1 Introduction

The development of horticulture industries worldwide generates huge quantities of fruit wastes accounting for 25–30% of the total amount of processed fruits (Sagar et al. 2018). Apple pomace (AP) is a leftover biomass obtained during the processing of apple fruits to produce juice, cider, or wine. Several million metric tons of apple pomace are estimated to be generated globally each year (Lyu et al. 2020), and the amount is still increasing along with the world production of apples. The ways to dispose of apple pomace include its use for feeding livestock, composting, fuel production, and spraying as mulch for landfilling. However, the range of its applications is relatively small at present. Hence, other applications are required to solve the issue of disposal of excess apple pomace in a sustainable and environmentally friendly manner. The disposal of AP generates high costs due to its abundance and instability after tissue disintegration and the resulting altered activity of multiple enzymes (Krasowska and Kowczyk-Sadowy 2018). Therefore, appropriate management of these wastes is a very important issue. Intensive agricultural practices lead to soil degradation, which is often characterized by a decline in the content of soil organic matter, and the use of organic wastes in agriculture is one of the modes of recycling thereof (Diacono and Montemurro 2010). This is of particular importance in sandy soils characterized by low water holding capacity and cation exchange capacity. Due to the low organic matter content and poor fertility, these soils require large amounts of irrigation and fertilizer inputs. Application of exogenous organic matter (EOM) was shown to increase the fertility of intensively used lands and organic C (OC) sequestration (Montemurro et al. 2015; Goebel et al. 2011). Many experimental studies indicate that EOM stimulates soil microbial activity and thus influences soil respiration and N transformations (Wang et al. 2019). It was also found to improve the hydraulic properties of soil by influencing soil aggregation, pore structure, wettability, and repellency (Wang et al. 2000). Such properties of soil aggregates as wettability and infiltrability help to assess the water flow rates in the conductive pores inside the aggregates (Eynard et al. 2006). Limited aggregate wettability or repellency can lead to reduced hydraulic conductivity and water infiltration into the soil (Król et al. 2015); water losses through evaporation (Shokri and Or 2011); and increased surface runoff, erosion, and risk of contamination of surface waters. Furthermore, the mechanical stability of aggregates in response to soil water repellency can be reduced due to the loss of the stabilizing effect of water menisci or increased by lower aggregate breakdown and slaking through air entrapped during wetting (Lipiec et al. 2006). Additionally, aggregates diminish microbial decomposition of organic matter and have an impact on denitrification and N losses (Brzezińska et al. 2018).

Spring wheat and faba bean are important crops differing strongly in their demands for soil nitrogen and water use (Adams et al. 2018), i.e., factors affected by water deficit and addition of AP. However, due to the complexity of multiple interactions, the knowledge of processes involved in the overall impact of recyclable organic wastes on soils and crops is still poor. The high water and carbohydrate contents in AP are properties that strongly differ from other better recognized sources of EOM. This is probably the first such complex evaluation of the impact of the addition of raw unprocessed apple pomace to agricultural soils.

The objective of this study was to determine the effect of AP addition to sandy soil on microbial activity, N transformations, and hydrophysical properties of soil aggregates. We also tested the response of spring wheat and faba bean to AP application to soil with optimum and limited water availability. We hypothesized that (1) the addition of apple pomace to soil increases microbial activity, resulting in altered N transformations depending on the aggregate size. (2) The reduced N availability in the soil resulting from the AP addition and mild water deficit does not have a negative effect on legumes due to the symbiotic association with N-fixing bacteria.

2 Material and Methods

The soil used in the experiment was Podzol derived from loamy sand (Table 1). It was taken in early spring from a 0- to 30-cm-depth layer of a cultivated field (N 50.42947; E 22.60175). The soil was sieved through a 4-mm mesh to remove any debris. The soil size fractions were determined by a Mastersizer 2000 (Malvern, UK) laser diffractometer according to the procedure described by Ryżak and Bieganowski (2011). The apple pomace was the leftover of production of apple juice. It was stored in the freezer at a temperature of − 24 (± 2) °C until the beginning of the experimental procedures. The total phosphorus and potassium contents were determined colorimetrically and by flame photometry, respectively; the total N was measured according to the Kjeldahl method. The specific properties of both the soil and apple pomace are presented in Table 1.

