the micronutrients, whereas the values of skewness and kurtosis suggested normality in the data. The effects of the restoration activities on micronutrients concentrations were not clear.   The concentration of Cu increased from 1.61 to 1.84 mg kg −1 and 1.32 to 1.49 mg kg −1 after restoration in the AJ and SK sites, respectively, while it reduced from 1.20 to 0.97 mg kg −1 after restoration in the QRC sites. In the case of Fe, a reduction from 5.04 to 4.04 mg kg −1 and 5.79 to 2.64 mg kg −1 was observed after restoration activities in the AJ and QRC sites, respectively, whereas an increment from 7.11 to 7.44 mg kg −1 was seen in the SK sites with restoration. Similarly, the concentration of Mn reduced from 2.82 to 1.80 mg kg −1 and 2.82 to 1.07 mg kg −1 in the restored areas of AJ and QRC, respectively, while, on the contrary, it increased from 2.13 to 3.31 mg kg −1 in the restored areas of SK. This trend was even different in the case of Zn, which reduced from 0.25 to 0.14 mg kg −1 after restoration in the AJ sites, while increasing from 0.08 to 0.12 mg kg −1 and 0.13 to 0.23 mg kg −1 in the QRC and SK sites, respectively, after the restoration. Therefore, these results reflect that there was no specific trend for the variations in the concentrations of micronutrients after land restoration. It is established that the availability of micronutrients is influenced by soil physiochemical and biological properties, such as speciation of the element, concentration of oxides and carbonates, SOM, and pH [50]. The availability of cationic micronutrients decreases, while the availability of anionic micronutrients increases, with a rise in pH. In the current study, the pH of the AJ and QRC sites increased with restoration, while it decreased in the SK sites. This decrease in soil pH might have resulted in the higher solubility and availability of the micronutrients (Cu, Fe, Mn, and Zn). On the contrary, the rise in pH has subsequently reduced the available portion of Fe, Mn, and Zn in the QRC and AJ sites. Moreover, the variations in the concentrations of micronutrients in soil after restoration could also be linked to an unstable soil structure, the uptake of nutrients by the plants, and leaching [51,52]. However, plant-soil interactions should be explored to understand the sustainable restoration of soil and higher availability of floral resources for honeybees.

Correlation Studies
The correlations between different physiochemical properties (pH, EC, SOC, SOM, and CaCO 3 ) and soil nutrients (P, K, Cu, Fe, Mn, and Zn) were analyzed via Pearson's correlation coefficients (Table 6). The values of correlation coefficient (r 2 ) closer to 1 represent a stronger correlation, while the + or − sign shows the type of relationship at a 0.05 level of significance. The calculated correlations suggested a negative correlation of soil pH with EC (p < 0.05) and Fe contents. Moreover, soil Fe, Mn, and Zn contents were positively correlated with EC (p < 0.05). Likewise, soil Fe contents were positively correlated with SOC and SOM (p < 0.05). Nan et al. [53] reported the significant positive correlation of micronutrients with SOM. Soil Mn contents were also positively correlated with P and Fe (p < 0.05), while Zn was positively correlated with Fe and Mn (p < 0.05). Pearson correlations is a bivariant method used to investigate the relation between two parameters, thus, the results of the calculated correlation matrix showed some relations between soil available nutrients and soil properties [54]. Soil is a complex system made up of solid, liquid and gaseous phases, as well as various organisms. Therefore, the interpretation of different soil properties and of different types of soils is difficult due to the diversity of characteristics [55]. Therefore, due to varying soil locations, soil characteristics, and nutrient status, the correlations between the various parameters of soil collected from different localities were inconsistent. Table 6. Pearson correlation coefficients (r 2 ) and probability (p) as estimated for the relation of different parameters (pH, electrical conductivity (EC), heavy metals (Cu, Fe, Mn, and Zn), soil organic carbon (SOC), soil organic matter (SOM), CaCO 3 , phosphorus (P), and potassium (K)) of soil samples collected from Al-Jenebeen (AJ), Queen Rearing Center (QRC), and Shekiran (SK) in southwestern Saudi Arabia.

Conclusions
Soil degradation extent in forests of southwestern Saudi Arabia was evaluated in this study. About 78 samples from Al-Jenebeen (AJ), Queen Rearing Center (QRC), and Shekiran (SK) areas were collected, both from control (no treatment) and restored (restoration activities) areas. Soil physiochemical properties, such as phosphorus (P), potassium (K), pH, electrical conductivity (EC), soil organic matter (SOM), soil organic carbon (SOC), calcite (CaCO 3 ), texture, and micronutrients (Cu, Zn, Fe, and Mn), were determined. The data of soil physical and chemical properties showed inconsistent trends and larger variations. Overall, all the soil had lower SOM and nutrient contents, however, the soils were slightly alkaline and nonsaline. The results exhibited that sandy loam was the most dominant textural class in all the studied sites (~60%), followed by sandy clay loam. The variations in soil properties with restoration activities were inconstant. SK soil exhibited relatively prominent positive effects of restoration practices, as compared to QRC and AJ soils, as predicted by the highest SOC retention, reduced pH, and retention of nutrients. Therefore, currently, restored areas in SK could be beneficial for honeybee production due to the higher availability of floral resources. However, identifying the existing plant resources, soil physiochemical characteristics, and restoration potential of the study areas must be explored more for sustainable honeybee flourishing. Therefore, it was concluded that further temporal studies are needed to explore the long term effects of restoration activities on rehabilitation potential in the Al-baha region of Saudi Arabia.