1. Introduction
In addition to providing good quality food, the solutions applied in plant production should ensure that the natural environment is protected. In modern agriculture, the use of mineral fertilizers is common; their inappropriate use, however, poses a serious hazard to the aquatic environment. Soilless cultivations are isolated from the soil, and fertigation (fertilization and irrigation) installations have come into widespread use [
1]. This enables the optimization of the obtained yields, through the adjustment of the composition and amount of the nutrient medium to the current needs of crops, taking into account the weather conditions. In view of the need to ensure an optimum amount of nutrients, and to prevent the accumulation of salts in the root zone, these cultivations must be conducted using an excess of the nutrient medium. This usually amounts to 25%–45%, which results in the generation of approximately 4.5 L·m
−2 of drainage water with a high concentration of nutrients [
2]. We are currently living in a low carbon economy, with a growing awareness of environmental protection and a strengthening of water resource-related legislation, and the need to recover nutrients from wastewater has become apparent [
3].
All over the world, the issue of water management in such sites has not been completely resolved. The problem of overflow management should be regarded as very serious and increasing [
4]. In Poland, almost 100% of soilless cultivations are operated using open fertilization systems. This means that the excess nutrient medium is discharged directly either into the ground within the greenhouse, or to the surface waters. This practice is common in many countries [
1,
4,
5]. In order to protect the environment, various biological and physicochemical methods of wastewater treatment can be used [
6]. Conventional treatment generally does not allow for the recovery or the reuse of nutrients, leading to the loss and dilution of important resources [
7]. Fertilizer components are thus irretrievably lost. However, wastewater can be a source of valuable commodities, including phosphate, nitrogen, calcium, potassium, and other micro- and macro-elements used in fertilization [
3], which can be used in processes such as sorption [
8] or ultra- and micro-filtration [
9]. With regards to tomato cultivation on mineral wool, the amounts of nitrogen and phosphorus introduced to the environment may amount to 23–245 kg N·ha
−1 and 2–54 kg P·ha
−1 per month, respectively, for a production period of 9–10 months [
1,
10]. Similar losses are noted for other soilless cultivations such as roses or cucumbers. For roses, the amount of nitrogen lost may amount to 2000 kg N·ha
–1 in a year, which accounts for 60% of the amount introduced into the cultivation [
11]. While in the fertigation of cucumbers, the amount of nitrogen lost may account for 33%–43% and the amount of phosphorus lost may account for 35%–47% of the load introduced along with the nutrient medium. For phosphorus, this is all the more important, as the non-renewable resources of phosphorus are estimated to only last for the next 50–100 years [
12]. The compounds contained in the overflow, while moving throughout the ground, penetrate the groundwater and pollute it. This hinders its use for fertigation purposes and in many other economic sectors, as well as in supplying drinking water [
1,
13]. This has resulted in the need to find the best economic and ecological solutions, enabling a reduction in the amount of biogenic compounds introduced into the environment through drainage water from soilless crop cultivation. To this end, it is first necessary to characterize the quality of the generated overflow, and thus the trends in its management. This will produce the highest environmental and economic benefits, such as a reduction of production costs related to water intake and the purchase of mineral fertilizers, resource recovery, and improved sustainability, by creating a circular economy in soilless tomato cultivation. The aim of the study was to determine the qualitative changes in drainage water (i.e., a specific type of industrial wastewater discharged during soilless tomato cultivation under shelter). The study was conducted at two sites, differing in cultivation area surface and the type of substrate used. It also presents the existing trends in the treatment and/or management of drainage waters.
3. Results and Discussion
The drainage water generated during soilless tomato cultivation under shelter poses a serious hazard to the aquatic environment, and at the same time, their characteristics prevent the application of traditional biological treatment solutions. The quality of wastewater is determined by the composition of the nutrient medium supplied to the root system; the growth phase of plants; the cultivation method, including the type of substrate used; and the weather conditions both inside and outside the greenhouse. Despite fluctuations in the values of basic parameters considered during the design of wastewater treatment systems, their general feature is a high content of oxidised nitrogen compounds (nitrates) and phosphorus (orthophosphates), as well as a very low organic compound content. This prevents the direct application of any processes of biogenic compound removal using heterotrophic microorganisms [
2,
4].
