Nitrogen Isotope Fractionation during Composting of Sewage and Agri-Food Sludge with Pruning Waste
by
, , , and
José Antonio Sáez
1
,
Pilar Flores
2,
María Ángeles Bustamante
1,*,
Juan C. Sanchez-Hernandez
3
,
Raúl Moral
1 and
María Dolores Pérez-Murcia
1 1
Department of Agrochemistry and Environment, Miguel Hernández University, EPS-Orihuela, Ctra. Beniel km 3.2, 03312 Alicante, Orihuela, Spain
2
Horticultural Sustainability and Quality Team, IMIDA, 30150 La Alberca, Murcia, Spain
3
Laboratory of Ecotoxicology, Institute of Environmental Science (ICAM), University of Castilla-La Mancha, 45071 Toledo, Spain
*
Author to whom correspondence should be addressed.
Agronomy 2020, 10(12), 1954; https://doi.org/10.3390/agronomy10121954
Submission received: 11 November 2020
/
Revised: 4 December 2020
/
Accepted: 8 December 2020
/
Published: 12 December 2020
(This article belongs to the Special Issue Recycling Agricultural, Industrial, and Municipal Byproducts While Enhancing Agricultural Production and Protecting the Environment – Volume I)
Abstract
:This work studies the changes in δ15N signature during the composting of sewage sludge (MS) and agri-food sludge (AS) with different bulking agents and the potential relationships between the changes in this parameter with both the source of the organic matter used as a raw material and the stability of the end-materials obtained. For this, eleven mixtures were prepared in commercial composting conditions using sewage sludge from municipal wastewater in a range of 60–85% (on a fresh weight basis) or agri-food sludge in a range of 65–75%, mixed with seven different pruning wastes as bulking agents. The thermal profile was monitored throughout the composting processes, and the main physico-chemical and chemical parameters were determined. The results obtained confirmed a correct development of the composting processes, observing slight differences in process evolution depending on the type of sludge used. The composts obtained showed adequate contents of nitrogen, phosphorus and potassium (NPK) and reached a good degree of maturity. Significant differences in the specific nitrogen isotopic composition were found in the initial materials. Moreover, the results suggest that the type of sludge had a main contribution in the δ15N value of the initial composting mixtures. The use of δ15N is recommended as an indicator of the composting process, especially to evaluate N dynamics, and the quality of the resultant compost.
1. Introduction
Composting constitutes one of the main treatments for the management and valorisation of a wide typology of organic wastes. Typical organic wastes used as raw materials in composting are animal manures and crop wastes [1,2,3], agro-industrial wastes [4,5], municipal solid wastes [6,7], sewage sludge [8,9] and agri-food sludge [10,11]. Moreover, there is extensive literature on the benefits of the use of compost as soil amendment, maintaining soil organic matter contents, sustaining crop productivity and improving soil quality, especially in the long-term, due to the slow release of nutrients [12,13]. Compost is one of the main sources of nitrogen, especially in agricultural systems, such as organic farming, where only organic amendments and specific fertilisers of natural origin are allowed [14]. However, currently there are no standard analytical techniques to identify the type of fertilisers used, which makes it difficult to detect the use of prohibited synthetic fertilisers in organic farming systems [14,15]. In this context, in the last decade, the use of the 15N natural abundance (δ15N), based on the use of the N isotope ratio (15N/14N) has emerged as a promising technique for discriminating between organically and conventionally grown crops [14,16]. The method is based on the higher δ15N values of composted materials with respect to synthetic fertilisers, because of the physical and biological processes that take place during composting, which leads to 15N isotope enrichment in favour to lighter 14N isotope [2]. Thus, the crops obtained using compost as organic fertiliser likely contain higher δ15N values in their tissues than those obtained with mineral fertilisers [16,17]. Accordingly, the 15N signature will be different in the soil and crops of a farming system, depending on the type of N source, reflecting the inputs of N fertilisers with different δ15N values [15,18]. Nevertheless, very few studies have dealt with δ15N dynamics during the composting and especially regarding the influence of the feedstock. Lynch et al. [19] studied the changes in δ15N during the composting of corn silage, reporting an increase in δ15N values and a reduction in the heterogeneity of the bulk organic material 15N signature. Kim et al. [2] evaluated the temporal changes during composting of livestock manure and the effect of the bedding material used, observing a clear effect of the bedding material on the δ15N of the composts obtained. Therefore, the aims of this work were twofold: (i) to examine the dynamics of the δ15N signature during composting of municipal sewage sludge (MS) and agri-food sludge (AS), mixed with different bulking agents; (ii) to establish potential relationships between δ15N signature and the properties of both the feedstock and the corresponding compost.