Table 1 Selected properties of apple pomace and the soil
Full size table

2.1 Experiment I: Impact of AP on Artificial Soil Aggregates

The soil collected from the field was moistened to a field capacity, and nutrients were added in doses corresponding to N (NH4NO3) 30 kg ha−1, P (KH2PO4) 60 kg ha−1, K (K2SO4) 100 kg ha−1, and Mg (MgSO4 × 7 H2O) 25 kg ha−1. Unmodified apple pomace was added in the dose corresponding to 20 t of fresh mass per hectare (assuming that AP was mixed within the 0–10-cm top soil layer, 16.7 g of AP was added per 1 kg of soil). The artificial aggregates were formed from soil with and without AP using a 6- and 10-mm-thick acrylic glass plate with drilled 6- and 10-mm-diameter holes, according to the method proposed by Józefaciuk and Czachor (2014). The specified mass of the soil was manually pressed into the holes of the plates. Then, the cylindrical aggregates with 6 and 10 mm diameters with (AP+) and without apple pomace (AP−) were removed from the plates. The mass of the aggregates was checked to ensure uniform density (1.65 ± 0.1 Mg m−3).

Immediately after formation, 4 large (10 mm) or 16 small (6 mm) aggregates were carefully placed in 120-ml glass flasks. The total dry mass of the soil aggregates in the flasks ranged from approx. 4.6 to 5.4 g for the smaller and larger aggregates, respectively. The flasks were then airtight-closed for 2 h with a rubber cork prior to the first measurements of the cumulative CO2 concentration in the headspace. The concentration of CO2 was measured in 2 ml of gas sampled using a syringe on Shimadzu GC 14A equipped with a thermal conductivity detector (TCD). After sampling of the headspace gas, the flasks were covered with aluminum foil, in which approximately 10 small holes were made with a puncture needle. The holes allowed gas exchange at a limited rate of soil drying. Unavoidable water losses were corrected by daily watering to the initial weight using a pipette. The concentration of CO2 was repeatedly measured on the 1st, 2nd, 4th, 7th, and 21st day after the formation of the aggregates. Two hours before each measurement of the CO2 concentration, the flasks were airtight-closed with a rubber plug. Cumulative CO2 emission was used to assess the respiration rate of the soil aggregates (mg CO2-C kg−1 dry soil h−1). The aggregates used for the respiration and soil N measurements were stored in the dark at 24 °C day (14 h) and 18 °C night temperatures.

The impact of AP on soil N was evaluated by measurements of NO3−-N and NH4+-N in the soil aggregates. Twenty-four hours and 14 days after preparation, 20-g aggregates were frozen and kept at a temperature of − 24 (± 2) C prior to the measurements of the NO3−-N and NH4+-N concentrations. The concentration of NO3−-N and NH4+-N was determined in soil extracts (0.01 MCaCl2) using a flow-type spectrophotometric analyzer FIA-Star 5010 (Foss Tecator, Sweden).

Two sizes of artificially formed soil aggregates (6 and 10 mm) prepared according to the procedure described above were used for measurements of aggregate tensile strength, water and ethanol wetting rates, and the repellency index (RI). The measurements were performed after incubation for 90 days at room temperature (22 (± 2) °C). The water (Qw) and ethanol (Qe) wetting rates of the initially air-dried soil aggregate fractions were derived from the steady-state flow measurements conducted using an infiltration device (Lipiec et al. 2006). The rate of flow from the tube filled with either water or ethanol through the measured aggregate as a function of time was taken as a measure of the water wetting rate. The repellency index was the ratio of ethanol (not influenced by repellency) and water wetting rates calculated using a formula proposed by Leeds-Harrison et al. (1994). The RI (hydrophobicity) of the soil was taken as a ratio of Qw and Qe. Due to the very rapid disintegration, the ethanol wetting rate and RI were not measured for the smaller aggregates.

