Table of Contents Author Guidelines Submit a Manuscript
Applied and Environmental Soil Science
Volume 2019, Article ID 6874268, 15 pages
Research Article

Land Cover and Soil Properties Influence on Forage Quantity in a Semiarid Region in East Africa

1Department of Environmental Management, Makerere University, P.O. Box 7062, Kampala, Uganda
2Department of Land Resource Management and Agricultural Technology, University of Nairobi, P.O. Box 29053-00625, Nairobi, Kenya
3University of Bonn, Regina-Pacis-Weg 3, 53113 Bonn, Germany
4University of Nairobi, Department of Agricultural Economics, Nairobi, P.O. Box 29053-00625, Nairobi, Kenya
5Department of Geography, Geo-informatics and Climatic Sciences, Makerere University, P.O. Box 7062, Kampala, Uganda

Correspondence should be addressed to Anthony Egeru; moc.liamg@18urege

Received 15 August 2018; Revised 13 November 2018; Accepted 25 November 2018; Published 8 April 2019

Academic Editor: Claudio Cocozza

Copyright © 2019 Anthony Egeru et al. This is an open access article distributed under the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.


Soil properties contribute to the widely recognised resilience of semiarid areas. However, limited attention has been given in providing a scientific basis of how semiarid soil properties in the various land covers occur and how they influence forage quantity. This study investigated the influence of different soil properties and land cover types on herbaceous biomass quantity in the Karamoja subregion of Uganda. A completely randomized design in three land cover types (thickets and shrublands, woodlands, and savannah grasslands) was implemented. In each vegetation type, 50 × 40 m plots were demarcated with nested plots to facilitate clipping of the herbaceous layer. Composite soil samples at two depths (0–15 cm, 15–30 cm) were obtained from each plot. The results showed that soil properties varied across land cover types. Soil pH ranged between 6.9 and 8.1 and SOM, N, P, and K were generally low in all land cover types. Soil hydraulic properties revealed the existence of rapid to very rapid permeability in thickets/shrublands, grasslands, and woodlands. Percent change in soil properties (0–15 cm to 15–30 cm) was highest in P, Ca, Mg, Na, and SOM. In the grasslands, P positively () influenced herbaceous biomass, whereas pH, K, Na, % sand, and % clay, N, and SOM had a negative relationship with herbaceous biomass (). Herbaceous biomass in the thickets/shrublands was negatively influenced by P, Ca, and Mg and % clay and positively by N and % silt (). Only N and SOM were significant determinants of herbaceous biomass in the woodlands (). The low level of soil nutrients observed in this study reveals the fragility of semiarid soils, indicating the need for sustainable landscape management.

1. Introduction

Land plays an important role in providing food and water security and building resilience to climate change. It further contributes to climate change mitigation, through carbon sequestration and helping to meet energy needs [1]. However, land degradation and its manifestations have emerged as serious challenges facing the global community. The degradation is jeopardizing livelihoods and environmental health and is triggering a knock-on effect on the prevalence of diseases for plants, animals, and humans. These effects are subsequently disrupting human welfare and wellbeing by negatively affecting food production and sustainable development [24]. The United Nations Convention to Combat Desertification (UNCCD) indicated that the world is facing a “perfect storm,” with a number of huge problems converging around land issues. The poor, whose survival greatly depends on land, are at the center of this global challenging storm. However, they have limited capacity to tackle the marshaling “storm” clouds [5]. Several studies [3, 69] have analyzed the causes of land degradation with the appreciation of biophysical processes in combination with human-induced drivers occurring at different spatiotemporal scales. The causes often range from the level of the individual land user, whose management practices may be destructive, exploitative, short-sighted or negligent, to the policy level at which land use and management across larger (administrative) areas are governed and may be ill-conceived, inequitable, discriminatory, and/or simply ineffective [3, 10].

Despite the on-going degradation discourse, soil properties still contribute to the widely recognised resilience of semiarid rangelands because they provide a degree of suppleness that prevents any shifts in ecological competitive dominance [11]. For example, the high hydraulic conductivities associated with semiarid soils facilitate rapid water movement from the topsoil to the subsoil, thereby reducing direct evaporative losses that are often restricted to the upper 50 cm soil layer [12]. Such patterns in semiarid soils lead to high water use efficiency owing to accelerated infiltration of incident rainfall, rapid movement of water beyond the topsoil, and the rapid plant uptake of the topsoil water [11]. Soil properties are affected by the human use and abuse of soils; this can easily disturb the resilience of semiarid soils due to associated degradation [13]. In a study conducted in northern Gadarif region of Sudan, land use/cover changes had significant influence on physical and chemical soil properties leading to land degradation [14]. Research on soil properties changes due to land use/cover management is critical to understanding land degradation processes, sustainable use and resource dynamics in semiarid areas. Semiarid resource dynamics, in particular, forage and water, are critical in sustaining pastoral and agropastoral livelihoods as they directly influence livestock production, a key food security holding [15].

Like other pastoralists in Eastern Africa and the Horn of Africa such as the Borana [16], Afar [17], Maasai [18], and Orma [19] who depend on native and natural pastures to feed their livestock, the Karamojong are no exception. In these locations, grasses and woody plants provide the bulk of fodder to animals [16]. The availability of fodder in these areas depends on complex relations and interactions between ecosystem components including among others: soil, water, plant, climate, and animals [20]. Comprehensive understanding of social, ecological, and economic sustainability of rangelands is dependent on full knowledge of these ecosystem conditions and their impact on forage-including herbaceous productivity. Rangelands vary in herbaceous forage availability and production across landscapes. This in itself has not received judicious investigation [21]. Meanwhile, in pastoral Karamoja, pasture status is perceived by the pastoralists in terms of plant growth taking into consideration three growth phases: the early regeneration that occurs soon after the initial rainfall showers, the maturing and flowering stages of grasses, and the standing dry hay [19].

The Karamoja pastoralists understand the critical role that soil and landscapes have on livestock grazing and management by exerting control on vegetation dynamics. In their classification, the Matheniko, for example, know of “hot” and “cold” soils with the “hot” soils being undesirable for night cattle kraaling. The Karamojong also have observed that sandy landscapes tend to be heavily grazed compared to black soil landscapes arising from differences in land cover types as well as herbaceous species [19]. However, these observations are only based on the traditional ecological knowledge and thus lack scientific explanations. In other rangeland areas such as in Benin, forage species tolerance to low soil fertility has been observed. Legumes have been observed to grow in sandy to clay soils with a better performance in medium textured soils [22]. In contrast, [23] identified nitrogen (N), phosphorus (P), potassium (K), and soil pH as four primary soil components important in forage production. Karltun et al. [24] showed a high positive correlation between nitrogen and biomass production in Ethiopia. Further, Juice et al. [25] established that the abundance, species composition, and nutrient content of vegetation are influenced by changes in concentration of cations and nutrient availability in soils. In a three year study conducted in a forest and watershed ecosystem in Pennsylvania, Pabian et al. [26] established that forage biomass availability was positively related to soil pH, calcium, and magnesium.

Several researchers [17, 27] attempted detailed investigations of rangeland status. A number of these studies have focused on rangeland conditions, with emphasis towards understanding “rangeland degradation” [28, 29]. Fewer studies have focused on rangeland productivity; a notable example is [30] who addressed the effect of bushland encroachment on grassland productivity. Pickup [31] discussed the role of climate on rangeland forage production. The effect of grazing and trampling on forage productivity has also received some attention [32]. Further, others have focused on the attendant effects of land use [33] and associated practices such as grazing [34], fire, and cultivation on soil properties in the rangelands [28]. As such, the understanding that soil characteristics contribute to the widely recognised resilience of semiarid rangelands has been overlooked [11]. There is an urgent need to investigate how land management and its modifications impact soil and soil properties in rangelands with a view of affirming how man might be “a destructive agent” of the rangelands. The missing link in most of these studies has been the scientific basis of semiarid soil properties in the different land cover types and how they influence semiarid forage production. Bridging this knowledge gap is important in East Africa where semiarid areas have traditionally been considered “wastelands” [35] whose inhabitants live in a state of “chaos” [36] and whose environments and practices are beyond development [37]. This study therefore determined the influence of different land cover types and soil properties on forage quantity in a semiarid Karamoja region of East Africa.

