Organic waste vermicomposting through the addition of rock dust inoculated with domestic sewage wastewater

Journal of Environmental Management 196 (2017) 651e658

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Research article

Organic waste vermicomposting through the addition of rock dust inoculated with domestic sewage wastewater Aline Sueli de Lima Rodrigues a, Carlos Mesak b, Murilo Luiz Gomes Silva b, Geovanna Souza Silva b, Wilson Mozena Leandro c, Guilherme Malafaia a, d, * ~o em Conservaça ~o de Recursos Naturais do Cerrado, Instituto Federal Goiano, Campus
rio de Pesquisas Biolo
gicas, Programa de Po
s-Graduaça Laborato Urutaí, Urutaí, GO, Brazil b Instituto Federal Goiano, Campus Urutaí, Urutaí, GO, Brazil c ~o em Agronomia, Universidade Federal de Goia
s, Campus Samambaia, Goia ^na, GO, Brazil
s-Graduaça Programa de Po d ~o em Biodiversidade Animal, Universidade Federal de Goia
s, Campus Samambaia, Goia ^na, GO, Brazil
s-Graduaça Programa de Po a

a r t i c l e i n f o

a b s t r a c t

Article history: Received 5 October 2016 Received in revised form 15 March 2017 Accepted 24 March 2017

The aims of the present study are to assess the organic waste vermicomposting process (cattle manure mixed with tannery sludge) by using inorganic waste (rock dust) inoculated with treated domestic wastewater sewage, as well as the vermicompost application in Ruellia brittoniana seedling production. Different proportions of organic and inorganic waste moistened (or not) in wastewater were vermicomposted (by Eisenia foetida) for 120 days in the first stage of the experiment. Statistically significant earthworm density increase was observed between the 60th and 90th experimental vermicompositing days in all the assessed groups. There was decreased E. foetida population density after 90 days. The K, P, TOC, C/N ratio and Ca, Na and Mg concentrations significantly decreased at the end of the vermicompositing process in comparison to the initial concentrations identified in most treatments. On the other hand, there was pH and N, Fe, Zn and Mn concentration increase in most of the vermicomposts assessed at the end of the experiment. All plants grown in soil containing vermicomposts presented higher Dickson Quality Index (DQI) than the control group, which was cultivated in soil containing commercial topsoil. Plants grown in soil containing 100% cattle manure and tannery sludge, moistened in treated domestic wastewater sewage, showed the highest DQI. Thus, the vermicomposting waste used in the present study, which was inoculated with treated domestic wastewater sewage, is an interesting vermicompost production technology to be used in ornamental plant production. © 2017 Elsevier Ltd. All rights reserved.

Keywords: Agro-industrial waste Eisenia foetida Sludge tannery Ornamental plants

1. Introduction The generation of solid waste, such as the organic waste from tannery industries (Nunes et al., 2016), is addressed as one of the biggest challenges faced by industries worldwide (Sharma et al., 2017). This waste remains in the companies' courtyards and has no defined use, the tannery organic waste, in particular, besides demanding proper storage and disposal location, represent risks to the health of humans and to the environment. Therefore, its proper disposal is not enough to solve the waste production issue. The creation of specific environmental laws and the increasing


rio de Pesquisas Biolo
gicas, Instituto Federal * Corresponding author. Laborato Goiano, Campus Urutaí, Rodovia Geraldo Silva Nascimento, 2,5 km, Zona Rural, Urutaí, GO, CEP: 75790-000, Brazil. E-mail address: [email protected] (G. Malafaia). http://dx.doi.org/10.1016/j.jenvman.2017.03.072 0301-4797/© 2017 Elsevier Ltd. All rights reserved.

public awareness about the issue, in the recent decades, have been pressuring companies to turn their production processes into sustainable ones (Varadarajan, 2015; Eggleston and Lima, 2015; Bhinge et al., 2015). However, waste treatment and disposal are just some of the steps to be taken towards developing environmentally sustainable production processes. Accordingly, many studies have assessed the use of wastes for more noble purposes, mainly for their use in agriculture (Malafaia et al., 2016; Silva et al., 2016; Kumar et al., 2016; Carey et al., 2016). Inorganic wastes have been the target of studies aiming at finding waste application in agriculture (Mendes et al., 2015; Ramos et al., 2017), given the large availability of it. It is estimated that 75% of the total ornamental rock production is lost as rock dust (Campos and Castro, 2007), which is produced throughout all natural stone production stages (extraction, processing and finishing). The most problematic environmental stages