Crushing strength tests were performed using ZwickLine Testing Machine Z5.0 (ZwickRoell Testing Systems GmbH, Germany). The aggregates were crushed between two steel plates at the speed of 5 mm min−1, and the first peak of force recorded was used to calculate tensile strength.

2.2 Experiment II: Plant Response to AP

Faba bean (Vicia faba L.) cv. Granit and spring wheat (Triticum aestivum L.) cv. Kandela were used to study the impact of the apple pomace on plant growth. The faba bean seeds were noninoculated with Rhizobium. The plants were grown in cylinders with an inner diameter of 10 cm and a height of 40 cm filled with soil characterized by a moderate bulk density of 1.5 Mg m−3. The apple pomace was uniformly mixed with soil from the 0- to 10-cm layer in a dose corresponding to 20 t of fresh mass per ha. The soil was fertilized according to the crop demands to obtain 3 and 5 t of faba bean and spring wheat grain yields per hectare, respectively. Therefore, the doses of N, P, K, Mg, and S applied to the soil with faba bean were the same as in experiment I with the soil aggregates, and the dose of N in the soil with spring wheat was increased to 60 kg ha−1 (NH4NO3). The initial number of three seedlings of faba bean per pot was reduced to one soon after germination. In the spring wheat variant, the initial number of approx. 10 seedlings per pot was reduced to four after germination. The different number of plants per pot yielded similar plant biomass at the end of the experiment.

The conditions during the growth of both crops were as follows: day and night temperatures 24 °C (14 h) and 18 °C, photosynthetic active radiation 150 μmol photons m−2 s−1, and relative air humidity 60%. Both plant species were grown for 63 days and subjected to the following treatments: (1) C AP−: optimum soil water availability without addition of apple pomace; (2) C AP+: optimum soil water availability with addition of apple pomace; (3) D AP−: mild water deficit without addition of apple pomace; (4) D AP+: mild water deficit with addition of apple pomace. The soil water potential was maintained at the optimum level corresponding to field capacity at the soil water potential of − 33 kPa throughout the experimental period. Soil in the treatments with water deficit had an optimum water potential during the first 14 days after sowing; then, water deficit conditions were induced to maintain the soil water potential in the range from − 80 to − 60 kPa until cutting the plants at the end of the experiment. Specific soil water availability was maintained by watering the experimental cylinders to the specified weight every 24 h.

Leaf chlorophyll content was measured at day 63 using a Chlorophyll Content Meter CCM-300 (Opti-Sciences, Inc., USA) in the middle section of fully expanded leaves.

Leaf gas exchange was measured every fifth day starting from the beginning of limited watering. The measurement was conducted using a GFS3000 gas-exchange system equipped with a standard measuring head 3100-S (Walz GmbH, Germany). The conditions in the head chamber with the leaf were the same as in the growth chamber, and the CO2 concentration during the measurements was 400 ppm.

Leaf relative water content (RWC) was determined at day 63 in the first fully developed leaves. Excised leaves were immediately weighed to obtain fresh weight (FW), rehydrated in distilled water for 24 h, and weighed again to determine turgid weight (TW). Dry weight (DW) was determined after drying at 105 °C to constant mass. Relative water content was calculated using the equation: RWC = (FW − DW)/(TW − DW) • 100.

The presented data are the mean and standard error values (unless indicated otherwise) of the measurements of the plant or soil material (exact n is specified under the figures). Statistical analysis of the results was performed using confidence tests with the ANOVA analysis of variance (STATISTICA 13, StatSoft Inc.). Normality was evaluated using residual analysis (for n ≤ 4); in other cases (n > 4), the Shapiro-Wilk test was used. The means were compared with the use of the HSD Tukey test at p < 0.05.

3 Results

3.1 CO2 Respiration and N-Transformations in Soil Aggregates

The respiration rate in soil aggregates with both diameters formed without addition of AP was relatively constant throughout the 21-day period of the measurements (Fig. 1), with a mean of 3.8 and 3.3 mg CO2-C kg−1 h−1 for the 6- and 10-mm aggregates, respectively. The difference in the respiration rate between the small and large non-amended (AP−) aggregates was significant only at the beginning.