2. Materials and Methods

2.1. Study Area

This study was conducted in Karamoja subregion located in the north eastern Uganda (Figure 1). Karamoja subregion is occupied by the Karamojong people who are part of the Karamoja cluster in the Greater Horn of Africa (GHA). The area is a semiarid with variable rainfall ranging from 500 to 1000 mm per annum and is poorly distributed. Rainfall is often characterised by storms that build up in the afternoons with velocities in the region of 13–18 km/h and with storm diameters of 32 to 48 km thereby producing intense rainfall of up to 25 mm/h [38, 39]. This pattern of rainfall is not surprising given the high temperatures and associated evapotranspiration averaging 28°C–33°C for minimum and maximum temperature and annual potential evaporation (PET) of 1800–2200 mm/annum, respectively [18, 40, 41]. The subregion is dominated by C4 grasses characterised by acacia/cymbogon/themeda complex [42]. Thus, the subregion is generally a savanna ecosystem that is made up of bushlands, woodlands, and thickets/shrublands [43]. Geologically, Karamoja consists of plains and isolated volcanic highlands including Mount Moroto, Mount Zulia, Mount Kadam, Mount Iriiri, and Mount Labwor and a series of other inselbergs (e.g., Kogwele, Kanamerinjor, Katipus, Morutit, Kapernakori in Kotido district and Koromwae, Napakgngaran, Turusuk, Nyanga, Thane, Arakas, Kolung, Nakithilet hills in Kotido-Kaabong). The subregions’ soils originate from the Precambrian basement complex. Western Karamoja generally consists of carbonatites with deeply dissected agglomerates, tuffs, and silica unsaturated flows of lava overlying the Precambrian basement. The soils in the plains and valleys of the subregion are dominated by dark grey to dark brown calcareous clays which are noteworthy for their extreme stickiness when wet and for their aridity shrinkage (tendency to form large deep cracks when dry). These clays are derived both from wind and water deposits [44]. The soils in the northern Karamoja are part of the ferruginous tropical soils that are freely drained and weakly developed lithosols. Karamoja’ soils are in general characterised by black cracking clays classified as vertisols under the FAO soil classification scheme [45].

Figure 1: Geographical location of Karamoja subregion.
2.2. Consultation with Local Stakeholders

Prior to undertaking forage quantification exercise, a previsit to the subregion was undertaken. During the previsit, an exercise to identify forage monitoring sites was conducted with elders, youth, scouts, and herders who have detailed knowledge of the land cover types in the region. Three land cover types were identified including: grasslands, thickets/shrublands, and savannah woodlands. These land covers were identified through consultative discussions that matched vegetation growth forms to land cover type. The local stakeholders also identified three vegetation growth forms. First is eparat echalichal which describes early regeneration after early and initial rainfall. This was indicated to occur around late February through to early April depending on the timing of rainfall onset. Second is akelebat/ekelebat/kelebat which describes the period when the herbaceous vegetation flowers and matures. This was indicated to occur between the months of June and July. Third is athakan which describes the standing dry hay that was indicated to often occur between the months of October and November. In order to corroborate the growth forms and periods as identified by local stakeholders, long-term monthly normalized difference vegetation index (NDVI) data were utilised. The National Oceanic and Atmospheric Administration-Advance Very High Resolution Radiometer (NOAA-AVHRR, 1981–2008) and Moderate Resolution Imaging Spectroradiometer (MODIS) NDVI (2000–2012) time series NDVI data were used for this purpose. Mean monthly NDVI deviations were computed. Computing the mean monthly NDVI deviations allowed us to identify vegetation growth periods (Figure 2).

Figure 2: Long-term monthly NDVI deviations revealing vegetation growth patterns in Karamoja.
2.3. Establishing Monitoring Sites

In this study, the identified land cover types (grasslands, thickets and shrublands, and woodlands), phenological stages, and periods (seasons: wet and dry) were considered as treatments/independent variables. Forage assessment monitoring sites were established based on three criteria. These criteria jointly developed by the scientific team and local stakeholders. First, the land cover had to be fairly stable in with the minimum grazing effect observed. A fairly stable land cover was taken to be that with a good balance of desirable forage species. Second, the land cover had to be fairly secure from potential raiders that paused insecurity in the subregion. Third, the land cover had to be fairly accessible that it could be reached on foot. A 15 km walkable distance from the last point a vehicle could access was considered. This was essential because some areas could experience sporadic rains. In addition, armed security guards provided by the Uganda People’s Defense Forces (UPDF) had to be back at the base before 6:00 pm.

2.4. Forage Quantification and Soil Sampling

In this study, forage was taken to mean the edible herbaceous parts of plants, other than separated grain, that can provide feed for grazing animals and/or can be harvested for feeding livestock [46]. In order to determine the influence of different land cover types and soil properties on forage quantity, a completely randomized design established in three land cover types (grasslands, woodlands, and thicket/shrublands) was used. Eight plots measuring 50 × 40 m were demarcated in each land cover unit in Moroto and Kotido districts. Plots of 50 × 40 m have been recommended when measuring above-ground biomass [47]. In the 50 × 40 m plots, nested plots were established for herbage clipping. Five nested plots of 5 × 5 m were established in the woodlands, 10 plots of 5 × 5 m in the thickets/shrublands, and 20 plots of 1 × 1 m in the grasslands. Clipped herbage was freshly weighed, and a 0.5 kg composite sample (all edible parts of plants) was taken for dry matter determination in the Makerere University Soil Science Laboratory. The assessment was conducted in three periods during January/February, June/July, and October/November in respect to vegetation growth periods identified with the local stakeholders.

The soil physical and chemical properties investigated included soil texture, soil structure, total nitrogen (TN), available phosphorus (Av. P), total potassium (TP), magnesium (Mg), sodium (Na), calcium (Ca), soil pH, and soil organic matter (SOM). Composite soil samples were collected using a soil auger of 50 mm diameter for soil texture, SOM, TN, Av. P, soil pH, Mg, Na, and Ca determination. Undisturbed soil samples (100 cm3) were taken for saturated hydraulic conductivity, and bulk density analysis using a core method by driving a core sampler into the soil to a desired depth. All the soil samples were taken at soil depths 0–15 cm and 15–30 cm from the same plots where forage was clipped. Soil samples were taken at these depths because they represent active root zone [48]. Further, these sampling depths have previously been applied in the semiarid areas of Mongolia [49].

2.5. Forage and Soil Samples Processing

Quantity of forage was determined through dry matter processing. Herbaceous forage samples taken to the laboratory were oven dried at 60˚ C until a constant weight. Following [50]; dry matter was determined gravimetrically as the residue remaining after oven drying. The gravimetrical results of different sampling plots were then pulled together by land cover type and averaged to obtain dry matter weight (kg/ha).

Soil available phosphorus was determined using spectrophotometry (Bray-1). Total nitrogen was determined by digestion and titration. For extractable bases (P and Na), flame photometry method was used after extraction with natural ammonium acetate. Ca and Mg were determined using atomic absorption spectrophotometry after extraction of the soils with a natural ammonium acetate solution. Further, saturated hydraulic conductivity was analyzed through a constant head method [51]. Soil organic matter (SOM) was determined using the Walkley–Black method. All these methods of analysis are detailed described in [52]. Soil structure was determined by the dry sieving technique and the results are expressed as mean weight diameter (MWD) of the aggregates [53]. Soil samples were passed through a 10 mm sieve [54], thereafter passed through a nest of concentric rings of progressively declining sieve sizes: 6.36, 4.75, 2.36, 1.18, 0.425, and 0.212 mm. A vibratory sieve shaker-FRITSCH analyzette 3E was set at amplitude 5 for 30 minutes during the processing of soil aggregates. Lastly, available water content (AWC) was computed following the approach described by [55]. Soil samples to determine available water content and bulk density were oven-dried at 105°C for a minimum of 24 h.

3. Data Analysis

In this study, four classical statistical techniques were utilised to analyze for associations between soil properties and forage availability. Descriptive statistics of soil properties from the different land covers (woodlands, grasslands, and thicket and shrublands) were generated to ascertain their patterns and trends. Correlations were thereafter conducted to test for the relationship between soil properties and forage quantity expressed in biomass (kg/ha). Analysis of variance (ANOVA) was performed to test for the significances in the mean differences related to soil properties and land covers during the two rainfall seasons. Prior to the ANOVA test, soil properties data were subjected to normality distribution test following the approach by [56]. Significant differences in ANOVA tests were determined at and land cover and soil properties means were compared by Fisher’s protected least significant difference (LSD) test. In addition, a principal component analysis (PCA) and generalized linear model (GLM) regression were acquired for determining the relationship and influence of soil properties on forage quantity in the land covers. Also, regression analysis was performed for each land cover type to identify landscape specific determinants. Classical statistical analysis was conducted using GenSTAT12 portable version [57].

4. Results

4.1. Variability of Soil Properties across Land Cover Types

The observed variability of soil properties across the land cover types in the study area are presented in Table 1. According to the USDA soil texture classification [58], all soils in the grasslands and thickets/shrublands are predominantly sandy clay loam while woodlands have sandy loam. However, soils generally depicted variability across the land cover types. Soil organic matter varied from 1.23 to 1.84% across the land cover types. The mean SOM values across the land cover types were below the critical value of 3.0%. The soil pH across the land cover types was neutral to alkaline. The mean soil pH was 7.7 for both soil depths across the land cover types. The minimum and maximum soil pH values were 6.9 and 8.4, respectively. The soil pH values observed are conducive for vegetation growth. The mean N and Av. P values across the land cover types for both soil depths were below their respective critical values (0.2% and 15 ppm, respectively). Among the selected soil properties analyzed, available P had the largest decline (88%) and increase (283%) from top soil (0–15 cm) to the subsoil (15–30 cm) across all the land cover types. Furthermore, grassland land cover type had the largest depletion and increment of available . When the results were subjected to the ANOVA test, the observed mean differences for the soil properties were significantly () different across the land cover types, except total nitrogen, soil organic matter, available water content, and potassium (at 15–30 cm depth) (Table 1).