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concern the sawmills and marble shops, because they generate fine or ultrafine material (powder) (Uliana et al., 2015). Buzzi (2008) analyzed sawmill wastes in Espírito Santo State (Brazil) and found that approximately 80% of the fine or ultrafine waste could be classified as non-inert, i.e., are prone to change their characteristics when they are released into the environment. Another particular problem associated with rock dust refers to the possibility of having such wastes causing negative impacts on the health of populations (Dalmora et al., 2016; Vrablik et al., 2017). Efforts have been done to find applications to the powder from ornamental stone production processes, and some research have shown the feasibility of using fine and ultrafine material in agriculture by incorporating rock powder to the soil (Santos et al., 2015; Paradelo et al., 2016). Soil fertilization by using rock powder can provide a wide range of macronutrients such as nitrogen, phosphorus, potassium, calcium, magnesium and sulfur, as well as of micronutrients such as iron, manganese, copper, zinc and sodium, which are suitable for plant growth (Ramos et al., 2017). However, the availability of nutrients resulting from rock powder depends on the rocks' natural composition, for the production of nutrients is slow and their amount may not be enough for the plant. Anjanadevi et al. (2016) state that nutrients solubilization based on these wastes can be accelerated by mixing them with organic waste in order to stimulate nutrient solubilization through biological pathways. Thus, studies have been developed to simulate processes or techniques able to optimize inorganic waste solubilization (Sarma et al., 2016; Voisin et al., 2017) and/or to find organic waste applications (Case et al., 2017). Different studies have reported waste vermiprocessing using mushroom (Song et al., 2014) and tomato
ndez-Go
mez et al., 2013) residues, leaf litter (Suthar and (Ferna Gairola, 2014), sewage (Sahariah et al., 2015), paper (Arumugam et al., 2015), tanning sludge (Malafaia et al., 2015a,b; Nunes et al., 2016), jute mill (Das et al., 2016a), paddy straw (Das et al., 2016b), and food and vegetable processing wastes (Sharma and Garg, 2017). These studies show the likelihood of converting waste of polluting potential, previously discarded into the environment potential, into composts able to be used for more noble purposes. However, an unexplored research field concerns the use of domestic sewage wastewater to vermicompost co-disposed organic waste by using inorganic waste. One may question if it would be worthy transforming organic or inorganic wastes through vermicomposting processes able to generate high agronomic quality composts. Thus, the aims of the present study were to assess the organic waste vermicomposting process (cattle manure mixed with tannery sludge) by using inorganic waste (rock powder) humidified in treated domestic sewage wastewater, as well as to analyze the applicability of the herein tested vermicompost to produce seedlings of the ornamental species Ruellia brittoniana. The study emerged with the hypothesis that it would be possible generating compounds of favorable nutritional characteristics to ornamental plant production by mixing different organic and inorganic wastes (rock powder) humidified in treated domestic sewage wastewater (organic inoculant) substrate through vermicomposting. At this point, it is possible stating that the current study stands out due to its contribution to polluting tannery and marble production waste mitigation since it is the first study to use organic inoculants to vermicompost organic and inorganic substrates. 2. Materials and methods 2.1. Step 1: vermicomposting Different vermicomposts resulting from organic and inorganic waste mixes at different concentrations were produced in the first

stage of the experiment. Three types of waste were used in the vermicomposting process: cattle manure, which was provided by the experimental farm of Goiano Federal Institute (IF Goiano), Urutaí Campus, Urutaí County, GO, Brazil; ornamental rock powder, resulting from the finishing process applied to several ornamental rocks, mainly to granite, slate and marble - provided by a company located in Pires do Rio County, GO, Brazil; and tannery sludge supplied by a tannery industry located in Inhumas County, GO, Brazil. The physicochemical and chemical features of the herein used waste can be seen in Table 1 (see the supplementary material). The rock powder used in the experiments was composed of samples collected every two weeks over three months. The chemical composition of the marble waste was taken into account, since it changes over time, depending on the rock matrix. The tannery sludge was left to dry before it was mixed to the cattle manure (dry and leathery); thus, the sludge was arranged in approximately 5-cm layers, on plastic sheets - the drying process was natural and lasted 45 days. The residues were mixed and, subsequently, sieved in 8 mm mesh in order to find uniform particle size and to remove undesirable materials, so that the vermicomposting process could run properly. The organic waste mix comprised 80% cattle manure and 20% liming type tannery sludge, which is an interesting ratio, from a nutritional point of view, as shown by Malafaia et al. (2015a). The earthworms belonging to species Eisenia foetida (red Californian earthworm), family Lumbricidae, were used in the vermicomposting process, since it is widely used in vermicomposting processes involving different waste types (Sharma and Garg, 2017). After the experimental units were defined (Table 2), the vermicomposting process was carried out in plastic containers of volumetric capacity 3 L; 1 kg of substrate (dry) was added to each container, as described by Vig et al. (2011), Malafaia et al. (2015a, 2015b). The temperature during the vermicomposting process was kept between 20 and 25
C. The vermicomposting process was conducted in protected environment (in a room at the Goiano IF - Urutaí Campus, GO, Brazil) for 120 days. The window in the vermicomposting room where the worms were stored was covered to prevent light radiation in the environment, in order not to interfere in the earthworms' actions in the substrates. All the containers were covered with a shading material commercially known as plastic screen Sombrit to avoid leakage and potential worm predation, as well as to allow substrate aeration. The substrate was moistened with drinking water or with treated domestic sewage wastewater to keep the humidity between 30% and 40%, according to Dores-Silva et al. (2011), Malafaia et al. (2015a, 2015b). The domestic sewage wastewater was used as organic inoculant in the process by assuming that the effluent would provide microorganisms able to help degrading the substrate and that the addition of nutrients enriches the compounds generated at the end of the vermicomposting process. The drinking water used in the current study was collected in the Goiano Federal Institute water supply system (Goiano IF Urutaí Campus, GO, Brazil), which is fed by water from the local Water Treatment Plant. The treated domestic sewage wastewater was collected in the wastewater treatment system, which is a stabilization pond located in the institution's surroundings. Three samples were collected throughout the trial period to feature the irrigation water used in the physical, chemical and physicochemical analyses, according to the methodology proposed by APHA et al. (1998). Table 3 (see supplementary material) shows the physicochemical and chemical characteristics of the water used in the experiment. After the experimental units were set, the mixes were manually