2. Materials and Methods
2.1. Composting Procedure
Eleven different commercial-scaled piles in trapezoidal form (25 m3 each pile) were prepared and composted using the passive windrow composting system with periodical mechanical turning. The main raw materials used in the elaboration of these composting mixtures were sewage sludge (MS) and agri-food sludge (AS), respectively. Four different MS were collected at different municipal wastewater treatment plants of Alicante (Spain). In all cases, the different MS samples were produced by aerobic treatment of wastewater, followed by a step of stabilization in anaerobic conditions. The four AS samples used come from the treatment of the wastewaters generated in two agri-food industries—i.e., pear and strawberry processing plant and dairy desserts—both located in Murcia (Spain). The treatment for these wastes consisted of three stages: a first stage of flotation by cavitation air supply (CAF), a second stage of denitrification in an anoxic reactor, and a later treatment in USBF reactor under aerobic conditions by forced aeration. The bulking agents used were different types of pruning wastes produced after park maintenance activities in the urban area of the municipality of Orihuela (Spain). These wastes were the following: tipa (Tipuana tipu) waste (TW); palm (Phoenix dactylifera L.) leaves (LP) and trunk (TP1, TP2, TP3 and TP4); giant reed (Arundo donax L.) waste (AD); cotton gin (CG); mulberry (Morus alba L.) waste (MA) and mixed garden pruning (GP). All these wastes were homogenised and crushed to <4 cm particle size, prior to the preparation of the composting mixtures in order to improve the homogeneity and aeration into the heaps. Table 1 summarises the mixtures of feedstocks and bulking agents on a fresh weight basis:
Moisture and temperature (piles and ambient) were periodically monitored throughout the composting process. Pile moisture was maintained at levels not less than 40%, while the temperature was registered using multiple probes connected to data loggers (HOBO-Data Logger). Four samples were conducted during the process (initial stage and maturity) obtaining the samples after mixing seven sub-samples collected the whole profile of each mixture and from seven sites [20]. Each pooled sample was divided into two fractions: the first fraction was dried at 105 °C for 24 h to determine the moisture contents, and the second fraction was dried at 45 °C, and ground using an agate ball mill (Frischt Pulverisette 3 SPARTAN) to obtain a sample of particle size < 0.5 mm, which was stored for later analyses.
2.2. Chemical Determinations
The physico-chemical and chemical parameters studied in the initial materials and composting samples were determined as follows: electrical conductivity (EC) and pH were measured in a 1:10 water-soluble extract (w/v), whereas organic matter (OM) content was determined by mass loss on ignition at 430 °C for 24 h. Total organic carbon (TOC) and total nitrogen (TN) were quantified using an automatic elemental microanalyser (EuroVector Elemental Analyser, Milano, Italy). The cation exchange capacity (CEC) was determined according to the method used by Bustamante et al. [20]. Na and K were measured by flame photometry (Jenway PFP7 Flame Photometer) after acid digestion (HNO3/HClO4, 1:4 v/v) of the sample, whereas P concentration was colorimetrically determined according to the method described in Bustamante et al. [20]. The phytotoxicity of composts was also determined by the germination index (GI) according to the method described by Zucconi et al. [21]. All the determinations were conducted in triplicate. TN losses were determined following Equation (1), where N1 and N2 are the initial and final TN contents, respectively, and X1 and X2 represent the initial and final ash contents [22]:
TN-loss (%) = 100 − 100 [(X1N2)/(X2N1)],
2.3. Determination of δ15N Signature in the Initial and Composting Materials
The samples were weighed (1–5 mg) with an accuracy of 0.001 mg (Mettler Toledo MX5), placed in tin capsules and measured using an EA1108 analyser (Carlo Erba Instruments) coupled to a MAT253 isotopic mass spectrometer (ThermoFinnigan) through a ConfloII interface. The molecules produced during the sample combustion are ionized and separated according of the masses of the constituent isotopes under the action of a magnetic field. The results of δ15N values are expressed in ‰ relative to atmospheric air. The accuracy of the method, evaluated by using the external standard acetanilide, resulted in ±0.15‰ (n = 10).
2.4. Statistical Analyses
The viability of the composting process was evaluated through the Quadratic Exothermic Index (EXI2), which was calculated as the quadratic sum of the daily difference between the temperature inside the pile and that in the surrounding environment during the bio-oxidative phase of composting [9]. The statistical analysis of the data was conducted using ANOVA followed by the least significant difference (LSD) test at p < 0.05. The Tukey-b test was used to check the statistically significant differences among feedstocks and composts in relation to the physico-chemical and chemical properties. The normality and homogeneity of the variances were checked using the Shapiro–Wilk and Levene test, respectively. In addition, factorial analysis (FA) was carried out to interpret the data set of initial mixtures and composted materials, initially considering all the parameters studied. However, the best results were obtained considering the following parameters: EC, OM, CEC, P, δ15N, TN and TOC. All statistical tests were conducted with the IBM SPSS 25 software package.