Fig. 1
figure 1

Respiration rate in 6-mm- and 10-mm-diameter cylindrical soil aggregates at 4 h (0 day) and on successive days after the formation of the aggregates from soil without apple pomace (AP−) and soil with the addition of apple pomace (AP+). The mean (n = 4) and standard error are shown; the different letters indicate statistical differences on the particular days at p < 0.05

Full size image

The level of CO2 evolved from the aggregates with AP (AP+) was significantly higher (p < 0.05) throughout the 21-day period with than without AP. The highest difference between AP+ and AP−, i.e., over 5.5 times and 4.0 times for the 6- and 10-mm aggregates, respectively, was noted after 24 h. Next, the differences between aggregates with and without AP slowly decreased but were still significant at the end of the incubation in both the smaller and larger aggregates.

Similar to the respiration rate, the decrease in the NO3−-N content occurred as early as 24 h after the addition of apple pomace (Fig. 2). The AP amendment significantly affected the nitrate-N and ammonium-N contents in the soil aggregates. Already, after 24 h, the concentration of NO3−-N was lower by 22% (8.1 mg kg−1) and 27% (10.5 kg−1) in the small and large AP+ aggregates, respectively, compared to the AP− aggregates. The differentiation in the N-ammonium concentration was even higher, as NH4+-N was by 87% (14.6 kg−1) and 91% (16.8 kg−1) lower in the small and large AP+ aggregates, respectively, compared to the AP− aggregates.

Fig. 2
figure 2

Concentration of nitrate-N (A, C) and ammonium-N (B, D) in 6-mm- and 10-mm-diameter artificial soil aggregates at 24 h (A, B) and on day 14 (C, D) after the formation of the aggregates without (AP−) and with apple pomace (AP+). The mean (n = 3) and standard error are shown; the different letters indicate statistical differences at p < 0.05

Full size image

After 14 days of incubation, the nitrate content in the AP− aggregates was slightly higher than initially, but strongly decreased in the AP+ aggregates. Therefore, the AP amendment resulted in a 93% and 78% decline in NO3−-N in the small and large AP+, respectively, compared to the AP− aggregates. The ammonium concentration strongly decreased in the AP− aggregates during the 14-day incubation period and apparently increased in the AP+ aggregates. Consequently, the level of NH4+-N differed significantly (3-fold), but only between the large AP− and AP+ aggregates.

3.2 Hydrophysical Properties of the Aggregates

Although the tensile strength of the aggregates was not affected by the apple pomace (Fig. 7, Appendix), the addition of AP significantly (p < 0.05) decreased the water wetting rate, as shown in Fig. 3. This reduction was more pronounced in the 10-mm aggregates (on average by 18.1%) than in the 6-mm ones (on average by 10.1%). In both treatments, the water wetting rate was higher in the larger aggregates. The ethanol wetting rate (measured only for the 10-mm aggregates) was not significantly different between the variants with and without the AP treatment. The repellency index (RI) for the 10-mm aggregates was significantly higher in the AP+ than AP− treatment.

Fig. 3
figure 3

Hydraulic properties of 6-mm and 10-mm soil aggregates with (AP+) and without apple pomace (AP−) after 90 days of incubation. The ethanol wetting rate and repellency index (RI) were not measured for the 6-mm aggregates due to their very rapid disintegration. The mean (n = 15–18) and standard error are shown; the different letters indicate statistical differences at p < 0.05 between objects with and without AP

Full size image

3.3 Growth of Spring Wheat and Faba Bean

The mild water deficit was induced to test the growth of plants in conditions that would additionally limit N availability. It was assumed that the reduced soil water availability decreased root water and dissolved nitrogen uptake. The measurements of leaf gas exchange (data not presented) showed that the average decline in transpiration from the first fully developed leaves of faba bean and spring wheat was approx. 38% and 25%, respectively, in the water deficit conditions, compared to the optimum conditions. The corresponding decrease in photosynthesis was much less pronounced and reached 1.9% and 12.9% for each of the crops.

