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Article

The Response of Water and Nutrient Dynamics and of Crop Yield to Conservation Agriculture in the Ethiopian Highlands

by
Sisay A. Belay
1,*,
Tewodros T. Assefa
1,
P. V. Vara Prasad
2,
Petra Schmitter
3,
Abeyou W. Worqlul
4,
Tammo S. Steenhuis
1,5,
Manuel R. Reyes
2 and
Seifu A. Tilahun
1
1
Faculty of Civil and Water Resources Engineering, Bahir Dar Institute of Technology, Bahir Dar University, Bahir Dar 26, Ethiopia
2
Sustainable Intensification Innovation Lab, Department of Agronomy, Kansas State University, Manhattan, Kansas, KS 66506, USA
3
International Water Management Institute, Yangon 11081, Myanmar
4
Blackland Research Center, Texas A&M AgriLife Research, Temple, TX 76502, USA
5
Department of Biological and Environmental Engineering, Cornell University, Ithaca, NY 14850, USA
*
Author to whom correspondence should be addressed.
Sustainability 2020, 12(15), 5989; https://doi.org/10.3390/su12155989
Submission received: 28 June 2020 / Revised: 22 July 2020 / Accepted: 23 July 2020 / Published: 24 July 2020
(This article belongs to the Section Sustainable Agriculture)
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Abstract

:
Smallholder agriculture constitutes the main source of livelihood for the Ethiopian rural community. However, soil degradation and uneven distribution of rainfall have threatened agriculture at present. This study is aimed at investigating the impacts of conservation agriculture on irrigation water use, nutrient availability in the root zone, and crop yield under supplementary irrigation. In this study, conservation agriculture (CA), which includes minimum soil disturbance, grass mulch cover, and crop rotation, was practiced and compared with conventional tillage (CT). We used two years’ (2018 and 2019) experimental data under paired-t design in the production of a local variety green pepper (Capsicum annuum L.). The results showed that CA practices significantly (α = 0.05) reduced irrigation water use (13% to 29%) and runoff (29% to 51%) while it increased percolated water in the root zone (27% to 50%) when compared with CT practices under the supplementary irrigation phase. In addition, CA significantly decreased NO3-N in the leachate (14% to 44%) and in the runoff (about 100%), while PO4-P significantly decreased in the leachate (33% to 50%) and in the runoff (16%) when compared with CT. Similarly, CA decreased the NO3-N load in the leachate and in the runoff, while the PO4-P load increased in the leachate but decreased in the runoff. The yield return that was achieved under CA treatment was 30% higher in 2018 and 10% higher in 2019 when compared with the CT. This research improves our understanding of water and nutrient dynamics in green pepper grown under CA and CT. Use of CA provides opportunities to optimize water use by decreasing irrigation water requirements and optimize nutrient use by decreasing nutrient losses through the runoff and leaching.

1. Introduction

Water and soil nutrients remain the most limiting resources for agriculture. However, rainfed and irrigated agriculture is often hindered by the depletion of soil nutrients through surface runoff and leaching during rainy phases [1,2], as well as by the scarcity of water during dry phases [2,3]. Surface runoff adversely affects the availability of water [3,4,5], soil nutrients [5,6,7], and soil organic matter for plant growth and development [8,9]. Percolated water (leaching) can also affect water and nutrient availability to some extent [5]. Agricultural activities exacerbate the removal of nutrients by either of the processes [10]. Nutrients that are removed by surface runoff are permanently lost before reaching the root zone of the plant, while nutrients that are leached below the root zone are at least temporarily lost from the root system. Concurrently, the nutrient and water components of surface runoff and percolation may also deteriorate the water quality of wells, reservoirs, and lakes [11]. Thus, the nutrients often removed by water movement and dynamics contribute not only to water quality deterioration, but this also imply an economic loss of soil fertility to the farmer. The current approach of agricultural systems, which promotes the use of more chemical fertilizers [12], particularly for vegetable production, shows a wider expansion of the above risks and is becoming a serious threat to our environment [12,13,14].
Hence, there is a need for a paradigm shift to improve smallholder agriculture systems that promote sustainable intensification, which encourages an increase in crop productivity with minimum inputs and protects the environment at the same time [12]. Smallholder vegetable production at home gardens is one approach of a localized strategy to improve the livelihood and nutrition of farmers in many developing countries [15,16], including Ethiopia. Smallholder vegetable production may also be optimized by applying conservation agriculture (CA) practices that would improve productivity with minimum inorganic inputs and minimize adverse effects on the environment. The CA system (minimum soil disturbance, complete soil cover, and proper crop rotation) has been used to improve irrigation water use efficiency and crop productivity while controlling soil nutrient losses caused by various factors [16,17]. No-tillage, despite the challenges of implementation and adoption [18], reduces runoff [4,19,20], increases percolation, and enhances water holding capacity of soils [7,21,22,23], when combined with grass mulch cover and proper crop rotation. The biological decomposition of grass mulch has improved the soil quality (adding soil nutrients) and soil structure, while a no-till practice combined with a complete soil cover reduces the soil compaction in the long term [24], particularly in drier regions or dry phases [7,23]. The yield of cereal crops has been increased in CA systems (due to higher water infiltration) under rainfed phases of production [7,19,22,25]. Water use efficiency and the yield of vegetables significantly increase under CA in dry irrigation phases of production compared with the conventional practices [16,26,27].
Most of the previous studies evaluated the impacts of CA practices mainly on cereal crops and on either rainfed or irrigated systems. There are few studies on the impacts of CA on water saving and yield measurement in grain crops in the sub-humid Ethiopian highlands [3,6,14,18,27]. However, experimental field measurements on commercial home vegetable production systems with measurements on water and nutrient dynamics in addition to yield have been limited. Such targeted experiments are required for a comprehensive impact analysis of CA under irrigated-rainfed vegetable production systems. Application of CA in vegetable production systems with local varieties based on market demand has greater opportunities for adoption. The demand for green pepper (Capsicum annum L.) is becoming greater, and farmers in this region are choosing to grow in their home gardens. Moreover, there is limited research under the supplementary phase (irrigated and then rainfed) on vegetables and particularly in peppers in Ethiopia. There were some limited to only dry phase production under irrigation; studies on vegetable fields were not continuous and insufficient, and none focused on green peppers, which require well-drained soils or climate conditions to escape from disease. Thus, the objective of this study is to investigate the impacts of CA on water dynamics (runoff, percolation, irrigation) and nutrient (nitrate and phosphorous removals) dynamics, and its contribution to improve crop (local green pepper, Capsicum annuum L.) yields under supplemental irrigation and rainfed systems. The results from this study contribute to the comprehensive evaluation and understanding of the CA system for improving productivity, water quality, ecosystem services, and the livelihood of people.

