{'fraction_non_alphanumeric': 0.02688821752265861, 'fraction_numerical': 0.012041432887354337, 'mean_word_length': 5.154316069057105, 'pattern_counts': {'":': 0, '<': 0, '<?xml version=': 0, '>': 0, 'https://': 0, 'lorem ipsum': 0, 'www.': 0, 'xml': 0}, 'pii_count': 0, 'substrings_counts': 0, 'word_list_counts': {'cursed_substrings.json': 0, 'profanity_word_list.json': 0, 'sexual_word_list.json': 0, 'zh_pornsignals.json': 0}}
Performance evaluation of artificial wetlands with floating macrophytes (Lemnas) in the treatment of urban effluents

Currently, the treatment of sewage by conventional systems require high investment costs, operation and maintenance for which public funds are usually insufficient. As a result, in many cases, the effluents are discharged into natural waterways without treatment, polluting rivers and groundwater with consequent increased risk of waterborne diseases. To mitigate these environmental impacts, a number of unconventional alternatives may be applied for the artificial wetlands that have low cost of installation and maintenance, and operate with low power consumption. Addressing the economic aspect, implementing the use of Superficial Wetlands in the treatment of urban effluent means a significant decrease in power consumption, being useful in rural schools closed neighborhoods and small urban populations. Considering the social component, the need for maintenance of wetlands in terms of cleanliness and other work to achieve operational effectiveness thereof constitutes a source of labor genuine work, involving the inhabitants of the area where the system is implemented.


Introduction
Currently, the treatment of sewage by conventional systems require high investment costs, operation and maintenance for which public funds are usually insufficient. As a result, in many cases, the effluents are discharged into natural waterways without treatment, polluting rivers and groundwater with consequent increased risk of waterborne diseases. To mitigate these environmental impacts, a number of unconventional alternatives may be applied for the artificial wetlands that have low cost of installation and maintenance, and operate with low power consumption. Addressing the economic aspect, implementing the use of Superficial Wetlands in the treatment of urban effluent means a significant decrease in power consumption, being useful in rural schools closed neighborhoods and small urban populations. Considering the social component, the need for maintenance of wetlands in terms of cleanliness and other work to achieve operational effectiveness thereof constitutes a source of labor genuine work, involving the inhabitants of the area where the system is implemented.
Finally from the environmental viewpoint, and taking into account the three pillars that make sustainability system, the contaminant removal accomplished supplemented with tertiary treatment allows the reuse of treated liquid in the irrigation of crops and green spaces as well also its use in aquaculture; recovering -in this way-the precious liquid so scarce in times of drought, reinserting it in the productive cycle as the production of fishmeal and reducing the environmental impact by avoiding pollution of surface and groundwater resources. In this work, the behavior of Biological Oxygen Demand (BOD 5 ), Chemical Oxygen Demand (COD), total suspended solids (TSS), total nitrogen (Nt), Total phosphorus (Pt) and total coliforms was studied according to two plant population densities of 50% and 100% coverage of the surface of wetlands and two Hydraulic Retention Time (HRT) of 4 days and 1 day. The aim of this work, then consisted in evaluating the performance of a system surface wetlands with floating macrophytes with two plant population densities and two hydraulic retention time (TRH), in the removal of organic matter, total suspended solids, nutrients (total nitrogen and total phosphorus) and total coliforms, in winter season, with unfavorable weather conditions. channels. The effluent, after receiving a pre-treatment, passes through the wetland where it is subjected to physico-chemical and microbiological processes for a certain retention time. The oxygen required for these processes is supplied by photosynthesis of the plants themselves or taken from the air by them, to be injected into the root zone. The oxygen transfer to the root zone by these aquatic plants, is essential for the microbial removal of some contaminants, further stimulating the degradation of organic matter and growth of nitrifying bacteria. 1 The main functions of aquatic plants are aerate the root system and provide oxygen to the microorganisms living in the rhizosphere, absorption of nutrients (nitrogen and phosphorus), removing contaminants assimilating directly in their tissue and filtration of the solids through the framework that forms its root system. Aquatic plants are involved in these processes of removal. Some of them pump oxygen to their submerged petioles, roots and stems. Oxygen is used by microbes performing decomposition, and attached to aquatic plants under the water level. 2 The constructed wetlands are used to treat a range of wastewaters: a. Domestic and urban water. Constructed wetlands are categorized according to their flow patterns: surface or subsurface.
There are three lines of technological development of artificial wetlands, whose mode of action is different, even based on the same biological principles. These are: Artificial wetlands free flowing, raceways or ponds consist of slope walls, where these and the bottom cover are tight (impermeable materials), to prevent water percolation susceptible to contamination of groundwater. Each system has appropriate inlet and outlet to ensure a uniform distribution of applied wastewater and harvesting structures. 4,5 Emergent vegetation used in wetlands FWS includes the cattails (Typha spp.), rushes (Scirpus spp.) and reeds (Phragmites spp.). In wetlands subsurface flow (SBF), the influent flow is horizontal subsurface type, because of the water below the surface of the system. 1 In a wetland SBF, no column continuous water, the influent flows through a porous bed of sand and/or gravel of variable thickness, holding the vegetation (hydrophytes or hygros). This bed is designed so as to allow the flow of wastewater through horizontal flow or vertical flow through the root system of aquatic macrophytes. The effluent is treated through various physicochemical and bacteriological processes. In systems subsurface flow sheet there is no water in sight of the observer. An artificial wetland SBF is specifically designed for wastewater treatment or for final treatment stage is constructed as a bed or channel containing an appropriate medium. The means used may be crushed rock, gravel, sand and other soil materials. The medium is typically ground with the same types of emerging vegetation present on the flooded meadows and, by design, the water level remains below the surface of the medium. 5 SBF wetlands are one or more channels shallow and coated to prevent percolation water table susceptible to contamination background. The type of coating depends on the soil conditions. In some cases local soil compaction is adequate, while in others addition of clay or plastic coating membranes, Polyvinyl Chloride (PVC) or High Density Polyethylene (PAD) is required. Emergent vegetation used in wetlands SBF includes the cattails and bulrushes (Typha spp.), rushes (Scirpus spp.) and reeds (Phragmites spp.). SBF wetlands horizontal flow, the water flows horizontally through the granular media and rhizomes and roots of plants. SBF species used in horizontal flow systems are typical emergent macrophytes of wetlands and reed (Phragmites), cattail (Typha) or the bulrushes (Scirpus). SBF vertical flow wetlands were developed in Europe as an alternative to the horizontal wetlands to produce nitrified effluents. Generally in SBF systems the vertical flow is combined with horizontal flow so that nitrification and denitrification occurs gradually, leading to elimination of nitrogen.