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Table 2 Experimental units set for the current study.a Treatments

Water types used in substrate humidification

Cattle manure (100%) Cattle manure (90%) þ ornamental rock dust (10%) Cattle manure (80%) þ ornamental rock dust (20%) 100% cattle manure and tannery sludgeb mix Cattle manure and tannery sludge (90%)b mix þ ornamental rock dust (10%) Cattle manure and tannery sludge (80%)b mix þ ornamental rock dust (20%) a b

Drinking water (DW)

Wastewater (WW)

T100C-DW T90C-DW T80C-DW T100M-DW T90M-DW T80M-DW

T100C-WW T90C-WW T80C-WW T100M-WW T90M-WW T80M-WW

T: treatment; C: cattle manure; M: cattle manure and tannery sludge mix; DW: drinking water; WW: wastewater. Cattle manure and tannery sludge mix used as described by Malafaia et al. (2015a): 20% liming type tannery sludge and 80% cattle manure.

revolved every 24 h, for 20 days, to remove volatile gasses. One sample of each treatment was collected to determine the initial concentration of the following attributes: pH, N, P, K, TOC, C/N, Ca, Mg, Na, Cu, Fe, Mn, and Zn, as described by EMBRAPA (1997). Subsequently, 20 adult earthworms were transferred to each container; the earthworm population density increased during the experiment (either adult or young), which is a bio-indicator parameter for vermicomposting processes, as described by Malafaia et al. (2015b). 2.1.1. Step 1 statistical analysis All data collected in step 1 were initially subjected to normal Anderson-Darling test, which was followed by the Levene homogeneity variance test. Next, they were subjected to analysis of variance (ANOVA), depending on the factor model (2  6) (two water types for substrate humidification and six treatments composed of different organic and inorganic substrate ratios). The experiment followed a completely randomized design, with six replications, i.e., number of samples ¼ 6, totaling 72 experimental units (Table 2). The Tukey's test was applied at 5% probability, in case of significant F. The Bartlett test was used to check the residual homoscedasticity. The initial and final characteristics of the treatment were compared through Student T test, with Bonferroni adjustment for multiple comparisons. The Assistat software, version 7.7 beta (free distribution copy), was used in all statistical analyses. 2.2. Step 2: the applicability of the vermicomposting generated in Ruellia brittoniana seedling production The use of vermicompost generated in the previous step of R. brittoniana (popularly known as Mexican Petunia) seedling production, after the vermicomposting period, was assessed. The aim of the current step was to assess whether the vermicomposts can be used to replace commercial substrates often used in ornamental nursery ponds. R. brittoniana was chosen as test plant because the species is easy to grow under many different conditions and because it is one of the most used ornamental species in landscaping projects. The plant is native to Mexico and belongs to family Acanthaceae; it is a herbaceous perennial plant with stem height up to 1 m (Gilman, 1999). R. brittoniana has large flowers composed of five thin and delicate tissue petals, which blossom in the tip of the stems (Gilman, 1999). Each vermicompost from Step 1 (Table 2) was tested for R. brittoniana seedling production. The 15 cm ± 0.3 cm seedlings were transplanted from a commercial ornamental plant nursery located in Rio Pires County, GO, Brazil to specific plastic seedling planting bags (11.5 cm diameter, 23.2 cm height). Each plastic bag was filled with a substrate preparation comprising 50% soil (Oxisol Typical - the physicochemical and chemical features are listed in Table 4 e see supplementary

material), 25% sand and 25% of the vermicompost produced in step 1. The experimental unit “control”, comprised 25% commercial
polis County, GO, Brazil), which was topsoil (Flora do Brasil®, Ana added to the experiment in step 2. The same soil and sand ratio adopted in the other treatments was used in the control experimental unit. The seedlings were kept in protected environment, under automated irrigation, and monitored for 70 days. The environment was of the single arch type, with east-west orientation. The environment structure was made of steel (30 m long, 7 m wide, ceiling height 3.0 m, arc height 1.2 m) and covered with low-density polyethylene film (0.15 mm thick), its sides were covered with Clarite screen mesh (2.0  2.0 mm). The plant shoot, stem diameter and total shoot and root dry matter measurements were taken at the end of the trial period. The plants were disaggregated by using running water in the substrate, which was sieved in steel mesh, until the roots were completely clean, in order to assess the root system. The plants were cut at the neck to separate the aboveground root. Subsequently, the shoot and root systems of the plants in each treatment were separately packed in paper bags and left to dry in internal air circulation oven at 60
C, for three days. The sum of shoot dry biomass (SDB) and root dry biomass (RDB) resulted in total dry biomass (TDB), which was used with height (H) and stem diameter (SD) readings to assess seedling quality by using the Dickson Quality Index (DQI) (Dickson et al., 1960), according to equation (1).