3. Results and Discussion
3.1. Chemical Characteristics and Isotopic Composition (δ15N) of the Initial Materials
Table 2 and Table 3 summarise the main chemical characteristics of the raw materials and bulking agents used in the composting mixtures. The different samples of MS and AS showed similar physico-chemical characteristics, with an acidic pH and electrical conductivity values varying between 3.4–5.8 dS/m (Table 2). However, AS samples showed higher contents of the organic matter fraction (69.4%) than MS samples (55.8%). Conversely, agri-food sludge samples had lower concentrations of N and K than MS samples and thus, lower δ15N mean values than MS samples (7.6 and 4.9‰, respectively). Moreover, the mean values of total nitrogen (TN) found in all the sludge samples were lower than those reported by Rigby et al. [23] in a review about biosolids from mesophilic anaerobic digestion treatment (7.5% TN). This discrepancy could be due to several sources of variation: (1) the source of N, (2) the proportion of N derived from the degradation of organic matter [24], and (3) the techniques used for producing and stabilizing each sludge. In our study, the higher δ15N mean values observed in the MS samples compared to AS samples could be explained by the stabilization technique used in each type of sludge. All the AS samples used in this study were stabilized in aerobic treatments. However, the stabilization of the MS samples was performed by anaerobic treatment, which could favour reduction conditions and, thus, the biological denitrification process. Consequently, the nitrogen is released as atmospheric N2 enriched in 14N and the values of δ15N in the remaining material increase [25]. Aside from AS3 (2.7‰), the range of the δ15N values determined in our sludge samples (6.1–8.5‰) was close to that found in other composting studies with N-rich organic wastes, such as livestock manures (δ15N = 5.3 and 7.2‰) [26]. Similarly, Choi et al. [27] and Kim et al. [2] reported close values of δ15N for cattle manure (7.5 and 7.9‰, respectively).
Regarding the selected characteristics of the bulking agents (Table 3), all the materials showed pH values close to neutrality; ranging from 5.5 (mulberry waste) to 7.3 (cotton gin waste). The electrical conductivity showed a larger variability range, with values from 1.4 dS/m in MA to >7 dS/m in the palm trunk wastes (PT). However, the organic matter contents were similar in the bulking materials (70–92%). In general, the concentrations of the macroelements studied (N, P, K and Na) did not differ much among them, except for the low TN values found in MA (0.7%) and the low P concentrations of MA (2.3 g/kg) and TW (3.2 g/kg). The δ15N mean value of pruning waste (8.0‰) was close to the values reported in previous studies. For example, Santiago et al. [28] found a similar value in a study about C3 metabolism bush plants (7.7‰). However, Barbanti et al. [3] reported 2.05‰ δ15N in C4 and CAM photosynthetic pathway metabolism plants, which was related to a more effective use of N, linked to mechanisms of C assimilation by tissues. In our study, the lowest value of δ15N corresponded to TW (2.6‰), which is in agreement with the results found by Santiago et al. [28] in leguminous species trees. It is postulated that the lower 15N natural abundance in leguminous species is due to symbiotic associations (root nodules) with Rhizobium group bacteria, which are capable of fixing atmospherics N2. Finally, it is interesting to remark the differences observed in the isotopic composition between the palm trunk samples (7.8, 10.5 and 8.5‰) and of the palm leaves (12.2‰). This tissue-specific difference in δ15N has also been documented in previous studies [24], and it is explained by tissue N redistribution. In both evergreen and deciduous species (caducifolias), the translocation of N from senescent leaves to new tissues increases the δ15N values during the assimilation of nitrate in leaf [29].
3.2. Thermal Development of the Composting Mixtures
The temperature in all the composting mixtures increased quickly, reaching thermophilic values (>40 °C) in the first week, these values lasting more than 30 days in all piles (Figure 1a,b). In general, the mixtures with MS showed temperature values >65 °C during a longer period than those with AS, although some of these piles showed higher temperature values. In addition, pile 5, containing MS, and pile 11, containing AS, remained more than 100 days with thermophilic temperature values. With this temperature dynamics, the Quadratic Exothermic Index (EXI2) (Vico et al., 2018) was used to describe, in detail, the exothermic behaviour of the composting mixtures. This parameter revealed marked differences in the exothermic behaviour between piles (Figure 2a,b). Pile 3 (MS and CG) and pile 8 (AS and PT) showed a faster increase in the temperature at the beginning of the process (Figure 2a,b), thus defining a short bio-oxidative phase with higher accumulated values of the index EXI2 at the end of this composting phase (Table 4). Some studies have reported the beneficial effects of adding bulking agents, such as cotton gin and palm tree wastes to the composting heap [1,9]. These materials generally provide an adequate physical structure in the mixture, thereby affecting the temperature reached during composting, requiring less energy to achieve maximum temperature values into the windrow. In general, the temperature of all the composting piles dropped to values close to ambient values after 45–50 days of the process, which corresponds to unaltered, high values of EXI2 until to the end of the process (Figure 2a,b). The mean EXI2 values were close for MS and AS piles, but the former was kept at temperature values >60 °C for a longer period than the latter, indicating that the thermophilic stage was more intensive and shorter for MS composts, and was most progressive in AS composts. In addition, the results obtained regarding the thermal behaviour in all the piles suggest that the maximum pathogen reduction is ensured in all the composting mixtures [30].