Contaminant removal
In artificial wetlands, contaminants in wastewater are removed by a number of physical, chemical and biological processes that take place in the natural environment, among these processes are sedimentation, adsorption to the soil particles, the assimilation by plants and microbial transformation. 6 In photosynthesis, the floating macrophytes employ oxygen and carbon dioxide from the atmosphere. The nutrients are taken from the water column through the roots, which are also a means for infiltration/adsorption to suspended solids and bacterial growth. Root development depends on the availability of nutrients in the water and nutrient demand by the plant. Consequently, density and media depth of treatment -for example, roots of plants-are affected by water quality, pretreatment and factors affecting the rate of plant growth, such as temperature and harvesting scheme. 7

Suspended solids removal
Most of the suspended and settleable solids are removed in the pretreatment and wetlands filter and settle the remaining complementing this removal. Macrophyte roots and the substrate reduce water velocity favoring both processes. 3 In free flow systems (surface flow) the suspended solids are removed by mechanisms of flocculation/sedimentation and filtration/Intercept. 1 It should be noted that besides solids containing influent, the system may also generate due to remains of plants, microorganisms and precipitates. Sedimentation occurs by gravity, and under ideal conditions is governed by Stokes' law, which states that the sedimentation rate is proportional to the square of the particle diameter and inversely proportional to fluid viscosity. In turn, the viscosity of a liquid decreases with temperatura. no longer depends on the temperature, but may be affected by this, for low HRT.
The effects of temperature may be significant for sedimentation processes. 10 It has been shown that a temperature differential of 1°C between the influent waste liquid and residual liquid in a sedimentation tank; will result in the formation of a density current. Accordingly, if the temperature of the influent is higher than the temperature of the liquid located in the sedimentation tank a thermal stratification will occur such that the incoming flow at higher temperatures will shift on the colder liquid in the tank sedimentation, where a dead space will be formed.

Removal of organic matter
The removal of organic matter takes place mainly by aerobic microbiological or anaerobic biodegradation, depending on the presence of dissolved oxygen. A small portion is also removed by physical processes such as sedimentation and filtration, when organic matter is attached to the suspended solids. 3 Biodegradation is carried out by microorganisms which are attached to plants, in particular to roots and sediment surface. 3 All microorganisms involved in the degradation process require a source of energy and carbon for the synthesis of new cells, as other nutrients and trace elements. According to their source of nutrients, they are classified as heterotrophic and autotrophic. Heterotrophs require organic material as a carbon source for the synthesis of new microorganisms, however, autotrophs utilize carbon dioxide as a carbon source. 3 An indicator of the amount of organic substances of biological origin (proteins, carbohydrates, fats and oils), and synthetic organic and biodegradable chemicals in the waste water is the biochemical oxygen demand (BOD 5 ). 11 To measure the organic material present in the waste water susceptible of being chemically oxidized the chemical oxygen demand (COD), analysis was done by oxidation with a dichromate solution in an acid medium. Saber et al, (2004) indicated that removal of COD, BOD 5 and TSS probably depends primarily on HRT and that greater HRT treatment system of lagoons of Lemna gibba no longer depends on the temperature, but may be affected by this for HRT low.