DQI ¼

TDB ðgÞ HðcmÞ SDðmmÞ

SDMðgÞ þ RDMðgÞ

(1)

TDB ¼ total dry biomass H ¼ plant height SDM ¼ shoot dry biomass RDM ¼ root dry biomass SD ¼ stem diameter

2.2.1. Step 2 statistical analysis The experimental arrangement in step 2 consisted of 13 treatments (12 treatments in the experimental units defined in step 1 (Table 2) þ a control group), with ten repetitions (i.e.: number of samples ¼ 10) distributed in a completely randomized design, thus totaling 130 experimental units. Initially, all the collected data were subjected to Anderson-Darling normality test, which was followed by Levene variance homogeneity test. Next, the data were subjected to simple analysis of variance (one-way ANOVA). The Tukey's test was applied at 5% probability in case of significant F. The Bartlett test was applied to check the residual homoscedasticity. All

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statistical analyses were performed in the Assistat software, version 7.7 beta (free distribution copy). 3. Results and discussion Twenty (20) adult earthworms were transferred to all treatments established in step 1 at the beginning of the experiment, and the first counting was performed 60 days after inoculation (time required by the earthworms to acclimatize to the environment). There was statistically significant increase in earthworm density between the 60th and the 90th experimental day, in all groups, during the vermicomposting process (Fig. 1), fact that suggests that this substrate has the necessary conditions for earthworm's survival and reproduction. A significant density reduction was observed in most treatments after the 90th experimental day (Fig. 1), similar to results found by Kaushik and Garg (2004), Kaur et al. (2010) and Malafaia et al. (2015b), when they carried out vermicomposting using textile industry sludge, paper production and tannery sludge waste. There was increased population density up to the 90th experimental day in the present and other studies; however, there was significant decrease in it after the present assessment. Assumingly, such reduction is directly related to decreased food availability in the substrates, which was also evidenced by significant substrate mass reduction in all treatments, at the end of the experiment (120 days), in comparison to the initial mass (Fig. 2). Such reduction in the substrate mass is likely related to the substrate conversion into vermicast (earthworm excreta) by the earthworms. The vermicast was subsequently converted into vermicompost. Such conversion reduced the volume and mass of the substrate introduced in the vermicompost. There was significant interaction between the factors “water types used for moistening the substrates” (factor 1) and “treatments” (factor 2) in the physicochemical (pH) and chemical attributes (N, P, K, C/N, TOC, Ca, Mg, Na, Cu, Fe, Mn, and Zn) assessed at the end of the experiment (Table 5 - see supplementary material). The interaction consequences to the assessed attributes can be seen

Fig. 1. The Eisenia foetida population density during the vermicomposting process. The ANOVA was applied through repeated measures for data analysis, at 5% probability. Data is expressed as means ± standard deviation. Legend: cattle manure (100%) (T100C and T100C-DW-WW); cattle manure (90%) þ ornamental rock dust (10%) (T90C-DW and T90C-WW); cattle manure (80%) þ ornamental rock dust (20%) (T80C and T80CDW-WW); 100% cattle manure and tannery sludge mix (T100M-DW and T100MWW); cattle manure and tannery sludge (90%) * mix þ ornamental rock dust (10%) (T90M-DW and T90M-WW) and cattle manure and tannery sludge (80%) * mix þ ornamental rock dust (20%) (T80M and T80M-DW-WW). DW: drinking water; WW: treated domestic sewage wastewater.