The mild water deficit induced in the early growth stage had a significant negative impact on both crops. The results indicate that, for both of the crops, there was no significant impact of the AP addition to the soil on the aboveground plant biomass at the optimal soil water availability (Fig. 4). However, in the dry soil, there was a significant decline in the shoot biomass in the spring wheat growing in the soil with AP, compared to the AP− treatment. The growth of faba bean was not negatively influenced by the addition of AP to the dry soil; similarly, no significant response to AP was noted for the biomass of root nodules (Fig. 8, Appendix).

Fig. 4
figure 4

Shoot dry mass (SDM) of faba bean (A) and spring wheat (B) grown in the dry soil (D) and soil with optimum water availability (C) without (AP−) and with the addition of apple pomace (AP+). The mean for the plant species (n = 4 for faba bean and n = 16 for spring wheat) and standard error are shown; the different letters indicate statistical differences at p < 0.05

Full size image

The limitation in N availability to the plants in the presence of apple pomace was likely induced by the decrease in the NO3−-N content. This effect occurred in soil aggregates where a several-fold decrease in the NO3−-N concentration was noted after the addition of AP (Fig. 2).

The increase in the chlorophyll concentration in the leaves is an indirect indicator of the enhanced N uptake by faba bean from the AP+ soil (Fig. 5). Importantly, this effect was accompanied by an increase in shoot biomass (Fig. 4) at optimum and reduced water availability. In turn, no impact of the apple pomace on leaf chlorophyll was noted in wheat growing in the wet soil, but a significant drop occurred in the leaves of the plants grown in the dry soil with the AP addition.

Fig. 5
figure 5

Concentration of chlorophyll in the first fully developed leaves of faba bean (A) and wheat (B) grown in soil with optimum (C) and limited (D) water availability without (AP−) and with the addition of apple pomace (AP+). The mean (n = 12) and standard error are shown; the different letters indicate statistical differences at p < 0.05

Full size image

The comparison of the relative water content (RWC) in the leaves of the studied crops (Fig. 6) indicates that the intensity of water deficit was generally low, as the faba bean leaves did not exhibit any significant dehydration, compared to the control plants. The wheat leaves had significantly lower RWC when grown in the soil with restricted watering and addition of the apple pomace, while no differences were noted in the AP− treatments.

Fig. 6
figure 6

Relative water content (RWC) in the leaves of faba bean (A) and wheat (B) grown in soil with optimum (C) and limited (D) water availability without (AP−) and with the addition of apple pomace (AP+). The mean (n = 4) and standard error are shown; the different letters indicate statistical differences at p < 0.05

Full size image

4 Discussion

The addition of apple pomace stimulated microbial respiration of the aggregates due to the presence of easily available carbohydrates (Fig. 1). The decline in the nitrate content in the AP+ aggregates already after 24 h and, to a much greater extent, after 14 days of incubation was likely due to assimilation by the growing microbes. Simultaneously, the intensive respiration at the beginning of the incubation (see Fig. 1) suggests rapid oxygen uptake. In the anaerobic parts of the aggregates, following O2 depletion, facultative anaerobes shift their metabolism and use NO3− as electron acceptors during denitrification (Włodarczyk et al. 2014). The significant difference in the NH4+-N contents between the AP+ and AP− aggregates after 24 h of incubation may have been due to the intensive N assimilation associated with the rapid growth of microbial communities stimulated by apple pomace. After 14 days, AP added to the smaller aggregates (6 mm) had no impact on the NH4-N content, whereas the significant increase in the content of NH4+-N in the 10-mm AP+ aggregates may have resulted from dissimilatory nitrate reduction to ammonium (DNRA), which occurs in anaerobic conditions as an alternative mechanism to denitrification (Silver et al. 2001). Dissimilatory nitrate reduction to ammonium strongly increases in anaerobic soil amended with easily available C (Levy-Booth et al. 2014). In fact, the importance of DNRA in soil is its capacity to increase N retention, because nitrate is transformed to ammonium, which is less prone to losses via leaching or as gaseous compounds (Rütting et al., 2011). The core of the larger aggregate is more susceptible to anaerobic conditions due to the lower surface-to-volume ratio. The larger 10-mm aggregates were characterized by a nearly 2-fold lower ratio of the surface area to their volume than the 6-mm aggregates. Natural mineralization may also have been involved in the observed increase in the NH4+-N concentration (Carswell et al. 2018). Although the soil used in the experiment was characterized by the pH below optimum for denitrification (Table 1) it appears that high availability of carbon from AP and nitrate from fertilizer (NH4NO3) at anaerobic sites sufficiently stimulated the process. Čuhel et al. (2010) explained high denitrification rates in acid soil used in their experiment by nonlimiting denitrifying conditions, i.e., soil incubation at 25 °C with limited oxygen, addition of NO3− and glucose.