2. Materials and Methods

2.1. Description of the Study Area

The study area is located in the Dengeshita experimental site in the headwaters of the Blue Nile in the Northern Ethiopian highlands (11.32° N and 36.85° E at an altitude of 2042 m), 80 km south of Bahir Dar, the capital of the Amhara region (Figure 1). Dengeshita has a gentle slope (2% to 5%) with a mean annual rainfall of 1400 mm and a temperature of 18 °C based on data from the Ethiopian National Meteorological Agency, Bahir Dar District. The top 40 cm soil has a loam soil texture, and the interplot variation of soil texture was insignificant based on initial soil analysis results. The soil is slightly acidic with a pH level of 6. Field capacity, permanent wilting point, available soil water, bulk density, total nitrogen, available phosphorus, and available potassium in the top 40 cm soil layer were 0.31 cm3 cm−3, 0.21 cm3 cm−3, 0.10 cm3 cm−3, 1.32 g cm−3, 0.93 g kg−1, 9.57 mg kg−1, and 191 mg kg−1, respectively. Detail soil characteristics of the study site can be found in Belay et al. [27].

2.2. Experimental Design and Layout

A total of 10 experimental plots were established on 100 m2 in size, where 50 m2 was randomly assigned for conservation agriculture (CA) and another 50 m2 for conventional tillage (CT) practice under a supplementary irrigated phase (Figure 1a,b). The experimental plots were initially selected based on the availability of productive shallow groundwater wells adjacent to irrigable farms and farmers’ willingness to participate in the experiment. CA consists of no-tillage and the application of grass mulch at the rate of 2 t ha−1, while CT is the current farmers’ practice of 4–6 tillage frequencies (tillage depth 15−25 cm using animal drawn plough) and without mulch cover. A paired-t design was used to examine the impacts of CA on water use, runoff, leachate, nutrient use, and crop yield as compared to CT treatment. Irrigation water was managed by the estimated reference evapotranspiration based on the methods explained by Allen et al. [28]. The crop rotation (onion– pepper–garlic–pepper–onion–pepper) was the same for both CA and CT agricultural practices; however, only the pepper production period was used for this research paper. Drip irrigation was used for both 2018 and 2019 experimental years (from March to mid of June). Each treatment subplot was subjected to an equal amount of irrigation water for a week to ensure uniform recovery of transplanted seedlings.

2.3. Crop Management Practices

Local variety pepper (Capsicum annuum L.) was transplanted on 13 March in 2018 and 19 March in 2019 (Table 1). The spacing between rows and plants during transplanting was 40 cm. After transplanting, the initial stage lasted for 20 days; the vegetative stage lasted for 30 days; the mid-season growth stage (flowering and fruiting) lasted for 50 days; and the late-season stage lasted for 60 days. Inorganic fertilizer (diammonium phosphate (DAP) and urea) was not applied in the pepper growing period (the 2nd irrigation season) based on the local practice. However, urea fertilizer (46-0-0: N-P-K) was applied to the plots at the rate of 200 kg ha−1 using split application method (twice) during the 1st irrigation season from October to March. Sufficient phosphorus fertilizer was available in the soil based on a soil laboratory investigation [27]. The nutrient content of local grass and cow dung was analyzed at the soil laboratory. Local grass (85% organic matter; 0.18% total nitrogen, and 17 ppm available phosphorus,) was applied at the rate of 2 t ha−1 as mulch cover for only CA treatment twice per irrigation period. Compost of cow dung or manure (42% organic matter; 2.1% total nitrogen, and 82 ppm available phosphorus) was applied at the rate of 5 t ha−1 equally for both treatments at the end of the 1st season harvest. The harvesting period was from June to August for both 2018 and 2019. Farmers used 4 to 6 harvests in each season, and a fresh pepper yield was then weighed from each subplot during every harvest and converted to t ha−1.

2.4. Data Collection

Climate data used for calculating the reference evapotranspiration (ETo) with the FAO Penman–Monteith equation [28] were collected from Dangila weather station (15 km from the site) for the period of 1995–2016. We excluded the years 1998–2000 from the period because of the large amount of missing data. We used the average of these processed climate data, which include temperature (maximum and minimum), relative humidity, actual sunshine hours, and wind speed. Crop water use (ETc) was determined by multiplying ETo by the crop coefficient [28] for the initial, development, mid-season, and end stages. The same crop coefficient was used for the growth stages of pepper crop for the experimental years (i.e., 0.7 for initial, 0.95 for development, 1.05 for mid, and 0.7 for the late season). Irrigation water to be applied to the pepper was determined at an allowable constant soil moisture depletion fraction (p = 0.4) of the total available soil water (TAW), where TAW was determined from the permanent wilting point, field capacity, root depth, and bulk density variables. The depth of water applied during each irrigation event was the net irrigation requirement estimated by the Penman–Monteith method (using the long-term data from 1995 to 2016), and that which was needed for inefficiencies in the irrigation system. Considering conveyance and other losses for a drip system, an irrigation efficiency of 90% was assumed. The same amount of water (5 mm per irrigation on average) was applied in the 2018 and 2019 years with different irrigation scheduling. Irrigation was ceased immediately after the onset of rainfall in mid of May.
Runoff was measured using runoff collectors of a geomembrane sealed trench of size 0.5 m by 0.4 m by 1 m (200 L in capacity), installed at the end of each treatment bed (Figure 1b). One trench was used for a treatment where the runoff drains from 4 beds into the trench. It was recorded during every storm during daytime, and runoff collected during the nighttime was recorded in the morning. Each time after measurement, the trench was cleaned from incoming sediments. The amount of leachate was monitored every 10 days using a wetting front detector (WFD) installed 40 cm below the soil surface (Figure 1c), and evaporation loss for irrigated fields (wet) at this depth was neglected. Capillary rise of water from a 6–10 m water table through a sand filter (always wet for irrigated fields) was also assumed unrealistic. Water passing the fine sand filter was collected at the bottom of the WFD where a small hose was attached to it for draining out the leachate every 10 day using a syringe. The amount of leachate (mL) obtained in the area of the WFD was converted to millimeters of leachate by dividing the cross-section area (20 cm diameter) of the WFD. A water sample of 50 mL (20 mL for NO3-N, 10 mL for PO4-P) was collected from the runoff, as well as the leachate for determining the concentration of nutrients (i.e., NO3-N and PO4-P). Available phosphorus and NO3-N concentrations were determined using the Palintest photometer 7500 tests. The nitrate-nitrogen and available phosphorus loads were calculated by multiplying drainage volumes for each period with the corresponding measured NO3-N and PO4-P concentrations.
Total water used by the crop plus evaporation was calculated using the Penman–Monteith method as stated by Belay et al. [27]. Actual crop water used by the pepper for the growing season was computed using the soil water balance equation by Kresović et al. [29], as shown below:
T a = I + R f + C r − R o − P 40 ±   Δ S
where ETa is evapotranspiration (mm) during the growing season; I is the amount of irrigation water applied (mm); Rf is actual rainfall recorded at site (mm); Cr is the capillary rise (mm), considered to be zero because the groundwater table was >4 m below the surface in the growing months; P40 is percolation (mm), considered to be at a 40 cm soil depth because the soil water content below 40 cm reached field capacity during rainy season months on the sampling dates; Ro is runoff (mm), measured using runoff collectors because the field was saturated in rainy months (June to August), and ΔS is the change in soil moisture content (mm) measured using the gravimetric method at the time of transplanting and after harvest.