in Tables 6 and 7 (see supplementary material). The initial and final values of each assessed attribute are shown in Table 8. Statistically significant substrate pH increase was observed at the end of the experiment (120 days of vermicomposting) - except for the T90M-WW treatment e in comparison to the initially identified pH (Table 8). However, lower pH was found in treatments (except for the T80M treatment) moistened with domestic sewage wastewater and substrate moistened in drinking water, when treatments were compared to each other (Table 6). Data published in the literature by different authors point to conflicting results regarding the effects of E. foetida vermicompost waste on the substrate pH. Vig et al. (2011) and Malafaia et al. (2015a), for example, reported pH increase during tannery sludge vermicomposting processes, possibly due to water dissolution in ammonia derived from microbial metabolism. Albanell et al. (1988) attributed the pH reduction to CO2 and to the production of organic acids during the metabolic activity of microorganisms found throughout the vermicomposting process. Such phenomenon may have occurred in the treatment moistened with domestic sewage wastewater in comparison to treatments using drinking water. The vermicomposting pH differences between results may be related to the used type of substrate, to the vermicomposting time, to the substrate moisture maintenance during the vermicomposting process and to the type of water used for this purpose. There was statistically significant C/N ratio decrease at the end of the experiment in comparison to the initially identified amounts in most treatments (T100C-DW, T90 C-DW, T90M-DW, T80M-DW, T80M-WW, T90C-WW, and T80C-WW) (Table 8). Such result indicates substrate maturation in these treatments. The C/N ratio decrease can be attributed to the carbon losses caused by microbial respiration and by the simultaneous nitrogen addition by earthworms in the form of mucus, as suggested in other studies (Atiyeh et al., 2002; Suthar, 2006; Tripathi and Bhardwaj, 2004; Aira et al., 2007; Tognetti et al., 2007; Hait and Tare, 2011; Vig et al., 2011). A pattern was not observed at the comparison of treatments moistened or not with domestic sewage wastewater, i.e., significant C/N ratio increase was identified in some treatments (T100C and T90C), as well as decrease in the T80C and T80M treatments and other differences in the T100M and T90M ones (Table 6). Accordingly, further studies must be conducted in order to better understand how the different organic and inorganic substrate ratios, moistened or not with treated domestic sewage wastewater, can affect the C/N ratio in order to generate a better substrate maturation at the end of the vermicomposting process. There was TOC decrease in all experimental groups when the initial and final values observed in the substrates were compared (Table 8). The TOC concentration reduction can be understood as the result of organic matter mineralization. Therefore, it is a substrate maturation indicator. According to Tripathi and Bhardwaj (2004), the TOC reduction also results from the respiratory activity of earthworms and micro-organisms, since this process releases CO2. Similar results were observed by Antunes et al. (2015) in a study wherein they found significant TOC reduction when the vermicompost derived from organic waste (bovine and equine manure, fruit and vegetable industrial processing, and food wastes). Moreover, despite the TOC reduction in all treatments at the end of the vermicomposting process, the values of this attribute were higher in most of the treatments added with organic inoculant (T100C, T90C, T80C, T90M and T80M) when the groups moistened with and without treated domestic sewage wastewater were compared (Table 6). The largest TOC values are probably related to the continuous carbon supply - carbon originated from wastewater used in substrate moistening. The treated domestic sewage wastewater (TOC ¼ 46.00 mg.L1) used in the present study had

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Fig. 2. Initial and final substrate masses composing the experimental treatments defined in the present study. The bars indicate the mean ± standard deviation. * indicates the statistically significant difference between the initial (time 0) and final (120th experimental day) according to the Student T-test, at 5% significance, with Bonferroni adjustment. Legend: cattle manure (100%) (T100C and T100C-DW-WW); cattle manure (90%) þ ornamental rock dust (10%) (T90C-DW and T90C-WW); cattle manure (80%) þ ornamental rock dust (20%) (T80C and T80C-DW-WW); 100% cattle manure and tannery sludge mix (T100M-DW and T100M-WW); cattle manure and tannery sludge (90%) * mix þ ornamental rock dust (10%) (T90M-DW and T90M-WW) and cattle manure and tannery sludge (80%) * mix þ ornamental rock dust (20%) (T80M and T80M-DW-WW). DW: drinking water; WW: treated domestic sewage wastewater.

TOC concentration 2.5 times higher than the concentration observed in drinking water (TOC ¼ 18.36 mg.L1) (Table 3). The vermicomposting process significantly decreased the K and P concentrations at the end of the experiment in comparision to the concentrations initially identified in all treatments (Table 8). Furthermore, the group humidified with wastewater presented the highest levels of these elements (Table 6), fact that can be related to the chemical composition of this water type (Table 3). Moreover, there was statistically significant N concentration increase in all experimental groups at the end of the vermicomposting process (Table 8) and in the treatments moistened with treated domestic sewage wastewater (Table 6) (except for the T80M group). According to Veras and Povinelli (2004) and, more recently, to Malafaia et al. (2015b), K is electrostatically adsorbed by the organic and inorganic matter, or can also be an organic waste and a living constituent of microorganisms. Therefore, the K concentration reduction in different treatments is assumingly related to the degradability of the waste composing the substrates during the vermicomposting process. Moreover, there was P reduction at the end of the vermicomposting process, in all the experimental treatments, due to P immobilization caused by the earthworms' metabolic activity, as shown in other studies (Veras and Povinelli, 2004; Singh et al., 2010; Vig et al., 2011; Malafaia et al., 2015a). Although the present N increased at the end of the vermicomposting process, it was not similar to that observed by Malafaia et al. (2015b), fact that corroborates similar studies using vermicomposts besides tannery sludge (Ravindran et al., 2008; Vig et al., 2011), as well as other substrates (Veras and Povinelli, 2004; Aquino et al., 2005; Godoy et al., 2009; Dores-Silva et al., 2011). Therefore, the increased N concentration found at the end of the vermicomposting process is related to the material mass reduction (as shown in Fig. 2) and to the nitrogenous products stemmed from