3.3. Composting Process: Effect on 15N Natural Abundance
Figure 3 shows δ15N variations in the raw materials, the initial composting mixtures and the composts obtained. There was a clear differentiation among the different groups of materials, and especially, between the initial composting mixtures and the composting end-products, the mature composts having the highest median δ15N values. This finding could be due to the N losses (preferentially 14N)—e.g., ammonia volatilization—during the composting process, which produces an enrichment in 15N in the composting end-products. Moreover, the highest degree of humification found in the final composts can also influence the δ15N values. Kramer et al. [31] found that, when the humified carbon fraction increased in aliphacity (ratio of unsubstituted aliphatics to carbohydrates), the δ15N value also increased. This relationship suggests that the 15N abundance is low when the carbon organic materials are mainly present in labile forms.
Total nitrogen losses and total nitrogen (TN) concentrations were also studied in the composting mixtures, trying to establish a relationship between these parameters and the values of δ15N in the composts at the beginning and end of the process (Table 5 and Figure 4). In addition, factorial analysis (FA) of the data corresponding to the parameters selected (EC, OM, P, TOC, δ15N, TN and CEC) of the initial mixtures and composted materials was carried out. According to the mass balance, the N losses showed a wide range of values. Low N losses (<10%) were accounted for compost 2 (2.5%), compost 4 (0.9%), compost 7 (0.9%) and compost 10 (4.8%) (Table 5). However, in the composts 1, 5, 6, 8, 9 and 11, N losses were similar to those found in previous studies. Guo et al. [32] reported N losses from 18 to 46% when composted pig manure and sawdust at different C/N ratio, and Sáez et al. [33] observed N losses of 44% during the composting of the solid phase of pig manure with cereal straw. Previous studies have documented the relationship between 15N abundance and the N loss during composting [2,19,34]. Particularly, Kim et al. [2] examined the changes in N isotope compositions during composting of livestock manure. They concluded that the 15N abundance increased during composting due to denitrification and ammonia volatilization processes, this last process being the main mechanism of N loss during composting. In addition, the chemical and/or biological N immobilization can contribute to the increase in δ15N during composting [2]. Kramer et al. [31] reported a contrasted trend in δ15N, observing an increase at the same time that the humification process increased and mainly attributed to microbial re-synthesis of polymerized compounds. The strong increase in δ15N seems to indicate that the humification was primarily due to microbial processing rather than to preferential degradation of labile constituents.
Regarding TN concentrations (Figure 4), a trend in TN content was observed, which was consistent in all the composting piles, with an average increase in the concentration values for MS composts and AS compost (27.4 and 27.5%, respectively) (Figure 4). In the final composts, in general, MS composts showed higher TN concentrations than AS composts, probably due to the greater N contents in MS samples than in AS samples.
Regarding δ15N values, this parameter also showed an increasing pattern in all the composting piles, but this increase was lower in AS composts than in MS composts (1.7 and 3.5‰, respectively). Thus, the trend of TN concentration during composting seems not to be directly related to δ15N values, since the values of these parameter did not show the same trend in the final composts as TN. In this sense, different N concentrations and their δ15N values in the raw materials may directly influence the δ15N values of the composting mixture through δ15N dilution or enrichment [19]. Kim et al. [2] observed a variable effect dilution/enrichment in the initial mixture prepared of cattle feedlot manure with rice hull and sawdust as bulking agents. These authors suggest that the relative contribution of 15N-depleted N from the bulking agent materials (isotope dilution) was greater in rice hull than in sawdust, resulting in a lower 15N of total N in rice hull compost. In our study, a different effect in the δ15N values of the initial mixtures has been observed. In all the mixtures prepared with MS, an effect of isotope dilution was observed when the different bulking agent was added, while in all the piles prepared with AS was observed an isotope enrichment. Therefore, these results suggest that the type of sludge had a main contribution in δ15N values in the initial composting mixtures.
Factorial analysis was conducted with the data of the selected parameters (EC, OM, TOC, CEC, P, δ15N and TN) corresponding to the initial composting mixtures and mature composts. For this analysis, three factors (F1, F2 and F3) were used and explained 83.5% of the total explained variance, where F1 explained 41.6% of the variance, F2 explained 23.9% and F3 explained 18% of the variance. Figure 5 shows the plot of the first and second factors for all the composting mixtures, corresponding to the initial and maturity stages of composting. FA allows to observe an important differentiation among groups, depending on the degree of stabilization of the material and the type of sludge used. Additionally, the parameter δ15N was positively correlated with TN and CEC, the latter being a parameter strongly associated to the humification processes during composting. This finding agrees with the previous data on the correlation between the increasing trend of δ15N and the humification process [31].