Decomposition processes in soil are controlled by the C/N ratio, and addition of fresh organic matter accelerates soil biogeochemical processes. When the C/N ratio in the added organic substrate ranges from 1 to 15, rapid mineralization and release of plant available N occurs (the lower the C/N ratio, the more rapid the release of available N into the soil), while the C/N ratio > 35 results in microbial immobilization (Brust 2019). Although apple pomace added in our study showed the C/N = 57.8, soil respiration was significantly higher in enriched aggregates over 21 days of the incubation. Soil microorganisms compete with plants for nitrogen and other nutrients in soil and decompose soil organic matter, plant litter, and organic residues with very wide C/N ratios (Vitousek et al. 2002). Therefore, the properties of added organic materials influence soil nutrient status. Huang et al. (2004) tested the effect of different plant residues (with a C/N ratio from 8 to 118) on CO2 and N2O emissions from soil (C/N of 12.8) and reported that cumulative gas emissions were negatively correlated with the C to N ratio in the added residues. Apparently, the incorporation of immature organic matter such as apple pomace (with C/N = 57.8) induced both microbial C and N transformations. Significant stimulation of soil respiration and the decrease in the nitrate content in the AP+ treatments were observed already at the beginning of the incubations (Figs. 2 and 3). Besides, AP+ had an adverse effect on wheat growth (Fig. 4b), which may suggest N-deficiency.

Since apple pomace was found to stimulate soil microbial activity and accelerate N transformation, its addition to soil may reduce NO3−-N and thus decrease the potential risk of N leaching. This can be clearly seen from the strong drop in NO3−-N on day 14 after application of AP (Fig. 2). Larney and Angers (2012) showed that EOM with low N content, as in the apple pomace, reduced N availability to plants mostly via stimulation of denitrification with formation of N2. On the other hand, apple pomace applied during aerobic composting of pig manure conserved NH4+-N and NO3−-N contents by inhibition of NH3 and N2O emission (Mao et al. 2017).

Soil aggregates are essential components affecting the soil structure. They determine the soil-water relationships, which are especially important during seedling establishment and early growth. Soil microorganisms can improve soil aggregate stability through production of extracellular polysaccharides. The increase in the microbial activity after the addition of AP was evidenced by the increase in the soil respiration rates (Fig. 1). Moreover, a positive correlation between aggregate stability and the dose of organic amendments was also observed in experiments on sandy loam textured soil with addition of various organic wastes, including AP (Yilmaz 2014).