earthworms. These products possibly come from annelid droppings, urine (in form of ammonia and urea), mucoproteins and from the earthworms' own tissues after death, since 65%e75% of these animals' body composition is formed by proteins (Atiyeh et al., 2002; Tripathi and Bhardwaj, 2004; Suthar, 2006; Vig et al., 2011). According to Dores-Silva et al. (2011), the increased use of N fertilizers enhances the vermicomposting ability, since nitrogen is an essential nutrient for plant growth and development. According to Atiyeh et al. (2002), the increase in nutrients such as N is directly related to the organic matter mineralization generated by the earthworms. The concentration of macronutrients such as Ca, Na and Mg found in vermicompost substrates has decreased in most of the experimental treatments at the end of the vermicomposting process (Table 8). However, no pattern was observed in treatments moistened with wastewater (Table 8), which were expected to present higher levels of these nutrients, due to their continuous supply by this type of water (Table 3). According to Singh et al. (2010), these nutrients' decline at the end of the vermicomposting process may be related to the consumption of the elements by the earthworms. The micronutrients Fe, Zn and Mn (except for Cu) had significant concentration increase at the end of the vermicomposting process in comparison to the initially identified concentrations (Table 8), which corroborates previously developed vermicomposting studies (Kaushik and Garg, 2004; Suthar and Singh, 2008; Vig et al., 2011; Garg and Gupta, 2011; Malafaia et al., 2015b). Furthermore, most substrates humidified with wastewater showed reduced concentrations of these elements (Table 8). Assumingly, such reduction in the vermicomposts moistened with wastewater may be related to the assimilation of these nutrients by the earthworms, as well as by the bacteria found in the substrates or by those living in the

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Table 8 Substrate chemical features at the beginning and at the end of the vermicomposting process using Eisenia foetida. Treatmentsa T100C-DW T90C-DW T80C-DW T100M-DW T90M-DW T80M-DW T100M-WW T90M-WW T80M-WW T100C-WW T90C-WW T80C-WW

Initial Final Initial Final Initial Final Initial Final Initial Final Initial Final Initial Final Initial Final Initial Final Initial Final Initial Final Initial Final

Treatmentsa T100C-DW T90C-DW T80C-DW T100M-DW T90M-DW T80M-DW T100M-WW T90M-WW T80M-WW T100C-WW T90C-WW T80C-WW

Initial Final Initial Final Initial Final Initial Final Initial Final Initial Final Initial Final Initial Final Initial Final Initial Final Initial Final Initial Final

pH

C/N (%)

TOC (%)

N (%)

P (mg.dm3)

K (cmolc.dm3)

6.9b ± 0.1 7.1a ± 0.2 7.2b ± 0.1 7.4a ± 0.1 6.9b ± 0.05 7.4a ± 0.1 7.5b ± 0.2 7.9a ± 0.1 7.4b ± 0.1 8.3a ± 0.02 7.4b ± 0.1 8.2a ± 0.1 6.9b ± 0.4 7.0a ± 0.1 7.2a ± 0.2 7.1b ± 0.05 6.9b ± 0.1 7.2a ± 0.1 7.5b ± 0.1 7.6a ± 0.1 7.4b ± 0.2 8.0a ± 0.02 7.4b ± 8.2a ±

11.60a ± 0.025 11.58b ± 0.038 11.59a ± 0.21 11.37b ± 0.0 14 11.58b ± 0.015 11.86a ± 0.018 11.63b ± 0.028 11.76a ± 0.045 11.61a ± 0.032 11.58b ± 0.014 11.60a ± 0.019 11.58b ± 0.057 11.60a ± 0.017 11.61a ± 0.015 11.59b ± 0.018 11.61a ± 0.012 11.58a ± 0.011 11.45b ± 0.021 11.63b ± 0.036 11.76a ± 0.014 11.61a ± 0.087 11.59b ± 0.018 11.60a ± 0.012 8.89b ± 0.077

5.57a ± 0.1 2.78b ± 0.1 5.05a ± 0.05 3.07b ± 0.1 4.54a ± 0.2 2.49b ± 0.12 4.95a ± 0.1 4.00b ± 0.02 4.50a ± 0.08 2.78b ± 0.05 4.05a ± 0.04 2.78b ± 0.06 5.57a ± 0.1 4.76b ± 0.08 5.05a ± 0.04 4.76b ± 0.03 4.54a ± 0.1 4.35b ± 0.2 4.95a ± 0.05 4.00b ± 0.06 4.50a ± 0.07 3.36b ± 0.1 4.05a ± 0.02 4.00b ± 0.02

0.24b ± 0.025 0.48a ± 0.014 0.27b ± 0.011 0.44a ± 0.015 0.21b ± 0.062 0.39a ± 0.054 0.34b ± 0.015 0.43a ± 0.032 0.24b ± 0.014 0.39a ± 0.018 0.24b ± 0.017 0.35a ± 0.098 0.41b ± 0.015 0.48a ± 0.014 0.41b ± 0.052 0.44a ± 0.054 0.39a ± 0.044 0.38a ± 0.055 0.34b ± 0.088 0.43a ± 0.074 0.29b ± 0.084 0.39a ± 0.065 0.35b ± 0.045 0.45a ± 0.024

1800a ± 125.6 69b ± 2.5 1637a ± 98.5 63b ± 3.8 1474a ± 121.1 65b ± 1.1 1444a ± 85.3 67b ± 6.4 1317a ± 124.1 70b ± 2.1 1189a ± 75.4 64b ± 1.5 1800a ± 11.2 65b ± 9.8 1637a ± 15.1 62b ± 10.1 1474a ± 25.7 61b ± 1.3 1444a ± 32.1 63b ± 2.4 1317a ± 88.1 64b ± 2.5 1189a ± 9.5 71b ± 1.9