2.5. Data Analysis

All data are presented with arithmetic means and was statistically analyzed using a paired-t analysis for means after checking the normality using the Jarque–Berra method [30]. Phosphorus concentration data were transformed to natural logarithm to observe the normality. All the results shown in the tables and figures are means of treatment plots or replicates. Mean values were compared for any significant differences using the least significant difference (LSD α = 0.05) method.

3. Results

3.1. Irrigation and Rainfall Contributions in the Pepper Growing Period

The amount of rainfall during the growing period of pepper was 594 mm in 2018 and 618 mm in 2019. The contribution of irrigation in 2018 was 46% in the CA (370 mm) and 56% in the CT (476 mm); while in 2019 its contribution was 37% in the CA (255 mm) and 42% in the CT (288 mm) (Table 2). The pepper growth was supported by rain in the wet period (Figure 2). Irrigation water was significantly reduced (p < 0.05) under CA compared to CT management. The grass mulch and no-tillage practices under CA treatment decreased the interval of irrigation application and hence reduced irrigation water. The cumulative depth of irrigation application throughout the dry periods of the pepper growing period is plotted in Figure 2.
Year to year difference in the contribution of irrigation application was due to the difference in the time of transplanting pepper. To avoid drainage problems in the rainy period, farmers have practiced the transplanting of pepper at the beginning of March where the initial and development stages occurred in the drier months and the fruit stage occurred in the wet months (Table 1).

3.2. Effect of Conservation Agriculture on Water Dynamics (Runoff and Percolation/Leaching)

The average runoff depth for the 2018 and 2019 years were, respectively, 53 and 96 mm under CA and 80 and 124 mm under CT (Table 2). In 2018, a significant (p < 0.05) decrease in the average runoff depth (51%) was observed in CA (53 mm) as compared to the CT (80 mm) (Table 2). Similarly, in 2019, a significant (p < 0.05) decrease in runoff depth (29%) was observed in CA (96 mm) as compared to the CT (124 mm) (Table 2). The commutative of daily runoff and the rainfall (mm) records are plotted for both years in Figure 3. It shows that the runoff under CT is significantly greater compared to that under CA.
Overall, runoff in year 2019 was significantly greater than that of 2018 (Table 2) because of the difference in the planting date (Table 1) and the delays in the onset of the wet period, which can be related to a lower contribution of irrigation in 2019.
On the other hand, the quantity of leachate was significantly increased in the CA (8 mm) when compared to the CT (6 mm) for the 2018 experimental season (Table 2; Figure 4). Similarly, in 2019, a significant (p < 0.05) increase in leachate was observed in CA (7 mm) as compared to the CT (5 mm) (Table 2; Figure 4). The amount of leachate increased slowly during the dry season while it increased rapidly after the onset of the rainfall around the beginning of May (Figure 4). This supports the nature of complementary processes of runoff and percolation, where a decrease in the former corresponds to an increase in the later. The temporal variation shows that the maximum leachate depth occurred after 20 July over the growing periods and then started decreasing onwards (Figure 4).

3.3. Consumptive Water Use of Pepper (ETc) under Supplementary Irrigation

The water used by pepper from irrigation and rainfall, i.e., the actual evapotranspiration (ETa), was in the range of 750 to 950 mm and 600 to 850 mm, respectively in the years 2018 and 2019 (Figure 5). The maximum ETa in the CA management was 770 and 700 mm while it was 798 and 715 mm in CT, respectively, for the years 2018 and 2019. However, the difference between treatments in ETa was significant (p < 0.05) only for 2018 (Table 2). The yield of pepper was significantly greater in CA compared with CT management (Table 2). The average yield of pepper under CA was 11.7 t ha−1 in 2018 and 6.2 t ha−1 in 2019 while the yield was 9.1 t ha−1 in 2018 and 5.9 t ha−1 in 2019 under CT management. This shows that the yield achieved in 2018 under CA treatment was 30% higher compared to that of CT. In 2019, the yield of pepper was only 10% higher under CA compared to the CT. The yield difference was statistically different (p < 0.05) only for the 2018. The peak pepper yield in CA occurred ahead of CT management in response to lower optimum water use for the site conditions. However, the yield under CT management has continued even after the end of the last harvest of pepper (Figure 5). The yield results in Figure 4 and the runoff results in Table 2 agree in that runoff in 2018 was less than 2019; however, the yield in 2018 was higher when compared with the yield in 2019. This means that plots in 2019 were subjected to water logging problems. Based on farmers’ intrinsic knowledge, which is in line with [31], well-drained soil is suitable to pepper production.

3.4. Nitrogen (NO3-N) Dynamics

NO3-N concentrations in leachate (percolated water) during the whole pepper growth period under CA and CT practices are shown in Figure 6. The concentration of NO3-N in the leachate was greater in the CT management compared to in CA. At later crop growth stages, with an increased canopy cover, the difference in the concentration of NO3-N between the treatments was mostly minimum (Figure 6). The mean concentration of NO3-N in the leachate was 2.8 and 1.8 mg L−1 in the CA treatment and 3.2 and 2.6 mg L−1 in the CT, respectively for the 2018 and 2019 pepper growing seasons (Table 3). The mean NO3-N loss in the leachate was significantly (p < 0.05) reduced under CA (29%) when compared with CT treatment (Table 3). Correspondingly, the load of NO3-N in the leachate was 20.1 and 15.1 g ha−1 in the CA treatment and 21.6 and 16.6 g ha−1 in the CT for the cropping seasons of 2018 and 2019, respectively. When the amount of leachate decreased, the associated NO3-N concentration increased at early crop stages over the drier months, i.e., from the start of cultivation to the harvest of pepper (Figure 6). Nitrate concentrations in the leachate for both treatments were the highest at the beginning of the growing period and decreased at the end of the growing period as rainfall amount increases (Figure 6).
On the other hand, the concentration of NO3-N in the runoff was 0.3 and 0.4 mg L−1 in the CA and 0.6 and 0.8 mg L−1 in the CT, respectively for the 2018 and 2019 cropping seasons (Table 3). Consequently, the load (g ha−1) of NO3-N in the surface runoff was found 39% lower in CA when compared with CT (Table 3). The result indicates that NO3-N concentration was significantly (p < 0.5) lower in the runoff when compared with its concentration in the leachate.