Table 1: Summary of chemical and physical soil properties characteristics.

In terms of physical soil properties, Ksat and bulk density experienced variations within and between land cover types. Grasslands had Ksat mean of 17.5 ± 10.1 (mm/h), thickets/shrublands 17.4 ± 11.1 (mm/h), and woodlands 39.4 ± 25.5 (mm/h). Bulk density showed an overall mean of 1.3 ± 0.1 (g/cm3) for all land covers with a minimal variation between land cover types. At 1.38 (g/cm3), the bulk density in the woodlands varied significantly from that in the grasslands and thickets and shrublands. Although there were differences in the wilting point, field capacity and the available water content (AWC) in the different land cover types (Figure 3), these differences were nonsignificant.

Figure 3: Shows wilting point (WP), field capacity (FC), and available water content (AWC) for the different land cover types in Karamoja.

5. Relationship between Soil Properties and Biomass

The correlation coefficients between individual soil properties and biomass are reflected in Tables 24. A few soil properties and biomass showed positive and negative dependence at 5% significance level. However, there were several soil properties that were closely associated with biomass at 10% significance level (Tables 24).

Table 2: Relationship between soil properties and forage quantity in grasslands.
Table 3: Relationship between soil properties and forage quantity in thickets/shrublands.
Table 4: Relationship between soil properties and forage quantity in the woodlands.
5.1. Relationship between Soil Properties, Land Cover, and Season

Soil physical and chemical properties in the grasslands, thickets and shrubs, and woodlands across the seasons are shown in Tables 5 and 6 for soil depths 0–15 cm and 15–30 cm, respectively. Top soil (0–15 cm) properties except percent silt content, SOM, TN, Av. P, K, and Mg differed significantly () across land cover. Across seasons, soil properties (TN, Ca, and Mg) showed significant differences (). Albeit no significant differences across land cover for SOM, statistically, grasslands had higher SOM (1.84% in dry season and 1.45% in wet season), though this is below the critical value (3.0%).

Table 5: Effects of land cover type on physical and chemical soil properties at 0–15 cm depth.
Table 6: Effects of land cover type on physical and chemical soil properties at 15–30 cm depth.

Likewise, soil properties in the lower depth (15–30 cm) except TN, percent silt, and Na differed significantly () across land cover. Comparing soil properties across the seasons, soil properties except percent clay and silt, exchangeable K, Av. P, Na, and soil pH differed significantly (). SOM was considerably higher (1.8%) in grasslands in the dry season while in the wet season, woodlands registered a slightly higher SOM. Like in the top soil, the mean SOM values across the land covers were below the critical values (3.0%).

Table 7 presents the effect of the soil properties on forage quantity across the land use cover types and seasons. Results showed that during the wet and dry seasons, woodlands had relatively higher dry matter at 42.3 Kg/ha and 31.7 Kg/ha, respectively. This was followed by 42.6 Kg/ha and 10.7 Kg/ha in the grasslands during the wet and dry seasons, respectively. On the other hand, thicket and shrublands land covers had 26.8 Kg/ha and 9.6 Kg/ha of biomass during the wet and dry seasons, accordingly. However, this pattern changed during the transitionary season with the thickets and shrublands having relatively higher dry matter 22.9 ± 9.6 Kg/ha, followed by grasslands and woodlands. Woodlands had a low biomass yield during the transitionary season because some of the plots had been interfered with by partial burning (use of fire).

Table 7: Influence of soil properties on forage quantity in the land cover units.
5.2. Influence of Soil Properties on Forage Quantity

The principal component analysis (PCA) revealed a strong correlation of six soil properties with the forage quantity (Figure 4). Results of the generalized linear regression model revealed different levels and patterns of influence soil properties have on forage quantity (Table 7). Soil pH, potassium and sodium, percent sand, and percent clay were observed to be inversely significant () in the grasslands. This indicates that a decline in these soil properties potentially triggers an increase in forage quantity in the grasslands. A similar pattern was observed in SOM and phosphorus. Meanwhile, magnesium (Mg) and nitrogen had a positive significant effect on forage quantity in the grasslands.

Figure 4: Principal component analysis of the relationship between forage quantity and soil properties.

In the thickets and shrublands, phosphorus, calcium, magnesium, and percent clay had a significant but inverse effect on forage quantity at 3.8%, 0.2%, 1.4, and 0.2% respectively. This indicates that a decline in these soil properties would result to an increase in biomass quantity in the thickets/shrublands land cover type. This trend was also observed in pH and SOM that had a 0.6% and 0.8% inverse influence rates on biomass, respectively. Notably, nitrogen was observed to have a relatively high positive significant () effect on forage quantity at 42.9% in the thickets/shrublands, indicating that a unit increase in nitrogen in the thickets/shrublands would lead to a 42.9% increase in forage quantity. Meanwhile, a low N : P ratio (0.004) pertained in the thickets/shrublands; this indicated that phosphorus was a limiting soil nutrient in the thickets/shrublands. Nitrogen was found to a negative () effect on forage quantity in the woodlands (Table 7). This revealed that a reduction in nitrogen in the woodlands would lead to an increased forage quantity in this land cover. However, calcium, pH, and percent sand showed a positive influence on biomass at 10% level. A lower N : P ratio (0.04) in the woodlands was identified revealing phosphorus limitations.

6. Discussion

6.1. Soil Properties in Various Land Cover Types

Soil pH is an important soil chemical property for healthy plant growth. This is because it controls the availability of nutrients most especially phosphorus [59]. At an average pH 7.7, the soils of Karamoja can be classified into moderately acidic to strongly alkaline category as described by [60]. Besides being high, the pH was variable across the three land cover types as well as with depth. The high pH observed in Karamoja is attributable to high calcium deposits within the subregion. The mining of calcium rich rocks (limestone and marble) in the subregion in Moroto and Amudat district provides evidence to the calcium rock deposits in the area. Further, the deep wells including boreholes in the subregion are characterised with hard water which is indication of high calcium compound deposits [61]. According to Perry [62], soils in semiarid and arid regions are generally characterised by neutral to high pH (7.0–8.7). Arshadullah et al. [63] have documented the presence of high alkaline pH in semiarid ecosystems of Pakistan. A high pH in semiarid environments is attributed to the fact that soils developing in these environments tend to retain the alkaline earth and alkali cations to a great extent. Thus, the hydroxides of these cations form, leading to an alkaline pH [64]. Further, this study has shown significant differences in pH of different land cover types. This variation in soil pH could be attributable to soil types [65], parent materials [66], and land use activities [67].

Nitrogen levels observed in the subregion as well as in respective land covers (grasslands, thickets/shrublands, and woodlands) were generally below the critical levels in [52]. However, they were relatively higher than those observed in semiarid Mulga lands of Australia [68]. Semiarid areas have been reported to have low nitrogen levels [69]. Albeit an exception to this pattern is found in the earlier study by [70] that revealed a relatively high nitrogen content of 5 to 8% in semiarid Senegal. Low N presence in the different land covers could be attributed to limited presence of leguminous plants in the land covers that could support N fixation. Notwithstanding low nitrogen across different land covers, Venkanna et al. [71] showed nitrogen variability with respect to land use/cover types in which grasslands often have relatively higher nitrogen compared to croplands.

The average soil organic matter (SOM) in this study was lower than the limit value suggested by Pradini et al. [72]. It is also far below the minimum level indicated by Smith and Elliot [73] as well as that documented by Arshadullah et al. [63] in the semiarid Pabbi, Pakistan. These low levels of SOM reveals a low soil fertility in the area. Yet, SOM is one of the important indicators of soil quality [74]. According to [65] semiarid areas are typified by relatively low SOM concentrations. This is often conspicuously low ranging between 0.5 and 3% and generally less than 1% [72, 73]. This presence of low SOM in semiarid areas has been attributed to inputs dominated by plant-derived organic matter, degradation processes regulated by microorganisms, and organomineral interactions [75]. Further, it is a result of low primary productivity and rapid SOM mineralization that often characterises semiarid regions [65]. Karamoja subregion is no exception to these patterns. This is because the quantified biomass as indicated by the results of this study is lower than in most grazing systems of the same rainfall regime. For example, Chen et al. [76] have shown evidence of herbaceous biomass quantity ranging between 518 kg/ha to 8075 kg/ha in the semiarid rangelands of Idaho. This is above the established herbaceous biomass quantified in the subregion. It is also important to note that in Karamoja, the frequent use of fire as a range management tool leads to limited ground litter cover that could potentially be decomposed into SOM.