3.4. Composting Process: Characteristics of the Composts
Table 6 summarises the selected chemical properties of the final composts. In general, AS- and MS-derived composts presented pH values close to neutrality. However, AS-derived composts had higher electrical conductivity (EC) values than MS-derived composts, despite of the higher EC values observed in MS samples. This fact could be due to the characteristics of the bulking agent used in AS pile (palm trunk), which showed the highest EC values (Table 3). Probably due to these higher contents in soluble salts, which may negatively affect the germination and the early stage of plant growth [35], these composts reached lower values of the germination index (GI) than MS compost at the end of the process (Table 6). However, the GI values reached in all the composts of our study indicate absence of phytotoxicity [21]. All the composts had OM concentrations higher than 35%, AS composts showing in general the highest OM contents, with similar values to those obtained by Vico et al. [9] and Morales et al. [11] during the co-composting of agri-food sludge. CEC and CEC/TOC ratio are parameters usually considered to evaluate compost maturity [36,37]. The values of the CEC and CEC/TOC ratio differed greatly among the obtained composts (Table 6). In general, MS composts showed higher mean values of these parameters than AS composts, although in all cases both parameters showed values higher than those established as reference values in the literature [38]. In the MS mixtures, the humification processes were probably more intense, which would lead to the formation of functional groups responsible for the cation exchange capacity [11]. Concerning the P and K concentrations, the values observed were similar to those found in other studies of composting using sewage sludge [39,40] and/or agri-food sludge [11] and higher than those reported by Awasthi et al. [41] in compost of sewage sludge with biochar. The AS composts presented the highest K content according to the results previously found in other studies of composting using agri-food organic materials [9,11].
4. Conclusions
The results in this study evidence that the use of 15N abundance in composting studies may be a suitable parameter to monitor the N losses throughout the composting process. Moreover, the results obtained show higher values of δ15N in the sewage sludge samples compared to agri-food sludge samples, while the bulking agents showed a wide variation in the δ15N values, even between wastes within the same plant species. The incorporation of the bulking agents to the composting mixtures produced an isotope dilution in the mixtures with sewage sludge, but an isotope enrichment in the agri-food derived mixtures, which indicates that the type of sludge had a main contribution in δ15N content of the initial composting mixtures. Furthermore, the different increasing trend of δ15N during composting in relation to total nitrogen contents seems to indicate that there is isotopic discrimination and confirms that exist other processes associated to this parameter, such as the humification processes during composting. Therefore, further studies concerning the changes of δ15N in the different stages of the composting should be carried out to increase the knowledge concerning the nitrogen dynamics during the composting process.
Author Contributions
Conceptualization, M.Á.B., R.M., J.C.S.-H. and P.F.; methodology, J.A.S., M.D.P.-M. and P.F.; software, J.A.S., R.M., J.C.S.-H. and M.Á.B.; validation, R.M., J.C.S.-H., P.F. and M.Á.B.; formal analysis, J.A.S. and P.F.; investigation, M.Á.B., R.M., M.D.P.-M.; resources, R.M., M.D.P.-M.; data curation, J.A.S., P.F., R.M. and M.Á.B.; writing—original draft preparation, J.A.S., P.F. and M.Á.B.; writing—review and editing, M.Á.B., P.F. and J.C.S.-H.; visualization, R.M.; supervision, R.M., M.Á.B. and M.D.P.-M.; project administration, R.M. and M.D.P.-M.; funding acquisition, R.M. All authors have read and agreed to the published version of the manuscript.
Funding
This research was funded by the Spanish Ministry of Economy and Competitiveness and by European Regional Development Funds (ERDF, “Una manera de hacer Europa”), in the framework of the project “Development of new resources and bioproducts based on residues of palmaceous species oriented to carbon sequestration and mitigation strategies, Palmresource” (Project AGL2013-41612-R).
Conflicts of Interest
The authors declare no conflict of interest. The funders had no role in the design of the study; in the collection, analyses, or interpretation of data; in the writing of the manuscript, or in the decision to publish the results.
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Figure 1.
(a) Temperature profiles in the composting mixtures derived from sewage sludge (MS); (b) Temperature profiles in the composting mixtures derived from agri-food sludge (AS).
Figure 1.
(a) Temperature profiles in the composting mixtures derived from sewage sludge (MS); (b) Temperature profiles in the composting mixtures derived from agri-food sludge (AS).
Figure 2.
(a) Evolution of the cumulative values of EXI2 during the bio-oxidative phase in the sewage sludge-derived composting mixtures; (b) Evolution of the cumulative values of EXI2 during the bio-oxidative phase in the agri-food sludge-derived composting mixtures.
Figure 2.
(a) Evolution of the cumulative values of EXI2 during the bio-oxidative phase in the sewage sludge-derived composting mixtures; (b) Evolution of the cumulative values of EXI2 during the bio-oxidative phase in the agri-food sludge-derived composting mixtures.