The COD values during the study for greenhouse 1 were 50.07–75.82 mg O
2·L
−1 (
Figure 2) and for greenhouse 2 they were 37.35–78.12 mg O
2·L
−1 (
Figure 3). They were higher compared with the values in the nutrient medium supplied to the system by an average of 132.1 ± 41.1% and 219.6 ± 92.9% (for greenhouse 1 and greenhouse 2, respectively). The increase in COD value was most probably caused by the concentration of the nutrient medium due to the transpiration of water by plants, and by organic pollutants in the form of various root exudates and dead plant parts (the root system). The highest COD values noted in the first month of the study (March) could have additionally resulted from the washing out of pollutants from the newly-laid mats, and from the nutrient substances that accumulated in the cubes in which seedlings had been prepared. This is due to the fact that prior to placing the plants in the mats and the commencement of proper fertigation, seed germination occurred in the mineral wool plugs. After approximately two weeks, the seedlings were planted out to cubes of mineral wool. After approximately one month (following the formation of the first inflorescence), they were transferred to the greenhouses under study. During that period, the amount of nutrient medium supplied to the root system in order to induce its expansion was reduced and the mats were saturated with water. These treatments resulted in an increase in the nutrient concentration in the cube with a seedling. After approximately 50% of the plants at the greenhouse burst into flower, the cubes with seedlings were placed in the pre-prepared holes in the mats.
In the nutrient medium supplied to the plants, the EC values ranged from 2.87 to 3.59 mS·cm
−1 (greenhouse 1;
Figure 2) and from 2.18 to 3.73 mS·cm
−1 (greenhouse 2;
Figure 3). The differences resulted from the composition of the supplied solutions, depending on the plant growth phase as well as the plants’ demand for water, which was determined by the atmospheric conditions. As a result of the transpiration, the concentration of the nutrient medium and an increase in the concentration of compounds dissolved in the overflow. The EC value for wastewater ranged from 4.40 to 6.93 m S·cm
−1 and from 4.94 to 6.94 mS·cm
−1, and was higher by an average of 67.1 ± 19.3% and by 98.2 ± 33.9% compared with the nutrient medium (for greenhouse 1 and greenhouse 2, respectively;
Figure 2 and
Figure 3).
The levels of TN and TP in the nutrient medium were adjusted, where possible, to the requirements of the plants in a specific growth phase, and to the atmospheric conditions. On the other hand, the concentration of biogenic compounds in the drainage water was determined by the quality of the nutrient medium supplied to the system, its use by plants, and the transpiration rates, and, thus, the concentration of the solution. During the growing period, the percentage of nitrogen and phosphorus content changes in both the dry matter of plants and in the substrate itself, with the changes in the nitrogen content occurring differently to the changes to phosphorus content. Moreover, they are determined by both the substrate used and the nutrient medium composition [
17]. In addition, nitrification and denitrification, as well as sorption processes may occur in the substrate, particularly in the initial period of cultivation.
During the study, percentage changes in the TN, TP, and EC concentrations were compared, and the relationships between them were determined. The study demonstrated that only a percentage increase in nitrogen concentration between the inflow and outflow was strongly correlated with the percentage increase in EC (
Figure 4). This relationship was noted both in greenhouse 1 (
p = 0.05, R = 0.81) and in greenhouse 2 (
p = 0.05, R = 0.80). No statistically significant correlations were noted between TN and TP, or TP and EC. This is of importance in a situation when overflow recirculation is applied. As shown by the study results, the measurement of EC itself is insufficient to properly balance the nutrient medium containing recirculate.
Nitrates were the main form of nitrogen supplied to the root system. The nitrate concentration was at a trace level, while the ammonia nitrogen concentration ranged from 12.39 to 17.39 mg N·L−1 (greenhouse 1) and from 6.35 to 12.35 mg N·L−1 (greenhouse 2), and was a result of the presence of ammonia nitrogen in the mineral fertilizers used for the preparation of the nutrient medium. In wastewater, the highest ammonia nitrogen concentrations were noted in the first month of the study, and amounted to 17.81 and 12.30 mg N·L−1 (for greenhouse 1 and greenhouse 2, respectively). In subsequent months, the ammonia nitrogen concentration did not exceed 1 mg N·L−1. Only at the end of the growing period (October and November) was there a slight increase in the concentration (up to 3.72 and 2.38 mg N·L−1 for greenhouse 1 and greenhouse 2, respectively). The initial high concentration of ammonium nitrogen most probably resulted from the low level of use by plants (small biomass of the root system and vegetative parts), and from the small number of nitrifying bacteria, which are characterized by a slow growth rate. In the subsequent months, ammonium nitrogen could be fully used up by plants, as well as oxidised in the nitrification process. The slight increase in concentration in the last months was probably caused by a reduction in the rate of plant growth and by the great biomass of the root system, and thus resulted in more intensive processes of decomposition of dead plant tissues.