The average phosphorus in the land covers was indicated at 3.4 ± 6.8 mg/kg with a range of 0.4 to 5.7 mg/kg. Thickets/shrublands were indicated to have the lowest average phosphorus content. These levels of phosphorus reveal severe deficiency because they are far lower than the critical limits (15 mg/kg−1). But, phosphorus (P) has been observed as the second most limiting micronutrient for plant growth after N. This is because P makes up to 0.2% of the plant’s dry weight and is a component of key molecules. Ample plant growth is dependent on a reliable supply of phosphorus [77]. Thus, P limitations observed in the subregion can quite well help to explain the low quantity of forage obtained per hectare in the different land covers. Further, the observed P in Karamoja was lower than that observed in semiarid northern Ghana [78] as well as in semiarid Argentina [79]. The cases of higher P levels identified by these two studies could be an exception in semiarid regions as several studies have shown P deficiencies in semiarid areas. Whereas, this study did not analyze the effect of phosphorus on livestock reproductive and growth performance, the apparently low levels offer insights into the likely livestock status performance.

The K content obtained in this study is slightly higher than that obtained by Chikuvire et al. [80] in semiarid Zimbabwe. Our results however show lower K levels compared to the results of [81] obtained in the Negev desert in Israel. This could be attributable to differences in land cover types as well as the geologies of the two places. The availability of potassium in the soil is generally attributed to the type of K-bearing minerals, the degree of weathering, and the intensity of soil forming processes [82]. Further, Paliwa and Sundaravalli [83] observed that burning in a semiarid ecosystem of Madurai positively influenced potassium availability. Given that burning is a management strategy that is applied on an annual basis in the Karamoja subregion, it is likely that in addition to parent material-related factors, it also contributes to relatively high K availability in the region. This is an issue that requires further investigation.

The bulk density observed in this study in the different land cover types was within the optimum value for arable soils. It also reveals that the land cover types had minimal levels of soil compaction. Based on the criteria for identification of monitoring sites, this result confirms the reliability of site selection criteria. Further, it shows that there is value in integrating traditional ecological knowledge when conducting rangeland monitoring studies. In an earlier study, Alderfer et al. [84] established that in nongrazed and lightly grazed landscapes, soil bulk density ranged between 1.09 and 1.51 Mg/m3, and this study’s results are within this range. Further, they had shown that for heavily grazed sites, soil bulk densities ranged from 1.54 to 1.91 Mg/m3, indicating relatively high compaction. Similarly, Ayoubi et al. [85] in a study in semiarid western Iran have shown that under pasture, soil bulk density is significantly lower (1.30 g·cm−3), which is in agreement with our findings. Considering that this study’s results show minimal compaction of the land cover types, degradation in the monitoring sites is thus limited.

According to [19] in an ethnological study in Karamoja, the Matheniko pastoralists of Moroto district had characterised their land covers as moderately to minimally used. This could further explain the favorable bulk density values observed in this study. It also shows that there is minimal livestock trampling in the grazing land covers. This study’s findings have further reinforced earlier findings by providing biophysical evidence from the grazing land covers within the subregion. However, in Oba’s findings, the landscapes with poor status were those near settlements and security establishments. Similarly, during the field process, we observed considerable gradient effect existing in and around the waterholes and protected kraals with high grazing and trampling intensity, lose soil, and compact soil particles in others as well as existence of erosion signs.

The low bulk density associated with minimum compaction observed in this study could thus provide plausible explanation to the relatively high saturated hydraulic conductivity (Ksat) also observed in this study. However, compared to saturated hydraulic conductivity results reported in semiarid profiles in Tunisia (4.84 ± 3.33 kg·s·m−3) and Senegal 3.93 ± 2.24 kg·s·m−3 [86], our results are slightly higher but lower than those reported in the semiarid Maireana shrubs of Australia [87]. It is important to note that there was considerable variation in Ksat values in the different land cover units with the highest values observed in the woodlands while the thickets/shrublands were within comparable range. Consequently, the land cover type was later found to have a significant effect on Ksat. This phenomenon is not unusual because it is not unusual to obtain variation in Ksat depending on the depth and the method in use [88], type of soil, for example, sandy versus clayey soils [86], land use practice [89], type of vegetation, and landform [90].

6.2. Influence of Land Cover and Seasonality on Soil Properties

A significant effect of land cover on soil properties was identified in this study. However, it varied with soil depth (0–15 cm and 15–30 cm). Land cover type had a significant influence on percent sand, percent clay, calcium content, and sodium and soil pH at 0–15 cm depth. At 15–30 cm depth, the range of influence expanded to include percent sand, percent clay, SOM, phosphorus, potassium, calcium, and magnesium and soil pH. Sodium and percent silt were not influenced by land cover type at this soil depth. Additionally, land cover had a significant impact on bulk density and saturated hydraulic conductivity (Ksat). Land cover alteration tends to influence bulk density and Ksat after conversion from one form to the other for example, from forested to nonforested-exposed lands [91]. Similarly, [14, 92] found a significant influence of land cover type on physical and chemical soil properties.

Changes in land cover led to land degradation in the Gadarif region of Sudan. Soil properties such as organic matter, interchangeable K, and available P showed degradation tendencies in the Trans-Mexican volcanic system of Mexico. Therefore, conversion of woodlands into grasslands will likely elicit a similar pattern as observed in the previous studies. Land cover changes have already been observed to be occurring in the subregion at an unprecedented rate with grasslands, thickets/shrublands, and woodlands being threatened by croplands [42]. Moreover, land cover types vary in their rooting characteristics; for example, forests and shrublands have been found to root deeper with better diameter, dispersion, and biomass than rooting systems of herbaceous plants (characteristic of grasslands) or cultivated crops [93]. Our results also reveal that soils under native vegetation cover often have low bulk density and high saturated hydraulic conductivity. This corroborates with the earlier findings of [94]. However, in the findings of Celik [95] and Li and Shao [96], soils exposed to human influence are often stripped of organic rich upper horizons, resulting in higher BD values and reduced infiltration rates.

Seasonality has a bearing on nutrient availability. Our results showed that season had significant influence on pH, bulk density, saturated hydraulic conductivity, soil organic matter, and nitrogen. This corroborates with findings of several researchers [97, 98] that reported the influence of season on various soil properties (SOM, total nitrogen, soil pH, available phosphorus, and exchangeable cations). Further, this study has reported a significant influence of season on saturated hydraulic conductivity and bulk density that are also significantly different across various land cover types. Additionally, the land cover type has been identified to influence saturated hydraulic conductivity, and this varies across seasons [99], as observed in this study.

6.3. Effect of Soil Properties on Forage Quantity

This study observed a positive relationship between nitrogen and forage quantity in thickets/shrublands and grasslands similar to the findings of other scientists [24, 100102] that established a positive relationship between increased nitrogen and above-ground forage quantity in various parts of Africa such as Laikipia in Kenya and Northern Cape, South Africa. The influence of nitrogen on herbaceous biomass arises from the N fertilization that often leads to increased net primary production (shoot biomass) and thicker stands [8, 9, 103]. This perspective has similarly been shown in this study (Table 7). However, in the woodlands, an inverse influence of nitrogen on forage quantity was observed. This could be attributed to the fact that in woody land cover types, there is often a strong negative dependence of woody cover on soil nitrogen availability [104]. This result is however contrary to the findings of other researchers [105107] that have showed that under conditions of increased nitrogen, the yield of biomass and dry matter are generally high. In the case of the current study, the result observed is attributable to the fact that nitrogen was not a limiting nutrient in the woodlands as results revealed phosphorus limitations. Phosphorus limitation on grass growth has been observed in semiarid Laikipia [108].

Potassium (K) is an essential macronutrient for normal plant growth. In a limited amount, it limits accumulation of crop/pasture biomass resulting tin stunting of crop/pasture as well as low yields [109111]. In this study, potassium exhibited inverse relationship with forage quantity in all the land cover types (Table 7). This contrasts with the findings of [110, 112] that opined that potassium has an incremental effect on plant biomass accumulation. The inverse relationship observed in this study could be attributed to relatively elevated potassium levels (0–15 cm (0.7 ± 0.2 cmol/kg) and 15–30 cm (0.6 ± 0.2 cmol/kg) soil depth. This was higher was higher than the critical soil potassium (0.19 cmol/kg) needed to achieve a 90% maximum yield in crops such as sorghum and maize [113]. Sorghum and maize are closer to herbaceous grasses that were quantified in this study. We attribute the relatively high K concentrations in this study to ash accumulation from continuous burning that takes place in the subregion. Routine burning is used as a management tool to facilitate forage regrowth. Biomass burning and continuous livestock grazing have previously been found to lead to relatively high potassium content concentrations in the grassland savannas in Kenya [114].