3.5. Phosphorus (PO4-P) Dynamics

Available phosphorus below the 40 cm soil layer showed a decreasing trend from the dry to wet months of the 2018 and 2019 cropping seasons. The concentration of PO4-P decreased with an increase in the leachate in 2018 and 2019 (Figure 4 and Figure 7). Figure 7 shows the changes in PO4-P concentration over time in 2018 and 2019. The mean concentration of PO4-P was 1.2 and 0.80 mg L−1 in the CA and 0.8 and 0.6 mg L−1 in the CT, respectively for 2018 and 2019 cropping seasons (Table 4). The mean PO4-P concentration in the leachate in 2018 and 2019 was, respectively, 50% and 33% higher in CA as compared with CT, which is also significant (p < 0.05) (Table 4). Correspondingly, the load (g ha−1) of PO4-P in the leachate was 8.4 and 15.1 g ha−1 in the CA treatment and 5.6 and 16.6 g ha−1 in the CT, respectively for the 2018 and 2019 cropping seasons (Table 4). The PO4-P concentration was higher at early crop stages while the quantity of leachate decreased in the dry months (March to May).
On the other hand, the mean concentration of PO4-P in the runoff was 0.55 and 0.6 mg L−1 in CA and 0.64 and 0.7 mg L−1 in CT for the 2018 and 2019 cropping seasons, respectively (Table 4). The difference between CA and CT in the mean concentration of PO4-P in the runoff was statistically significant (p < 0.05) (Table 4). Similarly, the corresponding load (g ha−1) of PO4-P in the runoff was 243 and 501 g ha−1 in the CA, whereas it was 389 and 702 g ha−1 in the CT for 2018 and 2019 cropping seasons, respectively (Table 4), which is significant (p < 0.05).

4. Discussion

4.1. Effects of CA on Agricultural Water Management

Conservation agriculture (CA) showed reductions in irrigation water use and runoff while it has increased soil water/percolation in the root zone compared with conventional tillage (CT) (Table 2). This was potentially due to the protection provided by the mulch cover and due to the minimum disturbance of soil by no-tillage practices. The use of mulch reduces evaporation of water from the soil [32], reduces the runoff by absorbing the energy of raindrops, and increases the percolation of water by delaying the runoff [33]. No-tillage encourages less disturbance of soil pore networks and increases porosity, which then increases percolated water within the soil and reduces runoff [34]. This water flow within the root media again encourages an improvement in soil water use that reduces water stress of shallow rooted vegetable crops [20,35]. Irrigation water reduction of about 15% was reported under CA practice compared with CT in the dry phase of garlic production in similar growing conditions [27]. In agreement with this study, Babalola et al. [36] reported that vetiver grass mulch (2 tones ha−1) decreased the runoff by 62% compared to the control (CT) while another study indicated the reduction in runoff by the use of crop residue mulches [37].
As discussed earlier, our objective with the CA study is not only to investigate the pathways of surface water (runoff) but also to observe the water movement within the soil profile under vegetable fields. In this study, we observed increased percolated water under CA compared with CT because of the use of mulch cover and no-tillage practices (Table 2). A continuous application of grass mulch cover prevented the formation of soil crust, which contributes to the reduction in surface runoff and the increases effectiveness of the macroporosity of the soil that enhances percolation water. Edwards et al. [38] observed that large numbers of continuous macropores formed by burrowing earthworms were observed in the no-till watershed compared with the tilled one, and the authors speculated that no-till contributed to high infiltration rates. Moreover, the increased grass mulch cover of no-till soil may produce a cooler and wetter environment near the soil surface, which is more favorable for micro flora and faunal activity [39,40]. Less soil compaction as a result of no-tillage combined with grass mulch directly encourages microbial activities and can improve the vertical water movement within the soil structure [24]. In addition, the primary concern with CA practices is not only to investigate the pathways of surface and subsurface water over or within the soil but also to observe the quality of the dynamic movement of water in the soils of irrigated vegetable fields. Understanding how CA and CT practices affect the movement of water, however, allows us to concentrate on the factors most likely to influence nutrient movement under supplementary irrigated farms.

4.2. Effects of CA on the Nitrogen Movement

Conservation agriculture practices reduced the concentration of NO3-N in the leachate under a vegetable production system (Table 3), possibly due to grass mulch and no-tillage practices, both of which allow for minimum nutrient losses. More water applied in CT during dry irrigation months has probably increased the removal of NO3-N by leaching due to fertilizer turnover by tillage (Table 2). At later crop growth stages, with an increased canopy cover, the difference in the concentration of NO3-N between the treatments was minimum (Figure 6). The NO3-N flux in the root environment was greater for some weeks after transplanting, while it decreased subsequently as the vegetative cover of pepper increased. In line with this study, a study in China showed that the NO3-N concentrations in percolated water was in a regular decreasing pattern from drier to wetter phases of irrigated straw-mulched rice production [41]. Consistent result of NO3-N load in the leachate was also reported by Govaerts et al. [42] in the CA experiment conducted in Mexico. Our study results are in line with the study in Croatia [21]. In both years, the concentration of NO3-N in the runoff was lower in CA than in CT due to various possible reasons. In the context of CA, the method of fertilizer application and the minimum soil disturbance during crop cultivation were important since urea (46-0-0; N-P-K) fertilizer was locally applied to vegetables near the seedlings during the 1st irrigation phase. In this regard, more nutrient movement would be expected into the soil, not by the runoff. This is in agreement with the result of Yadav [43], which showed that 20% of the NO3-N that joins the groundwater came from the root zone for most of the crops. Another study indicated that grass mulch incorporated greater soil organic matter and NO3-N over surface soil layers, and this protected it from the runoff in the case of CA [44].

4.3. Effects of CA on Phosphorus Movement

In CA treatment, PO4-P concentration (mg L−1) and load (g ha−1) were higher in the leachate and decreased in the runoff compared with the CT treatment (Table 4). The higher PO4-P concentrations in the leachate may be attributed to its subsequent accumulation in the lower layers due to the higher water movement in the soil layer under CA practices. No-tillage combined with mulch, in general, is characterized by a higher phosphorus content in surface soil profile, which contributed to phosphorus dynamics within the soil layers compared to CT. Similar results have been also reported by Ben-Gal and Dudley [45]. A higher total phosphorus content was also reported in the soil surface layers under no-tillage compared to CT [46]. The higher phosphorus in no-tillage is mainly due to minimum soil disturbance, allowing for the accumulation of phosphorus fertilizer applied, as well as the phosphorus of mulch or crop residues added though time [47,48]. No-tillage combined with grass mulch practices are also suitable for the transformation of inorganic phosphorus (P) added through the fertilizer into organic forms, thereby increasing biological P reactions in the soil surface layer [49]. PO4-P concentration showed signs of decrease from the initial crop stage to harvest, in which case the concentration at each observation dates is higher for CA compared with that for CT (Figure 7). PO4-P concentration decreased from the dry irrigation phase to the wet rainy period where rainfall was in excess. The reason for this may be the increase in nutrient uptake by the crop and the cumulative removal of PO4-P by the runoff and leachate.