Figure 3.
Natural δ15N values (‰) in the initial materials, initial composting mixtures and mature composts. The vertical lines of rectangles represent the lower and upper quartiles of distributions. The middle lines inside the rectangles represent median values.
Figure 3.
Natural δ15N values (‰) in the initial materials, initial composting mixtures and mature composts. The vertical lines of rectangles represent the lower and upper quartiles of distributions. The middle lines inside the rectangles represent median values.
Figure 4.
Total nitrogen concentration (%) in the initial composting mixtures and final composts.
Figure 5.
Plot of first and second factor extracted from factor analysis of initial composting mixtures and mature composts. Arrows correspond to the projection of the variables studied. EC: electrical conductivity; OM: organic matter; TOC: total organic carbon; CEC: cation exchange capacity; TN: total nitrogen; MS: sewage sludge; AS: agri-food sludge.
Figure 5.
Plot of first and second factor extracted from factor analysis of initial composting mixtures and mature composts. Arrows correspond to the projection of the variables studied. EC: electrical conductivity; OM: organic matter; TOC: total organic carbon; CEC: cation exchange capacity; TN: total nitrogen; MS: sewage sludge; AS: agri-food sludge.
Table 1.
Proportions of feedstocks and bulking agents in the composting treatments.
| Composting Pile | Raw Material | Bulking Agent | Ratio (Dry Weight) |
|---|---|---|---|
| 1 | 68% (MS2) | 32% (LP) | 36:64 |
| 2 | 60% (MS2) | 40% (AD) | 30:70 |
| 3 | 70% (MS2) | 30% (CG) | 38:62 |
| 4 | 75% (MS2) | 25% (GP) | 54:46 |
| 5 | 75% (MS3) | 25% (TW) | 41:59 |
| 6 | 85% (MS3) | 15% (MA) | 55:45 |
| 7 | 68% (MS4) | 32% (TP1) | 30:70 |
| 8 | 66% (AS1) | 34% (TP2) | 28:72 |
| 9 | 68% (AS2) | 32% (TP3) | 24:76 |
| 10 | 75% (AS3) | 25% (TP4) | 35:65 |
| 11 | 75% (AS4) | 25% (TP4) | 34:66 |
Raw material: municipal sewage sludge (MS1, MS2, MS3 and MS4), and agri-food sludge (AS1 and AS2 from fruit-processing plants, AS2 and AS4 from dairy desserts). LP: palm (Phoenix dactylifera L.) leaves; AD: giant reed (Arundo donax L.) waste; GP: mixed garden pruning; CG: cotton gin; TW: tipa (Tipuana tipu) waste; MA: mulberry (Morus alba L.) waste; TP: palm (Phoenix dactylifera L.) trunk.
Table 2.
Main physico-chemical and chemical characteristics of the raw materials used in the composting mixtures (data on a dry weight basis).
Table 2.
Main physico-chemical and chemical characteristics of the raw materials used in the composting mixtures (data on a dry weight basis).
| Raw Material | pH | EC (dS/m) | OM (%) | TOC (%) | TN (%) | δ15N (‰) | Ratio C/N | K (g/kg) | P (g/kg) | Na (g/kg) |
|---|---|---|---|---|---|---|---|---|---|---|
| MS1 | 6.1 | 4.4 | 66.8 | 43.6 | 5.5 | 6.9 | 7.9 | 26.2 | 2.43 | 3.73 |
| MS2 | 6.8 | 4.8 | 47.5 | 31.1 | 4.2 | 7.6 | 7.4 | 36.0 | 2.73 | 3.03 |
| MS3 | 5.1 | 5.0 | 50.8 | 36.0 | 5.2 | 7.4 | 6.9 | 30.0 | 2.58 | 2.58 |
| MS4 | 4.9 | 5.8 | 58.1 | 40.1 | 7.0 | 8.5 | 5.8 | 25.1 | 4.72 | 2.28 |
| Mean ± SD | 5.7 ± 0.8 | 5.0 ± 0.6 | 55.8 ± 8.5 | 37.7 ± 5.4 | 5.5 ± 1.1 | 7.6 ± 0.6 | 7.0 ± 0.9 | 29.3 ± 5.0 | 3.12 ± 1.0 | 2.90 ± 0.6 |
| AS1 | 5.6 | 5.5 | 81.4 | 50.5 | 6.7 | 4.6 | 7.5 | 17.4 | 6.88 | 4.54 |
| AS2 | 7.2 | 5.1 | 52.4 | 34.5 | 3.3 | 6.1 | 10.4 | 5.87 | 5.68 | 5.68 |
| AS3 | 5.5 | 3.6 | 69.0 | 52.3 | 4.9 | 2.7 | 10.4 | 6.07 | 4.34 | 4.34 |
| AS4 | 5.4 | 3.4 | 74.7 | 44.8 | 4.4 | 6.2 | 10.3 | 3.98 | 5.45 | 5.45 |
| Mean ± SD | 5.9 ± 0.8 | 4.4 ± 1.0 | 69.4 ± 12.4 | 45.5 ± 8.0 | 4.8 ± 1.4 | 4.9 ± 1.6 * | 9.7 ± 1.4 * | 8.3 ± 6.1 * | 5.59 ± 1.0 * | 5.00 ± 0.6 * |
MS: sewage sludge; AS: agri-food sludge. EC: electrical conductivity; OM: organic matter; TOC: total organic carbon; TN: total nitrogen. * p < 0.05, t-Student test. SD: standard deviation.