The SOM was found to have negative relation with forage quantity in thicket/shrublands and grassland land covers while it increased forage quantity in the woodlands. This result is particularly intriguing because SOM is generally expected to have a positive association with above-ground biomass production [115]. However, the pattern observed could also suggest that greater SOM could be associated with higher clay content which in itself could be an active negative factor for perennial plant growth. Further, we opine that this outcome could be arising from the limited soil moisture in the grasslands and thickets/shrublands. This leads to limited decomposition of litter; as a result, the available SOM cannot be transferred into available nutrient for plant growth. It is important to note that this result contrasts the findings of [116] who reported that total above-ground biomass was influenced by soil organic matter. Owing to the complex nature of soil quality and/or soil health effects, we hold the maxim that “correlation is not causality” with regard to this study’s findings.

7. Conclusions

This study has shown that soil nutrient levels in Karamoja are generally low confirming the notion of low nutrient availability in semiarid areas. However, instances of above average soil nutrient levels such as the case with potassium whose value was above the critical level determined as necessary to achieve a 90% yield in crops such as sorghum were observed. Secondly, nitrogen and phosphorus limitations varied in the different land cover types. Nitrogen was observed as a limiting nutrient in the grasslands while phosphorus was a limiting nutrient in the thickets/shrublands and woodlands. Thus, any improvement on pasture production as well as crop production (particularly sorghum that is commonly grown in the region) in these land covers ought to address these nutrient limitations. Thirdly, seasonality and differences in land covers influenced forage quantity; this strengthens the evidence of heterogeneity, a key attribute that has for long facilitated local level (land cover type) to regional level (landscape level) opportunistic livestock herd management among pastoralists and agropastoralists in the subregion. Besides seasonality and land cover type influence on forage quantity, soil properties both physical (bulk density and saturated hydraulic conductivity) and chemical (N, P, K, SOM) have a significant influence on forage quantity in the subregion. We recommend for long-term monitoring of soil properties and forage under different grazing regimes in Karamoja subregion. Further, it is vital that the identified soil nutrients that influence forage quantity be validated in the subregion.

Data Availability

Primary data for this study and the results contained therein are available and can be made available on request.

Conflicts of Interest

The authors declare that they have no conflicts of interest.

Authors’ Contributions

Anthony Egeru was involved in the study conceptualization, development, data collection, and manuscript write-up. Oliver V. Wasonga, provided technical backstopping in the study design and manuscript development and quality assurance processes in the study. Geofrey Gabiri provided support in data collection and data analysis. Laban A. MacOpiyo played a role in research design, data collection supervision, and field based monitoring for quality assurance. John Mburu supported the editorial components of the manuscript development process. Gilbert Jackson Mwanjalolo Majaliwa provided technical backstopping in data analysis, interpretation of results, and manuscript structuring.


This study was funded in part by Carnegie Corporation of New York through Makerere University and Regional Universities Forum for Capacity Building in Agriculture. The funding agency did not take part in the design of the study neither in the collection, analysis, and interpretation of data thereof leading this paper.