During the study, in all of the wastewater samples, the TN concentration was higher compared with the supplied nutrient medium, by an average of 66.7 ± 31.0% and 80.7 ± 39.7%, and ranged from 403.59 to 614.89 mg N·L
−1 and from 270.00 to 577.40 mg N·L
−1 for greenhouse 1 and greenhouse 2, respectively (
Figure 2 and
Figure 3, respectively). Nitrates accounted for over 99% of the TN in the overflow (with the exception of the samples from March; the beginning of the cultivation, approximately 95%) from both greenhouse 1 and greenhouse 2. As for the TP, the concentration in the wastewater ranged from 35.44 to 78.00 mg P·L
−1 (greenhouse 1), and from 54.10 to 104.00 mg P·L
−1 (greenhouse 2). On average, the TP content was higher by 15.7 ± 21.1% and by 56.4 ± 43.9% compared with the nutrient medium; however, in certain months, the values for the overflow were lower. In greenhouse 1, these samples were from March, June and September, while for greenhouse 2, these samples were from March and April (
Figure 2 and
Figure 3, respectively).
The obtained results are consistent with those provided in the literature [
18]. Breś [
10] reported average values for nitrates of 327, 378, 385, 261, and 162 mg N·L
−1 for the soilless cultivation of Cunero F1 tomatoes, Flavorino F1 tomatoes, Millennium F1 cucumbers, Red Champ roses, and Amaretto Gerbera, respectively. These levels were higher by 114% 156%, 141%, 141%, and 120%, respectively, compared with the nutrient medium supplied to the system. As for TP, they amounted to 37, 38, 68, 51, and 13 mg P·L
−1. The TP concentration in the overflow was lower, by 69% and 89% (tomato cultivation), and by 81% and 45% in rose and Gerbera cultivation, respectively, compared with the nutrient medium. Values higher by an average of 112% were only noted for wastewater originating from cucumber fertigation. On the other hand, in all of the cultivations, the salinization (expressed as EC) was higher than the solution supplied to the root system by 148%, 176%, 164%, 163%, and 133%, and amounted to 4.99, 5.04, 4.27, 3.47, and 2.52 m S·cm
−1 [
10]. Other researchers have reported similar results. In a study by Grasselly et al. [
18], the nitrate concentration in the overflow from soilless tomato cultivation ranged from 150 to 500 mg N·L
−1. Park et al. [
19] reported average values for a mixture of wastewater from tomato and cucumber cultivations at a level of 325 mg N·L
−1, 38 mg P·L
−1, an EC of 37.5 µmho·cm
−1, and a pH of 6.45. The authors agree that drainage water from sheltered cultivation is characterized by a low content of organic compounds, combined with a high content of easily accessible mineral compounds with a high potential for migration in the natural environment. This is a significant threat to the natural environment.
In order for soilless cultivation under a shelter to be safe for the natural environment, water resource management in such greenhouses should be based on closed cycles with partial pre-treatment and overflow recirculation. However, the water used for irrigation is often characterized by high salt concentrations, including, not only Na
+ and Cl
−, but also Ca
2+, Mg
2+, and SO
42− [
20]. Hence, in most cases, the quality of the available irrigation water in terms of mineral composition is incompatible with the application of completely closed systems [
21].
In other cases, drainage water should be subjected to desalination, including high-performance denitrification and dephosphatation prior to being introduced into the natural system or sewage system. This is required by both Polish and European Union law [
22,
23]. For example, in Poland, wastewater discharged from this type of cultivation into the environment should have a total phosphorus concentration of not more than 3 mg P·L
−1, and a total nitrogen of 30 mg N·L
−1 [
24]. In order to remove the biogenic compounds from wastewater from soilless cultivations, biological, physical, and chemical methods were applied. As for the methods, based on the activity of plants and microorganisms, there were restrictions associated with atmospheric conditions and the need to use an internal source of organic carbon to ensure an appropriate C:N:P ratio [
2,
19,
25]. The application of chemical methods involves the use of reagents, the formation of additional deposits, and, frequently, high investment and operational costs [
26,
27,
28]. From an economic and environmental perspective, the best solution is the recovery of biogenic compounds (primarily in relation to phosphorus), as well as the use of overflow recirculation, which enables a reduction in the amount of mineral fertilizers and water used. This, however, involves the need to balance the composition of the nutrient medium, which is frequently a difficult problem to solve. In addition, the recirculate needs to be free from pathogens [
29,
30].