4.4. Effects of CA on Pepper Yield

Conservation agriculture, apart from numerous other advantages, improved yield and the early maturity of pepper compared with conventional tillage treatment (Figure 5), which is consistent with the results of Ravinderkumar et al. [50], showing that the application of organic mulches resulted in the flowering of tomatoes in fewer days after transplanting compared with the control management. In both years of this study, most of the initial and development stages of pepper were sufficiently supported by irrigation, and the fruit filing stages were supported by rainfall in both treatments. However, the yield achieved in CA treatment for 2018 and 2019 was higher compared with CT. The yield variation between the treatments was caused by the conducive soil moisture availability under CA management due to the use of grass mulch and minimum soil disturbance, particularly at the initial and development stages during the dry phase.
In 2019, the yield of pepper was lower than the yield in 2018, which may be attributed to the period of transplanting pepper relative to the rainfall onset. In 2019, transplanting was done one week later than 2018; it received more rainfall and was exposed to overwatering during fruit filing stage. As indicated before, the contribution of irrigation was higher in 2018 (46% for CA and 56% for CT) compared with 2019 (35% for CA and 37% for CT) for both treatments. In agreement with this study, Jaimez et al. [51] revealed that a water deficit and overwatering during the period of flowering and the fruit development stages reduced pepper fruit production. The authors, in addition, concluded that the transplanting of pepper about 2 months before a rainy season can improve the yield since the rain season coincides with flowering and fruit development stages [51]. Conversely, these stages are also critical, and water availability in the root zone in the dry phase is essential in order to avoid a significant decrease in fruit production, which was maintained by CA practices in this study. It has been observed that under CA practice, 20–40 mm additional water was stored in the root zone, especially in the lower root–soil layers, which is beneficial at the grain filling stage of the crop [27]. Wale et al. [52] also noted that the optimum crop water requirement of green pepper lies between 300 and 700 mm depending on the climatic conditions.

5. Conclusions

In this study, we observed that CA practices increased yields, reduced irrigation water, reduced runoff and the associated NO3-N in the leachate and runoff compared to CT. The average of the two years indicated a 20% increase in yields, 21% decrease in irrigation water, 40% lower runoff, 38% higher percolation, 29% lower NO3-N in the leachate, and 100% lower NO3-N in the runoff under CA compared with CT. In contrast, PO4-P concentration in CA was higher in the leachate but lower in the runoff. While N dynamics in the root zone indicated a decreasing rate with time, the phosphorus dynamics were not consistent across CA or CT. The observed responses of runoff, leachate, yield and nutrient dynamics under CA in this research provided a better understanding on the response of pepper to CA and the associated benefits in terms of increased yield as well as lower irrigation water and nutrient losses. We conclude that in supplementary irrigation vegetable production systems, CA can provide opportunities to optimize water use by decreasing irrigation water requirements and optimize nutrient use by decreasing nutrient losses through runoff and leaching. These best management practices will not only improve yield and efficiency of inputs (water and nutrient) but also decrease pollution and protect our environment.

Author Contributions

S.A.B. has contributed to the conceptualization, methodology, investigation, data collection, and acquisition, data analysis, writing the original draft manuscript in scientific content. T.T.A. contributed to revising the manuscript for the intellectual content. P.S. contributed to the methodology and revising of the manuscript. A.W.W. and P.V.V.P. contributed to the revising and editing of the manuscript. T.S.S. contributed to the rewriting of the manuscript to the scientific content. M.R.R. contributed to the conceptualization and design of the experiment. S.A.T. contributed to the conceptualization, data collection, acquisition framework, supervision, project administration, funding acquisition and rewriting the manuscript to the scientific content. All authors have read and approved the final version of the manuscript.

Funding

This research was funded by the American people through support by the United States Agency for International Development (USAID) Feed the Future Innovation Lab for Collaborative Research on Sustainable Intensification (Cooperative Agreement No. AID-OAA-L-14-00006, Kansas State University) through Texas A&M University’s Sustainably Intensified Production Systems and Nutritional Outcomes, and University of Illinois Urbana-Champaign’s Appropriate Scale Mechanization Consortium projects. The contents are the sole responsibility of the authors and do not necessarily reflect the views of funding agencies or represented organizations.

Acknowledgments

This research is made possible by the generous support of the American people through support by the United States Agency for International Development (USAID) Feed the Future Innovation Lab for Collaborative Research on Sustainable Intensification. Additional support was received of the CGIAR Research Program on Water, Land and Ecosystems (WLE) supported by donors to CGIAR. The contents are the sole responsibility of the authors and do not necessarily reflect the views of USAID. The authors would also like to acknowledge the Blue Nile Water Institute and Bahir Dar Institute of Technology for sponsoring the project. Contribution number is 21-008-J from the Kansas Agricultural Experiment Station.