Table 3.
Main physico-chemical and chemical characteristics of the bulking agents used in the composting mixtures (dry weight basis).
Table 3.
Main physico-chemical and chemical characteristics of the bulking agents used in the composting mixtures (dry weight basis).
| pH | EC (dS/m) | OM (%) | TOC (%) | TN (%) | δ15N (‰) | Ratio C/N | K (g/kg) | P (g/kg) | Na (g/kg) | |
|---|---|---|---|---|---|---|---|---|---|---|
| LP | 6.6 | 5.1 | 91.9 | 45.1 | 2.6 | 12.2 | 18.0 | 2.1 | 14.6 | 6.8 |
| AD | 6.6 | 3.7 | 74.8 | 34.8 | 2.4 | 6.9 | 14.3 | 1.4 | 9.1 | 2.4 |
| CG | 7.3 | 4.5 | 71.4 | 39.3 | 2.3 | 7.6 | 17.1 | 3.1 | 17.7 | 3.0 |
| GP | 6.9 | 5.8 | 69.3 | 30.6 | 2.4 | 8.0 | 13.1 | 7.0 | 17.2 | 4.7 |
| TW | 5.7 | 2.2 | 88.9 | 43.7 | 1.6 | 2.6 | 27.7 | 2.1 | 3.2 | 2.0 |
| MA | 5.5 | 1.4 | 94.0 | 43.9 | 0.7 | 6.1 | 61.1 | 1.9 | 2.3 | 1.5 |
| TP1 | 6.7 | 6.6 | 83.2 | 40.4 | 2.0 | 7.8 | 20.9 | 1.1 | 14.2 | 8.5 |
| TP2 | 5.7 | 7.8 | 80.2 | 37.7 | 1.3 | 9.4 | 28.9 | 1.6 | 6.4 | 8.3 |
| TP3 | 6.5 | 7.4 | 88.0 | 41.4 | 1.2 | 10.5 | 33.7 | 2.7 | 16.2 | 4.5 |
| TP4 | 6.1 | 13.1 | 85.5 | 38.9 | 1.3 | 8.5 | 31.7 | 1.3 | 28.5 | 12.3 |
| Mean ± SD | 6.4 ± 0.6 | 5.8 ± 3.3 | 82.7 ± 8.5 | 39.6 ± 4.4 | 1.8 ± 0.6 | 8.0 ± 2.6 | 26.7 ± 14.1 | 2.4 ± 1.7 | 12.9 ± 8.0 | 5.4 ± 3.5 |
LP: palm leaves (Phoenix dactylifera L.); AD: giant reed (Arundo donax L.) waste; CG: cotton gin; GP: mixed garden pruning; TW: tipa (Tipuana tipu) waste; MA: mulberry (Morus alba L.) waste; TP: palm trunk (Phoenix dactylifera L.) waste. EC: electrical conductivity; OM: organic matter; TOC: total organic carbon; TN: total nitrogen. SD: standard deviation.
Table 4.
Indicators of the exothermic behaviour of the composting mixtures.
| Index EXI2 (°C2) | Ratio Days in Bio-Oxidative Phase/Days with Temperature >40 °C | Ratio EXI2/Days in Bio-Oxidative Phase | Days > 60 °C | |
|---|---|---|---|---|
| Pile 1 | 50,535 | 107/79 | 472 | 13 |
| Pile 2 | 52,264 | 68/37 | 769 | 5 |
| Pile 3 | 112,255 | 71/58 | 1581 | 40 |
| Pile 4 | 79,126 | 71/46 | 1114 | 46 |
| Pile 5 | 75,035 | 112/110 | 670 | 112 |
| Pile 6 | 61,654 | 109/99 | 566 | 105 |
| Pile 7 | 65,904 | 81/78 | 814 | 78 |
| Pile 8 | 108,673 | 75/56 | 1449 | 56 |
| Pile 9 | 54,746 | 69/34 | 793 | 34 |
| Pile 10 | 43,856 | 100/68 | 439 | 68 |
| Pile 11 | 59,408 | 134/109 | 443 | 109 |
EXI2: quadratic exothermic index (quadratic sum of the daily difference between the average temperature of the pile and the ambient temperature). Piles 1–7, mainly constituted by sewage sludge; Piles 8–11, mainly constituted by agri-food sludge.
Table 5.