  1. R. J. Thomas, M. Akhtar-Schuster, L. C. Stringer et al., “Fertile ground? Options for a science-policy platform for land,” Environmental Science and Policy, vol. 16, pp. 122–135, 2012. View at Publisher · View at Google Scholar · View at Scopus
  2. M. J. Swift, K. Stroud, A Shepherd et al., Confronting Land Degradation in Africa: Challenges for the Next Decade. World Agroforestry into the Future, World Agroforestry Centre, Nairobi, Kenya, 2006.
  3. L. Fleskens and L. C. Stringer, “Land management and policy responses to mitigate desertification and land degradation,” Land Degradation and Development, vol. 25, no. 1, pp. 1–4, 2014. View at Publisher · View at Google Scholar · View at Scopus
  4. T. Wang, “Aeolian desertification in northern China,” Journal of Arid Land Studies, vol. 24, no. 1, pp. 13–15, 2014. View at Google Scholar
  5. M. Akhtar-Schuster, M. Winslow, J. Vogt et al., “Understanding desertification and land degradation trends,” in Proceedings of the UNCCD First Scientific Conference, during the UNCCD Ninth Conference of Parties, Buenos Aires, Argentina, September 2009. View at Publisher · View at Google Scholar
  6. A. Cerdà and H. Lavée, “The effect of grazing on soil and water losses under arid and mediterranean climates. Implications for desertification,” Pirineos, vol. 153-154, pp. 159–174, 2010. View at Publisher · View at Google Scholar
  7. K. T. Weber and S. Horst, “Desertification and livestock grazing: the roles of sedentarization, mobility and rest,” Pastoralism: Research, Policy and Practice, vol. 1, no. 1, pp. 1–11, 2011. View at Publisher · View at Google Scholar · View at Scopus
  8. T. Wang, X. Xue, L. Zhou, and J. Guo, “Combating Aeolian desertification in northern China,” Land degradation and development, vol. 26, no. 2, 2012. View at Publisher · View at Google Scholar · View at Scopus
  9. S. Wang, B. J. Fu, G. Y. Gao, and J. Zhou, “The hydrological responses of different land cover types in a re-vegetation catchment area of the Loess Plateau, China,” Hydrology and Earth System Sciences Discussions, vol. 9, no. 5, pp. 5809–5835, 2012. View at Publisher · View at Google Scholar
  10. R. B. Harris, “Rangeland degradation on the Qinghai-Tibetan plateau: a review of the evidence of its magnitude and causes,” Journal of Arid Environments, vol. 74, no. 1, pp. 1–12, 2010. View at Publisher · View at Google Scholar · View at Scopus
  11. A. J. Doudill, A. Louise-Heathwaite, and D. S. G. Thomas, “Soil water movement and nutrient cycling in semi-arid rangeland: vegetation change and system resilience,” Hydrological Processes, vol. 12, no. 3, pp. 443–459, 1998. View at Publisher · View at Google Scholar
  12. P. Vossen, “Algorithm for the simulation of bare sandy soil evaporation and its application for the assessment of planted areas in Botswana,” Agricultural and Forest Meteorology, vol. 50, no. 3, pp. 173–188, 1990. View at Publisher · View at Google Scholar · View at Scopus
  13. D. Gabriels and W. M. Cornelius, “Human-induced land degradation,” in Land Use, Land Cover, and Soils Science, vol. 3, Encyclopedia of Life Support Systems, Paris, France, 2002, View at Google Scholar
  14. K. Biro, B. Pradhan, M. Buchroithner, and F. Makeschin, “Land use/land cover change analysis and its impact on soil properties in the northern part of Gadarif region, Sudan,” Land Degradation and Development, vol. 24, no. 1, pp. 90–102, 2011. View at Publisher · View at Google Scholar · View at Scopus
  15. K. B. Showers, A History of African Soil: Perceptions, Use and Abuse. Soils and Societies, The White Horse Press, Isle of Harris, UK, 2006.
  16. S. Tefera, H. A. Snyman, and G. N. Smit, “Rangeland dynamics in southern Ethiopia: (3). Assessment of rangeland condition in relation to land-use and distance from water in semi-arid Borana rangelands,” Journal of Environmental Management, vol. 85, no. 2, pp. 453–460, 2007. View at Publisher · View at Google Scholar · View at Scopus
  17. E. Abule, H. A. Snyman, and G. N. Smit, “Rangeland evaluation in the middle Awash valley of Ethiopia: I. Herbaceous vegetation cover,” Journal of Arid Environments, vol. 70, no. 2, pp. 253–271, 2007. View at Publisher · View at Google Scholar · View at Scopus
  18. C. Neely, S. Bunning, and A. Wilkes, Review of Evidence on Drylands Pastoral Systems and Climate Change: Implications and Opportunities for Mitigation and Adaptation, Food and Agriculture Organization of the United Nations, Rome, Italy, 2008, Land and Water Discussion Paper 8.
  19. G. Oba, “Harnessing pastoralists’ indigenous knowledge for rangeland management: three African case studies,” Pastoralism: Research, Policy and Practice, vol. 2, no. 1, p. 1, 2012. View at Publisher · View at Google Scholar · View at Scopus
  20. M. Azimi, G. A. Heshmati, M. Farahpour, M. Faramarzi, and K. C. Abbaspour, “Modeling the impact of rangeland management on forage production of sagebrush species in arid and semi-arid regions in Iran,” Ecological Modeling, vol. 250, pp. 1–14, 2012. View at Publisher · View at Google Scholar · View at Scopus
  21. M. K. Ngugi and R. T. Conant, “Ecological and social characterization of key resource areas in Kenyan rangelands,” Journal of Arid Environments, vol. 72, no. 5, pp. 820–835, 2008. View at Publisher · View at Google Scholar · View at Scopus
  22. S. Adjolohoun, Yield, nutritive value and effects on soil fertility of forage grasses and legumes cultivated as ley pastures in the Borgou region of Benin, Faculté Universitaire des Sciences Agronomiques, Gembloux, Belgique, 2008.
  23. R. D. Mathison and P. R. Peterson, “Enhancing soil fertility to improve forage quality,” in Proceedings of 2011 Minnesota Beef Cow/Calf Days, Minneapolis, MN, USA, February 2011.
  24. E. Karltun, M. Lemenih, and M. Tolera, “Comparing farmers' perception of soil fertility change with soil properties and crop performance in Beseku, Ethiopia,” Land Degradation and Development, vol. 24, no. 3, pp. 228–235, 2011. View at Publisher · View at Google Scholar · View at Scopus
  25. S. M. Juice, T. J. Fahey, T. G. Siccama et al., “Response of sugar maple to calcium addition to northern hardwood forest,” Ecology, vol. 87, no. 5, pp. 1267–1280, 2006. View at Publisher · View at Google Scholar
  26. S. E. Pabian, N. M. Ermer, W. M. Tzikowski, and M. C. Brittingham, “Effects of liming on forage availability and nutrient content in a forest impacted by acid rain,” PLoS ONE, vol. 7, no. 6, Article ID e39755, 2012. View at Publisher · View at Google Scholar · View at Scopus
  27. T. B. Solomon, H. A. Snyman, and G. N. Smit, “Cattle-rangeland management practices and perceptions of pastoralists towards rangeland degradation in the Borana zone of southern Ethiopia,” Journal of Environmental Management, vol. 82, no. 4, pp. 481–494, 2007. View at Publisher · View at Google Scholar · View at Scopus
  28. H. A. Snyman and C. C. du Preez, “Rangeland degradation in a semi-arid South Africa-II: influence on soil quality,” Journal of Arid Environments, vol. 60, no. 3, pp. 483–507, 2005. View at Publisher · View at Google Scholar · View at Scopus
  29. H. A. Snyman, “Rangeland degradation in a semi-arid South Africa-I: influence on seasonal root distribution, root/shoot ratios and water-use efficiency,” Journal of Arid Environments, vol. 60, no. 3, pp. 457–481, 2005. View at Publisher · View at Google Scholar · View at Scopus
  30. D. Hernández-Daumas, B. L. Maass, and J. Isselstein, “Encroachment of woody plants and its impact on pastoral livestock production in the Borana lowlands, southern Oromia, Ethiopia,” African Journal of Ecology, vol. 44, no. 2, pp. 237–246, 2006. View at Publisher · View at Google Scholar · View at Scopus
  31. G. Pickup, “A simple model for predicting herbage production from rainfall in rangelands and its calibration using remotely-sensed data,” Journal of Arid Environments, vol. 30, no. 2, pp. 227–245, 1995. View at Publisher · View at Google Scholar · View at Scopus
  32. M. Mellado, A. Rodríguez, E. A. Lozano, J. Dueñez, C. N. Aguilar, and J. R. Arévalo, “The food habits of goats on rangelands with different amounts of fourwing saltbush (Atriplex canescens) cover,” Journal of Arid Environments, vol. 84, pp. 91–96, 2012. View at Publisher · View at Google Scholar · View at Scopus
  33. A. Angassa, B. Sheleme, G. Oba, A. C. Treydte, A. Linstädter, and J. Sauerborn, “Savanna land use and its effect on soil characteristics in southern Ethiopia,” Journal of Arid Environments, vol. 81, pp. 67–76, 2012. View at Publisher · View at Google Scholar · View at Scopus
  34. P. Hiernaux, C. L. Bielders, C. Valentin, A. Bationo, and S. Fernández-Rivera, “Effects of livestock grazing on physical and chemical properties of sandy soils in Sahelian rangelands,” Journal of Arid Environments, vol. 41, no. 3, pp. 231–245, 1999. View at Publisher · View at Google Scholar · View at Scopus
  35. J. Silale and S. M. Nyambegera, “The influence of socio-economic factors in the transformation of rural economies in arid and semi-arid areas: lessons from Turkana County of Northern Kenya,” International Journal of Business and Social Research, vol. 4, no. 1, pp. 109–120, 2014. View at Google Scholar
  36. C. Hesse and J. MacGregor, Pastoralism: Drylands’ Invisible Asset? IIED, London, UK, 2006.
  37. J. Davies, “Turning the tide: enabling sustainable development for Africa’s mobile pastoralists,” Natural Resources Forum, vol. 32, no. 3, pp. 175–184, 2008. View at Publisher · View at Google Scholar · View at Scopus
  38. G. Ngirane-Katashaya and A. Kaford, “An innovative intervention by a multiplicity of surface and underground interlinked dams/weirs, sand storages, sub geological engineering to solve Karamoja’s perenial water shortage,” in Proceedings of Second International Conference on Adavances in Engineering and Technology, pp. 640–649, Nanjing, China, December 2011.