The wetting rate is one of the soil aggregate characteristics that determines the stability of the soil structure (An and Liu 2017), especially during rainfalls when aggregate breakdown is caused by rapid release of entrapped air. We observed a decrease in the wetting rate of both aggregates (Fig. 3), indicating that addition of AP can decrease soil susceptibility to the erosion process. As demonstrated by Urbanek et al. (2007), aggregates from both treatments can be classified as subcritically water-repellent (1.95 < RI < 50). The approximately 34% increase in RI after the addition of apple pomace (Fig. 3) may have additional consequences for prediction of water flow in soil. Indeed, Vogelmann et al. (2017) observed that an altered RI of soil aggregates modifies the water infiltration behavior especially during droughts. The experiment conducted by Cesarano et al. (2016) showed that the increase in water repellency in sandy loam soil occurs independently of the plant litter type until it is in an undecomposed state. The increase in the repellency of the soil aggregates observed in our experiment after the apple pomace addition may depend on the decomposition of soil organic matter. Indeed, Goebel et al. (2011) suggested a close relationship between the stability of soil organic matter and water repellency, as the resistance of organic matter to microbial decomposition is increased in water-repellent soils. The non-statistically different (at p < 0.05) wetting rate of ethanol (which easily infiltrates hydrophobic soil) between the AP+ and AP− treatments (Fig. 3b) implies that the significantly lower water wetting rate of the AP+ vs. AP− aggregates (Fig. 3a) and the higher repellency index (RI) can be related to the increasing content of hydrophobic compounds from AP and enhanced microbial activity (Peng et al. 2003). Furthermore, the addition of organic C from AP characterized by low pH, at which the solubility of humid acids decreases and the surface tension of water increases (Hurraß and Schaumann 2006), can further elucidate the higher repellency index in the AP+ aggregates (Fig. 3). The increase in repellency can be enhanced by the low surface area of the coarse-textured soil used in this study, which requires a lower quantity of hydrophobic organic matter to coat soil particles, compared to fine-textured soil (Hajnos et al. 2013).

The addition of the AP to the soil had different effects on both studied crops. The faba bean biomass was not affected by AP, but the leaf chlorophyll content was higher in plants growing in soil with optimum soil water availability and AP addition. In turn, the spring wheat was affected by AP only in the dry soil, at which a negative impact of AP on biomass and leaf chlorophyll was noted. Crops are generally differentiated in their response to water deficit, and this relation depends on plant-soil microorganism interactions (Naylor and Coleman-Derr 2018).

Hirich et al. (2013) showed that organic amendment improved biomass production of quinoa under water deficit. In our study, faba bean responded better than the spring wheat to the mild water deficit in the soil amended with AP (Fig. 4). As shown by Zheng and Shetty (2000), the beneficial impact of AP on pea growth depended on the presence of Trichoderma species producing specific plant growth stimulating substances from AP. Although we did not examine the impact of the AP application on the biodiversity of soil microorganisms, the Trichoderma genus is common in soil and rhizosphere. Beneficial impact of soil the microorganism-plant interactions may have been enhanced after the AP application, resulting in increased microbial activity (Fig. 1) maintaining the growth of faba bean (Fig. 4) in the soil of limited N and water. In contrast to olive pomace amendment, which had no effect on available N in soil (Innangi et al. 2017), the AP application decreased the N availability to plants, especially in the drought conditions. As reported by Eschen et al. (2006), addition of easily available C to the soil decreases the inorganic N concentration due to immobilization of N by resident soil bacteria and fungi. In the conditions of their experiment, the growth of legumes appeared to be much less dependent on soil N than in the case of the grasses due to the symbiotic association with N-fixing bacteria in the root nodules of legumes. This may explain the higher chlorophyll concentration in the faba bean leaves (Fig. 5) and at the same time the lack of an adverse effect of the AP addition on faba bean growth. Additionally, as indicated earlier, water stress and nitrogen deficiency induced structural changes in nodule anatomy connected with changes in nitrogenase activity (Mrema et al., 1997).

5 Conclusions

The impact of apple pomace on the soil respiration and the concentration of nitrate and ammonium nitrogen in soil aggregates depends on their size, as larger aggregates are more susceptible to anaerobic conditions. The tensile strength of the aggregates in the present study was not affected by the apple pomace, whereas the water repellency index was higher in the apple pomace–amended than the non-amended soil. The decreased N availability related to the water deficit and addition of the AP to the soil exerted different effects on the growth of faba bean and spring wheat. A negative impact on the growth performance of wheat was noted in the apple pomace–amended soil in the water deficit conditions, but there was no such a negative response in the case of the faba bean due to the symbiotic association with N-fixing bacteria. Apple pomace had also a positive effect on the content of leaf chlorophyll in the faba bean. The results show that AP can be disposed of without any special pre-processing as a soil amendment under faba bean, irrespective of soil water availability. Further studies are needed to investigate inoculation of AP with plant growth-promoting microorganisms, which potentially may enhance crop yields.