500a ± 10.1 166b ± 9.5 507a ± 6.5 166b ± 11.2 513a ± 1.1 172b ± 23.2 456a ± 1.5 170b ± 45.6 467a ± 9.5 160b ± 2.2 478a ± 10.2 162b ± 10.9 500a ± 45.2 172b ± 17.8 507a ± 80.1 162b ± 2.1 513a ± 30.4 166b ± 11.0 456a ± 10.2 63b ± 1.2 467a ± 40.1 162b ± 20.4 478a ± 5.7 166b ± 5.8

Ca (cmolc.dm3)

Mg (cmolc.dm3)

Na (cmolc.dm3)

Fe (cmolc.dm3)

Mn (mg.dm3)

Cu (mg.dm3)

Zn (mg.dm3)

8.1a ± 0.09 6.5b ± 0.08 7.6a ± 0.05 5.6b ± 0.06 7.1a ± 0.06 4.4b ± 0.06 9.7a ± 0.04 8.0b ± 0.08 9.0a ± 0.19 6.0b ± 0.07 8.3a ± 0.22 5.2b ± 0.01 8.1a ± 2.15 4.7b ± 0.04 7.6a ± 0.05 6.4b ± 0.17 7.1a ± 0.85 4.9b ± 0.08 9.7a ± 0.17 7.6b ± 0.02 9.0a ± 0.26 7.3b ± 0.04 8.3a ± 0.08 6.3b ± 0.15

4.7a ± 0.14 2.7b ± 0.15 4.3a ± 0.12 2.1b ± 0.20 3.9a ± 0.11 2.6b ± 0.14 3.9a ± 0.15 2.2b ± 0.12 3.6a ± 0.18 2.0b ± 0.19 3.3a ± 0.24 2.2b ± 0.15 4.7a ± 0.18 2.6b ± 0.17 4.3a ± 0.80 2.6b ± 0.22 3.9a ± 0.32 2.3b ± 0.45 3.9a ± 0.11 2.0b ± 0.12 3.6a ± 0.40 2.0b ± 0.15 3.3a ± 0.19 2.2b ± 0.16

3.1a ± 0.15 2.0b ± 0.15 3.4a ± 0.18 2.1b ± 0.14 3.8a ± 0.65 2.0b ± 0.12 3.9a ± 0.22 1.0b ± 0.21 3.1a ± 0.23 3.2a ± 0.25 3.1a ± 0.24 1.2b ± 0.45 3.8a ± 0.12 2.0b ± 0.11 3.7a ± 0.10 3.6a ± 0.12 3.1a ± 0.10 3.2a ± 0.09 3.6a ± 0.08 1.0b ± 0.11 3.6a ± 0.12 1.1b ± 0.15 3.9a ± 0.50 2.0b ± 0.22

3.0b ± 1.10 164a ± 22.22 16b ± 1.20 231a ± 19.15 29b ± 2.30 232a ± 40.56 44b ± 3.10 73a ± 2.00 53b ± 5.66 96a ± 10.33 61b ± 1.00 117a ± 55.66 3.0b ± 0.09 131a ± 33.11 16b ± 0.07 134a ± 11.78 29b ± 0.07 182a ± 40.66 44b ± 10.00 13a ± 1.66 53b ± 3.99 79a ± 14.22 61b ± 0.08 107a ± 0.55

28b ± 0.22 88a ± 0.41 27b ± 0.23 103a ± 0.25 26b ± 0.25 100a ± 0.88 45b ± 0.55 55a ± 0.26 43b ± 0.54 55a ± 0.25 40b ± 0.94 61a ± 0.52 28b ± 0.24 87a ± 0.55 27b ± 0.41 84a ± 0.23 26b ± 0.26 90a ± 0.25 45b ± 0.54 65a ± 0.66 43b ± 0.87 57a ± 0.59 40b ± 0.35 51a ± 0.23

80.0a ± 4.22 2.1b ± 0.09 72.0a ± 5.61 4.1b ± 0.66 64.0a ± 6.44 5.1b ± 1.27 65.2a ±14.60 0.9b ± 0.07 58.7a ± 22.66 1.8b ± 0.02 52.2a ± 10.11 4.1b ± 1.28 80.0a ± 2.22 1.6b ± 0.18 72.0a ± 22.60 3.0b ± 1.21 64.0a ± 2.44 5.2b ± 0.06 65.2a ± 3.22 0.5b ± 0.05 58.7a ± 0.66 1.7b ± 0.08 52.2a ± 1.22 3.1b ± 1.30