  39. S. Avery, “Water development and irrigation in Karamoja, Uganda. A review report submitted to dan church aid,” 2014, View at Google Scholar
  40. M. Mirzeler and C. Young, “Pastoral politics in the northeast periphery in Uganda: AK-47 as change agent,” Journal of Modern African Studies, vol. 38, no. 3, pp. 407–429, 2000. View at Publisher · View at Google Scholar · View at Scopus
  41. A. Grange, Climate Change and Adaptation Strategies in the Karamoja Sub-Region, DanChurchAid, Kampala, Uganda, 2010.
  42. A. Egeru, O. Wasonga, J. Kyagulanyi, G. Majaliwa, L. MacOpiyo, and J. Mburu, “Spatio-temporal dynamics of forage and land cover changes in Karamoja sub-region, Uganda,” Pastoralism: Research, Policy and Practice, vol. 4, no. 1, p. 6, 2014. View at Publisher · View at Google Scholar · View at Scopus
  43. A. Egeru, “Assessment of forage dynamics under variable climate in Karamoja sub-region of Uganda,” University of Nairobi, Nairobi, Kenya, 2014, Ph.D.thesis. View at Google Scholar
  44. A. S. Thomas, “The vegetation of the Karamoja district, Uganda: an illustration of biological factors in tropical ecology,” The Journal of Ecology, vol. 31, no. 2, pp. 149–177, 1943. View at Publisher · View at Google Scholar
  45. ACF, Food Security and Livelihoods Assessment Kaabong and Moroto, Karamoja, ACF, Kampala, Uganda, 2008.
  46. V. G. Allen, C. Batello, J. Hodgson et al., “An international terminology for grazing lands and grazing animals,” Grass and Forage Science, vol. 66, no. 1, pp. 2–28, 2011. View at Publisher · View at Google Scholar · View at Scopus
  47. H. Folster, NPP Tropical Forest: Magdalena Valley, Colombia, 1970-1971, R1. Data set, Oak Ridge National Laboratory Distributed Active Archive Center, Oak Ridge, TN, USA, 2013.
  48. P. A. Vadas, A. P. Mallarino, and A. McFarland, “The importance of sampling depth when testing soils for their potential to supply phosphorus to surface runoff,” 2006, Report of the Agriculture/Information Exchange Group (SERA-17/IEG), CSEERS Committee. View at Google Scholar
  49. J. Cao, X. Wang, X. Sun, L. Zhang, and Y. Tian, “Effects of grazing intensity on soil labile organic carbon fractions in a desert steppe area in Inner Mongolia,” Springerplus, vol. 2, no. 1, p. S1, 2013. View at Publisher · View at Google Scholar · View at Scopus
  50. D. Undersander, D. R. Mertens, and N. Thiex, Forage Analyses Procedures, National Forage Testing Association, Omaha, NE, USA, 1993.
  51. T. W. Wietsma, M. Oostrom, M. A. Covert, T. E. Queen, and M. J. Fayer, “An automated tool for three types of saturated hydraulic conductivity laboratory measurements,” Soil Science Society of America Journal, vol. 73, no. 2, pp. 466–470, 2009. View at Publisher · View at Google Scholar · View at Scopus
  52. J. R. Okalebo, K. W. Gathua, and P. L. Woomer, Laboratory Methods of Soil and Plant Analysis: A Working Manual, Sacred African Publishers, Nairobi, Kenya, 2nd edition, 2002,
  53. M. Diaz-Zorita, J. H. Grove, and E. Perfect, “Aggregation, fragmentation, and structural stability measurement,” in Encyclopedia of Soil Science, pp. 37–40, Taylor & Francis, Oxfordshire, UK, 2002. View at Google Scholar
  54. W. D. Kemper and R. C. Rosenau, “Aggregate stability and size distribution,” in Methods of Soil Analysis. Part 1. Physical and Mineralogical Methods-Agronomy Monograph no. 9, pp. 425–442, John Wiley & Sons, Hoboken, NJ, USA, 2nd edition, 1986. View at Google Scholar
  55. S. S. Andrews, D. L. Karlen, and C. A. Cambardella, “The soil management assessment framework,” Soil Science Society of America Journal, vol. 68, no. 6, pp. 1945–1962, 2004. View at Publisher · View at Google Scholar
  56. S. K. Wiser, R. B. Allen, P. W. Clinton, and K. H. Platt, “Community structure and forest invasion by an exotic herb over 23 years,” Ecology, vol. 79, pp. 2071–2081, 1998. View at Publisher · View at Google Scholar
  57. R. W. Payne, S. A. Harding, D. A Murray et al., The Guide to GenStat Release 12, Part 2: Statistics, VSN International, Hemel Hempstead, UK, 2009.
  58. United States Department of Agriculture (USDA) and Natural Resources Conservation Service (NRCS), “Soil taxonomy: a basic system of soil classification for making and interpreting soil surveys,” Agriculture Handbook 436, U.S. Government Print Office, Washington, DC, USA, 1999. View at Google Scholar
  59. P. Moody, Understanding Soil pH, Natural Resources and Water, Queensland Government, Australia, Brisbane, Australia, 2005.
  60. H. D. Foth and B. G. Ellis, Soil Fertility, Lewis CRC Press LLC, Boca Raton, FL, USA, 2nd edition, 1997.
  61. J. Burns, G. Bekele, and D. Akabwai, Livelihood Dynamics in Northern Karamoja. A Participatory Baseline Study for Growth Health and Governance Program, Tufts University, Medford, MA, USA, 2013,
  62. A. Perry, “Effects in arid regions,” in Ecotoxicology and Climate: With Special Reference to Hot and Cold Climates, P. Bourdeau, J. A. Haines, and W. Klein, Eds., pp. 155–180, John Wiley & Sons Ltd., Hoboken, NJ, USA, 1989. View at Google Scholar
  63. M. Arshadullah, M. Anwar, and A. Azim, “Evaluation of various exotic grasses in semi-arid conditions of Pabbi Hills, Kharian range,” Journal of Animal and Plant Sciences, vol. 19, no. 2, pp. 85–89, 2009. View at Google Scholar
  64. A. E. Al-Rawajfeh, H. Glade, and J. Ulrich, “Scaling in multiple-effect distillers: the role of CO2 release,” Desalination, vol. 182, no. 1–3, pp. 209–219, 2005. View at Publisher · View at Google Scholar · View at Scopus
  65. A. S. Carr, A. Boom, B. M. Chase et al., “Biome-scale characterisation and differentiation of semi-arid and arid zone soil organic matter compositions using pyrolysis-GC/MS analysis,” Geoderma, vol. 200-201, pp. 189–201, 2013. View at Publisher · View at Google Scholar · View at Scopus
  66. D. W. Anderson, “The effect of parent material and soil development on nutrient cycling in temperate ecosystems,” Biogeochemistry, vol. 5, no. 1, pp. 71–97, 1988. View at Publisher · View at Google Scholar · View at Scopus
  67. V. Geissen, R. Sánchez-Hernández, C. Kampichler et al., “Effects of land-use change on some properties of tropical soils - an example from Southeast Mexico,” Geoderma, vol. 151, no. 3‐4, pp. 87–97, 2009. View at Publisher · View at Google Scholar · View at Scopus
  68. G. B. Witt, M. V. Noël, M. I. Bird, R. J. S. Beeton, and N. W. Menzies, “Carbon sequestration and biodiversity restoration potential of semi-arid mulga lands of Australia interpreted from long-term grazing exclosures,” Agriculture, Ecosystems and Environment, vol. 141, no. 1-2, pp. 108–118, 2011. View at Publisher · View at Google Scholar · View at Scopus
  69. D. M. Mburu, F. K. Lenga, and M. W. K. Mburu, “Assessment of maize yield response to nitrogen fertilizer in two semi-arid areas of Kenya with similar rainfall pattern,” JAGST, vol. 13, no. 1, pp. 22–34, 2011. View at Google Scholar
  70. F. Bernhard-Reversat, “Biogeochemical cycle of nitrogen in a semi-arid savanna,” OIKOS, vol. 38, no. 3, pp. 321–332, 1982. View at Publisher · View at Google Scholar · View at Scopus
  71. K. Venkann, U. Kumar Mandal, A. J Solomon Raju et al., “Carbon stocks in major soil types and land use systems in semiarid tropical region of southern India,” Current Science, vol. 106, no. 4, pp. 604–611, 2014. View at Google Scholar
  72. G. Pardini, G. Dunjó, R. Barrena, and M. Gispert, “Land use effects on soil response to runoff generation and sediment yield in the Serra de Rodes catchment, Alt Emporà, NE Spain,” in Man and Soil at the Third Millennium, J. L. Rubio, S. Asins, V. Andreu, J. M. Paz, and E. Gimeno, Eds., p. 290e298, ESSC- European Society of Soil Conservation, Valencia, Spain, 2000. View at Google Scholar
  73. J. L. Smith and L. F. Elliott, “Tillage and residue management effects on soil organic matter dynamics in semiarid regions,” Advances in Soil Science, vol. 13, pp. 69–88, 1990. View at Publisher · View at Google Scholar
  74. A. Imeson, “The physical, chemical and biological degradation of the soil,” in Desertification in a European Context: Physical and Socio-Economic Aspects, E. Fantechi, D. P. Denis, P. Balabanis, and J. I. Rubio, Eds., pp. 153–168, European Commission, Directorate-General Science Research and Development, Brussels, Belgium, 1995. View at Google Scholar
  75. W. Zech, N. Senesi, G. Guggenberger et al., “Factors controlling humification and mineralization of soil organic matter in the tropics,” Geoderma, vol. 79, no. 1–4, pp. 117–161, 1997. View at Publisher · View at Google Scholar · View at Scopus
  76. F. Chen, K. T. Weber, and B. Gokhale, “Herbaceous biomass estimation from SPOT 5 Imagery in semiarid rangelands of Idaho,” GIScience and Remote Sensing, vol. 48, no. 2, pp. 195–209, 2011. View at Publisher · View at Google Scholar · View at Scopus
  77. D. P. Schachtman, R. J. Reid, and S. M. Ayling, “Phosphorus uptake by plants: from soil to cell,” Plant Physiology, vol. 116, no. 2, pp. 447–453, 1998. View at Publisher · View at Google Scholar · View at Scopus
  78. E. Owusu-Bennoah, J. G. Ampofo, and D. K. Acquaye, “Phosphorus status in semi-arid agricultural soils of northern Ghana,” Ghana Journal of Agricultural Science, vol. 28-29, no. 1, pp. 29–35, 1995. View at Publisher · View at Google Scholar
  79. L. Zhang, J. Gala, and G. Minoldo, “Soil phosphorus dynamics of wheat-based cropping systems in the semi-arid region of Argentina,” Applied and Environmental Soil Science, vol. 2014, Article ID 532807, 6 pages, 2013. View at Google Scholar