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. Rockström, J.; Kaumbutho, P.; Mwalley, J.; Nzabi, A.; Temesgen, M.; Mawenya, L.; Barron, J.; Mutua, J.; Damgaard-Larsen, S. Conservation farming strategies in East and Southern Africa: Yields and rain water productivity from on-farm action research. Soil Tillage Res. 2009, 103, 23–32. [Google Scholar] [CrossRef]
  2. Bekele, S.; Tilahun, K. Regulated deficit irrigation scheduling of onion in a semiarid region of Ethiopia. Agric. Water Manag. 2007, 89, 148–152. [Google Scholar] [CrossRef]
  3. Rockström, J. On-farm green water estimates as a tool for increased food production in water scarce regions. Phys. Chem. Earth Part B Hydrol. Oceans Atmos. 1999, 24, 375–383. [Google Scholar] [CrossRef]
  4. Lanckriet, S.; Araya, T.; Cornelis, W.; Verfaillie, E.; Poesen, J.; Govaerts, B.; Bauer, H.; Deckers, J.; Haile, M.; Nyssen, J. Impact of conservation agriculture on catchment runoff and soil loss under changing climate conditions in May Zeg-zeg (Ethiopia). J. Hydrol. 2012, 475, 336–349. [Google Scholar] [CrossRef] [Green Version]
  5. Bosch, D.D.; Potter, T.L.; Truman, C.C.; Bednarz, C.W.; Strickland, T.C. Surface runoff and lateral subsurface flow as a response to conservation tillage and soil-water conditions. Trans. ASAE 2005, 48, 2137–2144. [Google Scholar] [CrossRef]
  6. Tomer, M.; Moorman, T.; Kovar, J.; Cole, K.; Nichols, D. Eleven years of runoff and phosphorus losses from two fields with and without manure application, Iowa, USA. Agric. Water Manag. 2016, 168, 104–111. [Google Scholar] [CrossRef] [Green Version]
  7. Grandy, A.S.; Loecke, T.D.; Parr, S.; Robertson, G.P. Long-term trends in nitrous oxide emissions, soil nitrogen, and crop yields of till and no-till cropping systems. J. Environ. Qual. 2006, 35, 1487–1495. [Google Scholar] [CrossRef] [Green Version]
  8. Assefa, T.; Jha, M.; Reyes, M.; Worqlul, A. Modeling the impacts of conservation agriculture with a drip irrigation system on the hydrology and water management in Sub-Saharan Africa. Sustainability 2018, 10, 4763. [Google Scholar] [CrossRef] [Green Version]
  9. Bot, A.; Benites, J. The Importance of Soil Organic Matter: Key to Drought-Resistant Soil and Sustained Food Production; Food and Agriculture Organization of the United Nations: Rome, Italy, 2005. [Google Scholar]
  10. Carpenter, S.R.; Caraco, N.F.; Correll, D.L.; Howarth, R.W.; Sharpley, A.N.; Smith, V.H. Nonpoint pollution of surface waters with phosphorus and nitrogen. Ecol. Appl. 1998, 8, 559–568. [Google Scholar] [CrossRef]
  11. Logan, T.J. Agricultural best management practices for water pollution control: Current issues. Agric. Ecosyst. Environ. 1993, 46, 223–231. [Google Scholar] [CrossRef]
  12. Pretty, J.; Toulmin, C.; Williams, S. Sustainable intensification in African agriculture. Int. J. Agric. Sustain. 2011, 9, 5–24. [Google Scholar] [CrossRef]
  13. Matson, P.A.; Parton, W.J.; Power, A.G.; Swift, M.J. Agricultural intensification and ecosystem properties. Science 1997, 277, 504–509. [Google Scholar] [CrossRef] [Green Version]
  14. Heathwaite, A.L.; Johnes, P.J. Contribution of nitrogen species and phosphorus fractions to stream water quality in agricultural catchments. Hydrol. Process. 1996, 10, 971–983. [Google Scholar] [CrossRef]
  15. Assefa, T.; Jha, M.; Reyes, M.; Srinivasan, R.; Worqlul, A.W. Assessment of suitable areas for home gardens for irrigation potential, water availability, and water-lifting technologies. Water 2018, 10, 495. [Google Scholar] [CrossRef] [Green Version]
  16. Assefa, T.T. Experimental and Modeling Evaluation of Conservation Agriculture with Drip Irrigation for Small-Scale Agriculture in Sub-Saharan Africa. North. Ph.D. Thesis, Carolina Agricultural and Technical State University, Greensboro, NC, USA, 2018. [Google Scholar]
  17. Lal Bhardwaj, R. Effect of mulching on crop production under rainfed condition—A review. Agric. Rev. 2013, 34, 188–197. [Google Scholar] [CrossRef]
  18. Giller, K.E.; Corbeels, M.; Nyamangara, J.; Triomphe, B.; Affholder, F.; Scopel, E.; Tittonell, P. A research agenda to explore the role of conservation agriculture in African smallholder farming systems. Field Crops Res. 2011, 124, 468–472. [Google Scholar] [CrossRef] [Green Version]
  19. Araya, T.; Cornelis, W.M.; Nyssen, J.; Govaerts, B.; Gebregziabher, T.; Oicha, T.; Getnet, F.; Raes, D.; Haile, M.; Sayre, K.D.; et al. Impact of Conservation Agriculture on Runoff, Soil Loss and Crop Yield on a Vertisol in the Northern Ethiopian Highlands. In Proceedings of the 19th World Congress of Soil Science, Soil Solutions for a Changing World, Brisbane, Australia, 1–6 August 2010. [Google Scholar]
  20. Tesfaye, A.; Cornelis, W.M.; Nyssen, J.; Govaerts, B.; Bauer, H.; Gebregziabher, T.; Oicha, T.; Rates, D.; Sayre, K.D.; Haile, M.; et al. Effects of conservation agriculture on runoff, soil loss and crop yield under rainfed conditions in Tigray, Northern Ethiopia. Soil Use Manag. 2011, 27, 404–414. [Google Scholar]
  21. Romic, D.; Romic, M.; Borosic, J.; Poljak, M. Mulching decreases nitrate leaching in bell pepper (Capsicum annuum L.) cultivation. Agric. Water Manag. 2003, 60, 87–97. [Google Scholar] [CrossRef] [Green Version]
  22. Thierfelder, C.; Wall, P.C. Effects of conservation agriculture techniques on infiltration and soil water content in Zambia and Zimbabwe. Soil Tillage Res. 2009, 105, 217–227. [Google Scholar] [CrossRef]
  23. Radford, B.J.; Thornton, C.M. Effects of 27 years of reduced tillage practices on soil properties and crop performance in the semi-arid subtropics of Australia. Int. J. Energy Environ. Econ. 2011, 19, 565. [Google Scholar]
  24. Blanco-Canqui, H.; Lal, R. Regional assessment of soil compaction and structural properties under no-tillage farming. Soil Sci. Soc. Am. J. 2007, 71, 1770–1778. [Google Scholar] [CrossRef] [Green Version]
  25. Ghosh, B.N.; Dogra, P.; Sharma, N.K.; Bhattacharyya, R.; Mishra, P.K. Conservation agriculture impact for soil conservation in maize-wheat cropping system in the Indian sub-Himalayas. Int. Soil Water Conserv. Res. 2015, 3, 112–118. [Google Scholar] [CrossRef] [Green Version]
  26. Assefa, T.; Jha, M.; Reyes, M.; Tilahun, S.; Worqlul, A.W. Experimental evaluation of conservation agriculture with drip irrigation for water productivity in Sub-Saharan Africa. Water 2019, 11, 530. [Google Scholar] [CrossRef] [Green Version]
  27. Belay, S.A.; Schmitter, P.; Worqlul, A.W.; Steenhuis, T.S.; Reyes, M.R.; Tilahun, S.A. Conservation agriculture saves irrigation water in the dry monsoon phase in the Ethiopian highlands. Water 2019, 11, 2103. [Google Scholar] [CrossRef] [Green Version]
  28. Allen, R.; Pereira, L.; Raes, D.; Smith, M. Guidelines for Computing Crop Water Requirements. FAO Irrigation and Drainage Paper 56. Available online: http://www.fao.org/docrep (accessed on 16 March 2020).