6.1b ± 1.29 42.7a ± 22.5 5.5b ± 1.50 40.2a ± 10.5 5.0b ± 0.05 39.1a ± 11.5 14.4b ± 1.32 18.2a ± 2.22 13.0b ± 0.05 18.1a ± 1.22 11.6b ± 0.07 23.3a ± 0.09 6.1b ± 1.23 31.9a ± 12.22 5.5b ± 0.01 31.5a ± 6.11 5.0b ± 0.06 35.2a ± 2.55 14.4b ± 0.14 18.3a ± 1.22 13.0b ± 0.07 20.4a ± 0.77 11.6b ± 2.22 18.0a ± 1.55

a Legend: cattle manure (100%) (T100C and T100C-DW-WW); cattle manure (90%) þ ornamental rock dust (10%) (T90C-DW and T90C-WW); cattle manure (80%) þ ornamental rock dust (20%) (T80C and T80C-DW-WW); 100% cattle manure and tannery sludge mix (T100M-DW and T100M-WW); cattle manure and tannery sludge (90%) * mix þ ornamental rock dust (10%) (T90M-DW and T90M-WW) and cattle manure and tannery sludge (80%) * mix þ ornamental rock dust (20%) (T80M and T80M-DWWW). DW: drinking water; WW: treated domestic sewage wastewater.

intestinal biota of annelids. On the other hand, the increasing concentration of these micronutrients at the end of the vermicomposting process (whether in presence of organic inoculum or not), in comparison to the initial concentrations, may be related to the decreased substrate volume in the container (Fig. 2), fact that would explain the increased concentration of these elements after the 120th experimental day. Finally, the herein performed analysis of variance has shown DQI differences (F12,117 ¼ 8.692, p < 0.0001) in the different vermicomposts generated in the present study during R. Brittoniana seedling production. All plants grown in soil containing the vermicomposts presented higher DQI than those in the control group, which were cultivated in soil containing commercial topsoil (Fig. 3). Plants grown in soil containing the T100M-WW treatment (100% cattle manure and tannery sludge mix, moistened with treated

domestic sewage wastewater) have shown higher DQI than those subjected to the other treatments (Fig. 3). Such result may be correlated with the highest N, P and K values found in this treatment (Table 6), fact that would explain the best plant growth in the T100M-WW group. According to Gomes and Paiva (2004), DQI is a good seedling quality indicator, because it is used to calculate the plant's biomass distribution strength and balance, as well as takes many attributes into account; i.e., the higher the value, the better the seedling quality standard (Gomes and Paiva, 2004). Few studies in the literature have assessed plant cultivation in soil containing vermicomposts (Chandrashekara et al., 2000; Lazcano et al., 2011; De and Bandyopadhyay, 2013; Zacarias-Toledo et al., 2016; Das et al., 2016). Some of these studies show that the vermicompost addition to the soil, in appropriate and planned amounts, has positive effects on

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657

Appendix A. Supplementary data Supplementary data related to this article can be found at http:// dx.doi.org/10.1016/j.jenvman.2017.03.072. References

Fig. 3. Dickson Quality Index (DQI) of R. brittoniana produced in soil containing vermicompost composed of different organic and inorganic waste ratios, with or without organic inoculant. The bars indicate the mean ± standard deviation. Different lowercase letters indicate statistically significant differences between treatments in the analysis of variance (one-way ANOVA), at 5% significance level. Legend: cattle manure (100%) (T100C and T100C-DW-WW); cattle manure (90%) þ ornamental rock dust (10%) (T90C-DW and T90C-WW); cattle manure (80%) þ ornamental rock dust (20%) (T80C and T80C-DW-WW); 100% cattle manure and tannery sludge mix (T100M-DW and T100M-WW); cattle manure and tannery sludge (90%) * mix þ ornamental rock dust (10%) (T90M-DW and T90M-WW) and cattle manure and tannery sludge (80%) * mix þ ornamental rock dust (20%) (T80M and T80M-DW-WW). DW: drinking water; WW: treated domestic sewage wastewater.

the growth of the assessed crops. However, there was a gap in the literature about the vermicompost produced from organic (tannery sludge and cattle manure) and inorganic (rock dust) substrate mixes moistened with treated domestic sewage wastewater applied to R. brittoniana development. This result impairs the comparison between the data collected in the present study and previously published findings. However, based on the current results, the vermicomposts can be used to replace the commercial ones (topsoil), because they showed better results in R. brittoniana seedling production. 4. Conclusions Based on the results and according to the experimental conditions, it can be concluded that the combination of organic waste vermicomposting (manure and tannery sludge mix) and inorganic waste (rock dust) inoculated with treated sewage wastewater proved to be a viable vermicompost rich in N, P, K. The use of all vermicomposts from the herein assessed treatments proved to be feasible for R. brittoniana seedling production and for commercial substrate (humus) replacement. In addition, the T100M-WW treatment, which consisted of 80% bovine manure and 20% tannery sludge mix produced with organic inoculant, was responsible for the highest R. brittoniana seedling IQD. The study is innovative, but it did not intend to be exhaustive. Accordingly, it opens prospects for future research on the use of combined residues in substrate vermicomposting processes concerning transformations hard to be conducted. Furthermore, microbiological and maturity analyses applied to the vermicompost (through spectroscopic analysis, structural characterization and thermogravimetric analysis) were not performed in the present study, fact that may have favored the understanding about how vermicomposting helps the biotransformation of potentially polluting residues into more noble composts.

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