Total nitrogen losses, δ15N values of the initial composting mixtures and final composts and isotope discrimination.
Table 5.
Total nitrogen losses, δ15N values of the initial composting mixtures and final composts and isotope discrimination.
| TN Loss (%) | δ15N (‰) Initial Mixture | δ15N (‰) Mature Compost | Isotope Discrimination (‰) | |
|---|---|---|---|---|
| Compost 1 | 46.1 | 5.46 | 7.19 | 1.73 |
| Compost 2 | 2.51 | 6.66 | 9.51 | 2.85 |
| Compost 3 | 13.5 | 6.56 | 11.0 | 4.44 |
| Compost 4 | 0.96 | 6.96 | 9.75 | 2.79 |
| Compost 5 | 54.1 | 7.40 | 10.6 | 3.20 |
| Compost 6 | 35.9 | 6.65 | 12.3 | 5.65 |
| Compost 7 | 0.91 | 9.76 | 13.9 | 4.14 |
| Compost 8 | 27.1 | 7.16 | 11.0 | 3.84 |
| Compost 9 | 24.6 | 7.10 | 8.58 | 1.48 |
| Compost 10 | 4.76 | 6.15 | 7.39 | 1.24 |
| Compost 11 | 13.5 | 10.5 | 10.7 | 0.20 |
TN: total nitrogen. Composts 1–7, mainly constituted by sewage sludge; Composts 8–11, mainly constituted by agri-food sludge.
Table 6.
Chemical characteristics and maturity properties of the final composts.
| pH | EC (ds/m) | OM (%) | P (%) | K (%) | CEC (meq/100 g OM) | CEC (meq/g TOC) | GI (%) | |
|---|---|---|---|---|---|---|---|---|
| Compost 1 | 6.1 | 7.8 | 61.5 | 1.6 | 1.4 | 135 | 2.7 | 68 |
| Compost 2 | 6.7 | 3.4 | 44.3 | 1.8 | 1.1 | 99 | 2.0 | 131 |
| Compost 3 | 7.1 | 8.1 | 47.8 | 3.3 | 1.8 | 135 | 2.5 | 106 |
| Compost 4 | 7.2 | 8.2 | 40.7 | 2.7 | 1.6 | 166 | 2.7 | 81 |
| Compost 5 | 5.9 | 4.9 | 56.8 | 3.1 | 1.1 | 194 | 3.8 | 77 |
| Compost 6 | 5.7 | 5.5 | 59.6 | 3.3 | 0.9 | 159 | 3.1 | 77 |
| Compost 7 | 6.0 | 7.2 | 45.9 | 2.1 | 1.3 | 152 | 3.1 | 69 |
| Compost 8 | 6.9 | 6.7 | 42.7 | 1.6 | 1.6 | 82 | 1.5 | 72 |
| Compost 9 | 7.0 | 12.7 | 76.0 | 2.4 | 2.6 | 117 | 2.2 | 94 |
| Compost 10 | 6.7 | 13.1 | 74.9 | 2.5 | 2.4 | 91 | 1.9 | 71 |
| Compost 11 | 7.2 | 12.3 | 71.2 | 2.7 | 2.4 | 120 | 2.4 | 80 |
| MS-compost 1 | 6.1 | 6.5 | 50.9 | 2.6 | 1.3 | 148 | 2.8 | 87 |
| AS-compost 2 | 6.7 | 11.2 | 66.2 | 2.3 | 2.3 | 102 | 2.0 | 79 |
1 Mean value for all the sewage sludge-derived composts. 2 Mean value for all the agri-food sludge derived-composts. EC: electrical conductivity; OM: organic matter; CEC: cation exchange capacity; GI: germination index. Composts 1–7, mainly constituted by sewage sludge; Composts 8–11, mainly constituted by agri-food sludge.
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Sáez, J.A.; Flores, P.; Bustamante, M.Á.; Sanchez-Hernandez, J.C.; Moral, R.; Pérez-Murcia, M.D. Nitrogen Isotope Fractionation during Composting of Sewage and Agri-Food Sludge with Pruning Waste. Agronomy 2020, 10, 1954. https://doi.org/10.3390/agronomy10121954
AMA Style
Sáez JA, Flores P, Bustamante MÁ, Sanchez-Hernandez JC, Moral R, Pérez-Murcia MD. Nitrogen Isotope Fractionation during Composting of Sewage and Agri-Food Sludge with Pruning Waste. Agronomy. 2020; 10(12):1954. https://doi.org/10.3390/agronomy10121954
Chicago/Turabian StyleSáez, José Antonio, Pilar Flores, María Ángeles Bustamante, Juan C. Sanchez-Hernandez, Raúl Moral, and María Dolores Pérez-Murcia. 2020. "Nitrogen Isotope Fractionation during Composting of Sewage and Agri-Food Sludge with Pruning Waste" Agronomy 10, no. 12: 1954. https://doi.org/10.3390/agronomy10121954
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