  29. Kresović, B.; Tapanarova, A.; Tomić, Z.; Životić, L.; Vujović, D.; Sredojević, Z.; Gajić, B. Grain yield and water use efficiency of maize as influenced by different irrigation regimes through sprinkler irrigation under temperate climate. Agric. Water Manag. 2016, 169, 34–43. [Google Scholar] [CrossRef]
  30. Jarque, C.M.; Bera, A.K. Efficient tests for normality, homoscedasticity and serial independence of regression residuals. Econ. Lett. 1980, 6, 255–259. [Google Scholar] [CrossRef]
  31. Aliyu, L. Effect of organic and mineral fertilizers on growth, yield and composition of pepper (Capsicum annuum L.). Biol. Agric. Hortic. 2000, 18, 29–36. [Google Scholar] [CrossRef]
  32. Diaz, F.; Jimenez, C.C.; Tejedor, M. Influence of the thickness and grain size of tephra mulch on soil water evaporation. Agric. Water Manag. 2005, 74, 47–55. [Google Scholar] [CrossRef]
  33. Mohammad, A.G.; Adam, M.A. The impact of vegetative cover type on runoff and soil erosion under different land uses. Catena 2010, 81, 97–103. [Google Scholar] [CrossRef]
  34. Kabir, Z. Tillage or no-tillage: Impact on mycorrhizae. Can. J. Plant Sci. 2005, 85, 23–29. [Google Scholar] [CrossRef] [Green Version]
  35. Stroosnijder, L. Modifying land management in order to improve efficiency of rainwater use in the African highlands. Soil Tillage Res. 2009, 103, 247–256. [Google Scholar] [CrossRef]
  36. Babalola, O.; Oshunsanya, S.; Are, K. Effects of vetiver grass (Vetiveria nigritana) strips, vetiver grass mulch and an organomineral fertilizer on soil, water and nutrient losses and maize (Zea mays L) yields. Soil Tillage Res. 2007, 96, 6–18. [Google Scholar] [CrossRef]
  37. Erenstein, O. Crop residue mulching in tropical and semi-tropical countries: An evaluation of residue availability and other technological implications. Soil Tillage Res. 2002, 67, 115–133. [Google Scholar] [CrossRef]
  38. Edwards, W.M.; Norton, L.D.; Redmond, C.E. Characterizing macropores that affect infiltration into non-tilled soil. Soil Sci. Soc. Am. J. 1988, 52, 483–487. [Google Scholar] [CrossRef]
  39. Drees, L.R.; Karathanasis, A.D.; Wilding, L.P.; Blevins, R.L. Micromorphological characteristics of long-term no-till and conventionally tilled soils. Soil Sci. Soc. Am. J. 1994, 58, 508–517. [Google Scholar] [CrossRef]
  40. Pagliai, M.; Raglione, M.; Panini, T.; Maletta, M.; La Marca, M. The structure of two alluvial soils in Italy after 10 years of conventional and minimum tillage. Soil Tillage Res. 1994, 34, 209–223. [Google Scholar] [CrossRef]
  41. Zheng, C.; Zhang, Z.; Wu, Y.; Mwiya, R. Response of vertical migration and leaching of nitrogen in percolation water of paddy fields under water-saving irrigation and straw return conditions. Water 2019, 11, 868. [Google Scholar] [CrossRef] [Green Version]
  42. Govaerts, B.; Sayre, K.D.; Goudeseune, B.; De Corte, P.; Lichter, K.; Dendooven, L.; Deckers, J. Conservation agriculture as a sustainable option for the central Mexican highlands. Soil Tillage Res. 2009, 103, 222–230. [Google Scholar] [CrossRef]
  43. Yadav, S.N. Formulation and estimation of nitrate-nitrogen leaching from corn cultivation. J. Environ. Qual. 1997, 26, 808–814. [Google Scholar] [CrossRef]
  44. Larsson, A. The Effect of Agricultural Intensification on Nitrate Concentrations in Shallow Groundwater in Two Watersheds in Ethiopia. Master’s Thesis, Uppsala Universitet, Uppsala, Sweden, June 2019. [Google Scholar]
  45. Ben-Gal, A.; Dudley, L.M. Phosphorus availability under continuous point source irrigation. Soil Sci. Soc. Am. J. 2003, 67, 1449–1456. [Google Scholar] [CrossRef]
  46. Bolliger, A.; Magid, J.; Amado, J.C.T.; Neto, F.S.; dos Santos Ribeiro, M.D.F.; Calegari, A.; Ralisch, R.; de Neergaard, A. Taking stock of the Brazilian “zero-till revolution”: A review of landmark research and farmers’ practice. Adv. Agron. 2006, 91, 47–110. [Google Scholar]
  47. Tiecher, T.; dos Santos, D.R.; Calegari, A. Soil organic phosphorus forms under different soil management systems and winter crops, in a long-term experiment. Soil Tillage Res. 2012, 124, 57–67. [Google Scholar] [CrossRef] [Green Version]
  48. Redel, Y.D.; Rubio, R.; Rouanet, J.L.; Borie, F. Phosphorus bioavailability affected by tillage and crop rotation on a Chilean volcanic derived Ultisol. Geoderma 2007, 139, 388–396. [Google Scholar] [CrossRef]
  49. dos Santos Rheinheimer, D.; Anghinoni, I. Accumulation of soil organic phosphorus by soil tillage and cropping systems under subtropical conditions. Commun. Soil Sci. Plant Anal. 2003, 34, 2339–2354. [Google Scholar] [CrossRef]
  50. Ravinderkumar, S. Influence of different mulches on flowering an fruit setting of winter tomato. Crop Res. 1998, 12, 174–176. [Google Scholar]
  51. Jaimez, R.; Vielma, O.; Rada, F.; García-Núñez, C. Effects of water deficit on the dynamics of flowering and fruit production in Capsicum chinense Jacq in a tropical semiarid region of Venezuela. J. Agron. Crop Sci. 2000, 185, 113–119. [Google Scholar] [CrossRef]
  52. Wale, A.; Girmay, G. Determination of irrigation regime for hot pepper (Capsicum annum L.) in dry-land areas of Wag-Himra, North Eastern Amhara, Ethiopia. Arch. Agric. Environ. Sci. 2019, 4, 101–108. [Google Scholar] [CrossRef]
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Figure 1. Location map of the experimental site (a) and layout of conservation agriculture (CA) and conventional tillage (CT) treatments (a,b) and wetting front detector (WFD) (c). The bottom arrows (b) indicate the direction of runoff flows relative to the runoff collector.
Figure 1. Location map of the experimental site (a) and layout of conservation agriculture (CA) and conventional tillage (CT) treatments (a,b) and wetting front detector (WFD) (c). The bottom arrows (b) indicate the direction of runoff flows relative to the runoff collector.
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Figure 2. Cumulative rainfall versus irrigation water applied for conservation agriculture (CA) and conventional tillage (CT) for the experimental years of 2018 (a) and 2019 (b).
Figure 2. Cumulative rainfall versus irrigation water applied for conservation agriculture (CA) and conventional tillage (CT) for the experimental years of 2018 (a) and 2019 (b).
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Figure 3. Comparison of cumulative daily runoff depth between CA and CT treatments for 2018 (a) and 2019 (b) during the growth period of pepper.
Figure 3. Comparison of cumulative daily runoff depth between CA and CT treatments for 2018 (a) and 2019 (b) during the growth period of pepper.
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Figure 4. Percolated water (leachates) measured every 10 days of the experimental periods of 2018 (a) and 2019 (b) for CA and CT management.