  80. T. J. Chikuvire and S. Mpepereki, “Temporal variation of macronutrients in arable niches exploited by Zimbabwe’s semi-arid smallholder farmers,” Bulletin of Environment, Pharmacology and Life Sciences, vol. 1, no. 10, pp. 38–45, 2012. View at Google Scholar
  81. M. Segoli, E. D. Ungar, and M. Shachak, “Fine Scale spatial heterogeneity of resource modulation in semi-arid “island of fertility”,” Arid Land Research and Management, vol. 26, no. 4, pp. 344–354, 2012. View at Google Scholar
  82. S. Duta and A. V. Shanwal, “Potassium bearing minerals in some soils of semi-arid (Haryana) and humid (Assam) regions of India,” Agropedology, vol. 16, no. 2, pp. 86–91, 2006. View at Google Scholar
  83. K. Paliwa and V. M. Sundaravalli, “Effect of fire on nutrient dynamics in a semi-arid grazing land ecosystem of Madurai,” Current Science, vol. 30, no. 3, pp. 316–318, 2002. View at Google Scholar
  84. R. B. Alderfer and R. R. Robinson, “Runoff from pastures in relation to grazing intensity and soil Compaction1,” Agronomy Journal, vol. 39, no. 11, pp. 948–958, 1947. View at Publisher · View at Google Scholar
  85. S. Ayoubi, N. Emami, N. Ghaffari, N. Honarjoo, and K. L. Sahrawat, “Pasture degradation effects on soil quality indicators at different hillslope positions in a semiarid region of western Iran,” Environmental Earth Sciences, vol. 71, no. 1, pp. 375–381, 2013. View at Publisher · View at Google Scholar · View at Scopus
  86. E. Tarnavsky, M. Mulligan, M. Ouessar, A. Faye, and E. Black, “Dynamic hydrological modeling in drylands with TRMM based rainfall,” Remote Sensing, vol. 5, pp. 6691–6716, 2013. View at Publisher · View at Google Scholar · View at Scopus
  87. D. Dunkerley, “Hydrologic effects of dryland shrubs: defining the spatial extent of modified soil water uptake rates at an Australian desert site,” Journal of Arid Environments, vol. 45, no. 2, pp. 159–172, 2000. View at Publisher · View at Google Scholar · View at Scopus
  88. K. Verbist, W. M. Cornelis, D. Gabriels, K. Alaerts, and G. Soto, “Using an inverse modelling approach to evaluate the water retention in a simple water harvesting technique,” Hydrology and Earth System Sciences Discussions, vol. 6, no. 3, pp. 4265–4306, 2009. View at Publisher · View at Google Scholar
  89. N. Sauwa, A. Chiroma, U. U. Waniyo, A. L. Ngala, and N. M. Danmowa, “Water transmission properties of a sandy loam soil under different tillage practices in Maiduguri, Nigeria,” Agriculture and Biology Journal of North America, vol. 4, no. 3, pp. 227–233, 2013. View at Publisher · View at Google Scholar
  90. D. R. Bedford and E. E. Small, “Spatial patterns of ecohydrologic properties on a hillslope-alluvial fan transect, central New Mexico,” Catena, vol. 73, no. 1, pp. 34–48, 2008. View at Publisher · View at Google Scholar · View at Scopus
  91. K. Price, C. R. Jackson, and A. J. Parker, “Variation of surficial soil hydraulic properties across land uses in the southern Blue Ridge Mountains, North Carolina, USA,” Journal of Hydrology, vol. 383, no. 3-4, pp. 256–268, 2010. View at Publisher · View at Google Scholar · View at Scopus
  92. M. Bravo-Espinosa, M. E. Mendoza, T. CarlóN Allende, L. Medina, J. T. Sáenz-Reyes, and R. Páez, “Effects of converting forest to avocado orchards on topsoil properties in the trans-Mexican volcanic system, Mexico,” Land Degradation and Development, vol. 25, no. 5, pp. 452–467, 2012. View at Publisher · View at Google Scholar · View at Scopus
  93. I. Messing, A. Alriksson, and W. Johansson, “Soil physical properties of afforested and arable land,” Soil Use and Management, vol. 13, no. 4, pp. 209–217, 1997. View at Publisher · View at Google Scholar · View at Scopus
  94. K. Lee and R. Foster, “Soil fauna and soil structure,” Soil Research, vol. 29, no. 6, pp. 745–775, 1991. View at Publisher · View at Google Scholar · View at Scopus
  95. I. Celik, “Land-use effects on organic matter and physical properties of soil in a southern Mediterranean highland of Turkey,” Soil and Tillage Research, vol. 83, no. 2, pp. 270–277, 2005. View at Publisher · View at Google Scholar · View at Scopus
  96. Y. Y. Li and M. A. Shao, “Change of soil physical properties under long-term natural vegetation restoration in the Loess Plateau of China,” Journal of Arid Environments, vol. 64, no. 1, pp. 77–96, 2006. View at Publisher · View at Google Scholar · View at Scopus
  97. D. B. Watts, H. A. Torbert, and S. A. Prior, “Soil property and landscape position effects on seasonal nitrogen mineralization of composted dairy manure,” Soil Science, vol. 175, no. 1, pp. 27–35, 2010. View at Publisher · View at Google Scholar · View at Scopus
  98. A. Fatubarin and M. R. Olojugba, “Effect of rainfall season on the chemical properties of the soil of a Southern Guinea savanna ecosystem in Nigeria,” Journal of Ecology and the Natural Environment, vol. 6, no. 4, pp. 182–189, 2014. View at Publisher · View at Google Scholar
  99. P. Suwardji and P. L. Eberbach, “Seasonal changes of physical properties of an Oxic Paleustalf (Red Kandosol) after 16 years of direct drilling or conventional cultivation,” Soil and Tillage Research, vol. 49, no. 1-2, pp. 65–77, 1998. View at Publisher · View at Google Scholar · View at Scopus
  100. D. J. Augustine, “Spatial heterogeneity in the herbaceous layer of a semi-arid savanna ecosystem,” Plant Ecology, vol. 167, no. 2, pp. 319–332, 2003. View at Publisher · View at Google Scholar · View at Scopus
  101. K. R. Mbatha and D. Ward, “The effects of grazing, fire, nitrogen and water availability on nutritional quality of grass in semi-arid savanna, South Africa,” Journal of Arid Environments, vol. 74, no. 10, pp. 1294–1301, 2010. View at Publisher · View at Google Scholar · View at Scopus
  102. L. Song, X. Bao, X. Liu, and F., “Impact of nitrogen addition on plant community in a semi-arid temperate steppe in China,” Journal of Arid Land, vol. 4, no. 1, pp. 3–10, 2012. View at Publisher · View at Google Scholar · View at Scopus
  103. L. J. Li, D. H. Zeng, A. Y. Yu, Z. P. Fan, R. Mao, and P. L. Peri, “Foliar N/P ratio and nutrient limitation to vegetation growth on Keerqin sandy grassland of North-east China,” Grass and Forage Science, vol. 60, no. 2, pp. 237–242, 2012. View at Publisher · View at Google Scholar · View at Scopus
  104. M. Sankaran, J. Ratnam, and N. Hanan, “Woody cover in African savannas: the role of resources, fire and herbivory,” Global Ecology and Biogeography, vol. 17, no. 2, pp. 236–245, 2008. View at Publisher · View at Google Scholar · View at Scopus
  105. J. Glamoclija, M. Sokovic, D. Grubisic, J. Vukojevic, I. Milinekovic, and M. Ristic, “Antifungal activity of Critmum maritimum essential oil and its components against mushroom pathogen Mycogone perniciosa,” Chemistry of Natural Compounds, vol. 45, no. 1, pp. 96-97, 2009. View at Publisher · View at Google Scholar · View at Scopus
  106. D. Glamoclija, S. Jankovic, S. Rakic, R. Maletic, J. Ikanovic, and Z. Lakic, “Effects of nitrogen and harvesting time on chemical composition of biomass of Sudan grass, fodder sorghum, and their hybrid,” Turkish Journal of Agriculture and Forestry, vol. 35, no. 2, pp. 127–138, 2011. View at Google Scholar
  107. L. Pociene, L. Sarunaite, V. Tilvikiene, J. Slepetys, and Z. Kadziuliene, “The yield and composition of reed canary grass biomass as raw material for combustion,” Biologija, vol. 59, no. 2, pp. 195–200, 2013. View at Publisher · View at Google Scholar
  108. C. Riginos, J. B. Grace, D. J. Augustine, and T. P. Young, “Local versus landscape-scale effects of savanna trees on grasses,” Journal of Ecology, vol. 97, no. 6, pp. 1–7, 2009. View at Publisher · View at Google Scholar · View at Scopus
  109. H. Marschner, “Functions of mineral nutrients: macronutrients,” in Mineral Nutrition of Higher Plants, R. J. Haynes, Ed., pp. 195–267, Academic Press, Orlando, FL, USA, 1986. View at Google Scholar
  110. Z. M. Sawan, M. H. Mahmoud, and A. H. El-Guibali, “Influence of potassium fertilization and foliar application of zinc and phosphorus on growth, yield components, yield and fiber properties of Egyptian cotton (Gossypium barbadense L.),” Journal of Plant Ecology, vol. 1, no. 4, pp. 259–270, 2008. View at Publisher · View at Google Scholar
  111. N. Lua-Kapu, “Assessment of rangeland condition and evaluation of the nutritional value of common grass and browse species at the neudamm experimental farm, Namibia,” University of Namibia, Windhoek, Namibia, 2012, M.S. thesis. View at Google Scholar
  112. M. Wang, Q. Zheng, Q. Shen, and S. Guo, “The critical role of potassium in plant stress response,” International Journal of Molecular Sciences, vol. 14, no. 4, pp. 7370–7390, 2013. View at Publisher · View at Google Scholar · View at Scopus
  113. M. Bell, G. Harch, P. Want, and P. Moody, “Management responses to declining potassium fertility in Ferrosol soils,” in Proceedings 14th Australian Agronomy Conference of Global Issues, Paddock Action, pp. 21–25, Adelaide, South Australia, September 2008.
  114. J. Kioko, J. W. Kiringe, and S. O. Seno, “Impacts of livestock grazing on a savanna grassland in Kenya,” Journal of Arid Land, vol. 4, no. 1, pp. 29–35, 2012. View at Publisher · View at Google Scholar · View at Scopus
  115. B. Diabate, Y. Gao, Y. Li et al., “Associations between species distribution patterns and soil salinity in the songnen grassland,” Arid Land Research and Management, vol. 29, no. 2, pp. 199–209, 2014. View at Publisher · View at Google Scholar · View at Scopus
  116. R. F. Powers, D. Andrew Scott, F. G. Sanchez et al., “The North American long-term soil productivity experiment: findings from the first decade of research,” Forest Ecology and Management, vol. 220, pp. 31–50, 2005. View at Publisher · View at Google Scholar · View at Scopus