Figure 4. Percolated water (leachates) measured every 10 days of the experimental periods of 2018 (a) and 2019 (b) for CA and CT management.
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Figure 5. The relationship between evapotranspiration and pepper yield based on the data from replicated subplots of conservation agriculture (CA) and conventional tillage (CT) treatments conducted in 2018 and 2019 experimental years.
Figure 5. The relationship between evapotranspiration and pepper yield based on the data from replicated subplots of conservation agriculture (CA) and conventional tillage (CT) treatments conducted in 2018 and 2019 experimental years.
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Figure 6. NO3-N concentration (mg L−1) in the leachate; data collected every 10 days during pepper production period under conservation agriculture (CA) and conventional tillage (CT) treatments in 2018 (a) and 2019 (b) experimental years.
Figure 6. NO3-N concentration (mg L−1) in the leachate; data collected every 10 days during pepper production period under conservation agriculture (CA) and conventional tillage (CT) treatments in 2018 (a) and 2019 (b) experimental years.
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Figure 7. The concentration of PO4-P (mg L−1) in the leachate under CA and CT for 2018 (a) and 2019 (b).
Figure 7. The concentration of PO4-P (mg L−1) in the leachate under CA and CT for 2018 (a) and 2019 (b).
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Table
Table 1. Experimental activities of 2018 and 2019 green pepper cropping seasons.
Table 1. Experimental activities of 2018 and 2019 green pepper cropping seasons.
YearCropManagement ActivitiesDateMethods and Tools
2018Local variety pepper (Capsicum annuum L.) Seedling20 January 2018Watering-can
Cow dung application5 February 2018Manual
Tillage10–20 February 2018Draught animal
Planting13 March 2018Manual
Mulch application12 March 2018Manual
Irrigation13 March 2018–12 May 2018Drip irrigation
Weeding/hoeing20 April 2018, 5 May 2018, 10 July 2018Handpick
Harvesting1 June 2018–25 August2018Handpick
2019Local variety pepper (Capsicum annuum L.)Seedling9 January 2018Watering-can
Cow dung application5 February 2018Manual
Tillage15–25 February 2019Draught animal
Planting19 March 2019Manual
Mulch application12 March 2019Manual
Irrigation19 March 2019–18 May 2019Drip irrigation
Weeding/hoeing25 April 2018, 15 May 2018, 15 July 2019Handpick
Harvesting10 June 2019–29 August 2019Handpick
Table
Table 2. Mean (±standard deviation) for applied irrigation, runoff, percolation, crop water use (ETc), and fresh yield under conservation agriculture (CA) and conventional tillage (CT) treatment in the 2018 and 2019 supplementary irrigated pepper production period.
Table 2. Mean (±standard deviation) for applied irrigation, runoff, percolation, crop water use (ETc), and fresh yield under conservation agriculture (CA) and conventional tillage (CT) treatment in the 2018 and 2019 supplementary irrigated pepper production period.
Variables 20182019
CACTCACT
Applied irrigation (mm) 367.3 ± 55.4 b*475.4 ± 68 a254.8 ± 42.9 b287.8 ± 57.7 a
Rainfall (mm) **594.0594.0618.0618.0
Runoff (mm)53.2 ± 8.0 b80.1 ± 22.3 a95.5 ± 18.4 b123.6 ± 19.2 a
Percolation / leaching (mm)7.5 ± 2.4 a5.9 ± 1.9 b6.9 ± 1.6 a4.6 ± 2.4 b
Crop water used (ETc) (mm)796.7 ± 65.3 b855.6 ± 83.1 a678.7 ± 55.0 a686.6 ± 69.1 a
Fresh yield (t ha−1)11.7 ± 5.99.1 ± 4.36.2 ± 1.75.9 ± 2.3
Contribution of irrigation46%56%37%42%
* Numbers followed by the same letters under the same row heads in the same year are statistically nonsignificant at the α = 0.05 significant level. ** Rainfall is assumed the same for the village.
Table
Table 3. The mean concentration of nitrogen (NO3-N) in the leachate (mg L−1) and the corresponding load (g ha−1), as well as the concentration of NO3-N removed by surface runoff (mg L−1) and the corresponding load (g ha−1) for the two years in conservation agriculture (CA) and conventional tillage (CT) treatments.
Table 3. The mean concentration of nitrogen (NO3-N) in the leachate (mg L−1) and the corresponding load (g ha−1), as well as the concentration of NO3-N removed by surface runoff (mg L−1) and the corresponding load (g ha−1) for the two years in conservation agriculture (CA) and conventional tillage (CT) treatments.
Variables20182019
CACTCACT
NO3-N (leachate), mg L−12.8 ± 0.9 b3.2 ± 1.3 a1.8 ± 0.7 b2.6 ± 1.2 a
NO3-N (leachate), g ha−120.1 ± 7.8 b21.6 ± 9.1 a15.1 ± 12.8 b16.6 ± 16.2 a
NO3-N (runoff), mg L−10.3 ± 0.1 b0.6 ± 0.15 a0.4 ± 0.1 b0.8 ± 0.3 a
NO3-N (runoff), g ha−1148.8 ± 66.2 b384.0 ± 75 a333.7 ± 122 b866 ± 359 a
Numbers followed by the same letters under the same row heads in the same year are statistically nonsignificant at the α = 0.05 significant level.
Table
Table 4. The concentration of phosphorus (PO4-P) in the leachate (mg L−1) and its load (g ha−1), as well as the concentration of phosphorus (PO4-P) removed by surface runoff in (mg L−1) and the associated load (g ha−1) for the two treatments and under experimental years.
Table 4. The concentration of phosphorus (PO4-P) in the leachate (mg L−1) and its load (g ha−1), as well as the concentration of phosphorus (PO4-P) removed by surface runoff in (mg L−1) and the associated load (g ha−1) for the two treatments and under experimental years.
Variables20182019
CACTCACT
PO4-P (leachate), mg L−11.2 ± 0.7 a0.80 ± 0.4 b0.80 ± 0.5 a0.6 ± 0.3 b
PO4-P (leachate), g ha−18.4 ± 4.0 a5.6 ± 2.6 b15.1 ± 4.2 a16.6 ± 2.6 b
PO4-P (runoff), mg L−10.55 ± 0.1 a0.64 ± 0.15 b0.6 ± 0.2 a0.7 ± 0.3 b
PO4-P (runoff), g ha−1243 ± 66.2 a389 ± 75 b500.8 ± 215 a702.6 ± 312 b
Numbers followed by the same letters under the same row heads in the same year are statistically nonsignificant at the α = 0.05 significant level.

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Belay, S.A.; Assefa, T.T.; Prasad, P.V.V.; Schmitter, P.; Worqlul, A.W.; Steenhuis, T.S.; Reyes, M.R.; Tilahun, S.A. The Response of Water and Nutrient Dynamics and of Crop Yield to Conservation Agriculture in the Ethiopian Highlands. Sustainability 2020, 12, 5989. https://doi.org/10.3390/su12155989

AMA Style

Belay SA, Assefa TT, Prasad PVV, Schmitter P, Worqlul AW, Steenhuis TS, Reyes MR, Tilahun SA. The Response of Water and Nutrient Dynamics and of Crop Yield to Conservation Agriculture in the Ethiopian Highlands. Sustainability. 2020; 12(15):5989. https://doi.org/10.3390/su12155989

Chicago/Turabian Style

Belay, Sisay A., Tewodros T. Assefa, P. V. Vara Prasad, Petra Schmitter, Abeyou W. Worqlul, Tammo S. Steenhuis, Manuel R. Reyes, and Seifu A. Tilahun. 2020. "The Response of Water and Nutrient Dynamics and of Crop Yield to Conservation Agriculture in the Ethiopian Highlands" Sustainability 12, no. 15: 5989. https://doi.org/10.3390/su12155989

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