Nitrogen removal
The temperature is most influential on the growth of nitrifying bacteria operational factor. There is a significant reduction in the rate of nitrification with decreasing temperature. In contrast, the growth rate of nitrifying bacteria increases considerably with temperature in the range of 8°C to 30°C, an increase of 10% for each 1°C temperature rise in the genus Nitrosomonas, 12 Below 10ºC the nitrification rate drops abruptly. Above 10°C the nitrification increases almost in proportion to the temperature. Nitrosomonas have an optimal growth rate at 30°C, therefore, generally this is considered ideal for the nitrification process temperature. Below 4°C no growth of Nitrosomonas and Nitrobacter. 12 Denitrification is the final step in nitrogen removal. Occurs under anoxic conditions, i.e., without dissolved oxygen; or with less than 2% of saturation concentration, but where the oxygen is available sources such as nitrate, nitrite or sulfate. Similar to the process of nitrification, denitrification is also strongly temperature dependent, and requires sufficient carbon as an energy source for the bacteria to do the conversion. Saber et al., 9 notes that most of the removal of N depends on the growth rate of the duckweed and a lower percentage occurs by sedimentation and denitrification processes. It also states that during the winter season, the growth rate of the duckweed by low temperature (13-20°C) was significantly reduced and consequently decreased nutrient recovery.

Phosphorus removal
Phosphorus is present as orthophosphate, polyphosphate and organic phosphate. Organic phosphate and polyphosphates, require subsequent decomposition to a more assimilable orthophosphate. 3 Processes of phosphorus removal are the physicochemical type. The phosphorus which is in the form of (solid) particles can be deposited by sedimentation on the bottom of the wetland, or trapped between the submerged parts of the emerging plants and adhere on the surface forming biofilms, being susceptible to other processes of biological Type. 1 The soluble phosphorus dynamics includes physicochemical adsorption/absorption, exchange, precipitation, solubilization, and redox. The adsorption/absorption biofilms occur on plants and waste and wetland sediments. In sediments often occur an intensive exchange of phosphorus with the water column.
In biological transformation processes of phosphates, dissolved organic phosphorus, organic phosphorus and insoluble particulate phosphorus are not available for plants unless be transformed into soluble inorganic phosphorus. In wetlands these transformations can occur through the intervention of microorganisms that have been suspended as biofilms on surfaces of emerging plants and sediments. Once solubilized, it can be assimilated by plants and other organismsbacteria, algae-and therefore be temporarily removed from the water.
Phosphorus removal is primarily due to the deposition and immobilization of phosphates in the sediment; vegetation in turn, contributes phosphorus extractions, provided that the biomass is removed from the system. Considerably, phosphorus is one of the essential macronutrients for the growth of microalgae. It is taken as orthophosphate (P-PO 4 -3 ), whose concentration depends on the pH of the medium. There are factors that slow down the taking of orthophosphate by the algae, such as an excessively high or low pH. 13

Bacteria removal
The removal of these microorganisms is based on a combination of physical, chemical and biological factors. Physical factors include filtration, sedimentation, aggregation and action of ultraviolet radiation. Biological mechanisms include, predation and attack by bacteriophages, and death (declination die-off). Finally, chemical factors are oxidation, adsorption and exposure to toxins set by other microorganisms and exuded by the root of the plants.

Material and methods
The work was carried out in 2013, at the Pilot Treatment and Effluent Reuse Urban Plant of the National University of Río Cuarto (UNRC), Córdoba, Argentina. This plant processes a flow of 25,000 Ld -1 of wastewater generated by a residential complex of 130 students who stay in the University Student residence (REU) of UNRC. In the Pilot Plant, the treatment of liquid effluents is carried out by a pretreatment, primary treatment and secondary treatment, as explained below: Pretreatment REU effluents, discharged to a receiving chamber (Figure 1), where the material passes through a perforated stainless steel disc which acts as a first thick-prefilter material is, then poured by gravity into a steel cup stainless covered with perforations to operate as a second prefilter retaining the bulk might have passed the perforated disk. Every week the basket is retracted for cleaning, washed again and inserted in place. 14

Primary and secondary wastewater treatment
The receiving chamber accommodates two centrifugal pumps, which operate automatically whenever the chamber is stored in a volume of 3000 L effluent, sending to a sedimentation tank sludge 10,000 L capacity. From the settling tank sludge, separated liquids are referred to facultative lagoons with aquatic macrophytes for secondary treatment. 14

Experiment
In order to achieve the proposed objective, an experimental research was conducted to evaluate the decreased concentrations of BOD 5 (biochemical oxygen demand), COD (chemical oxygen demand), TSS (Total Suspended Solids) Nt (total nitrogen), Pt (total phosphorus) and Total Coliforms from urban effluents coming from Student Housing University (REU) of the National University of Rio Cuarto, after being treated by Wetlands Superficial with floating macrophytes (Lemnas), the varying the density of plants and hydraulic retention time (HRT) in winter season, with unfavorable climatic conditions for plant growth. In a second step, the TSS concentration in spring season was evaluated with higher temperatures. Six surface wetlands were constructed which scaled 2.10 m long, 0.90 m wide and 0.70 m deep, with a gradient of 1%. Sampler wells 0.50 m long, 0.30 m wide and 0.20 m deep were prepared. To complete the system a discharge pond of 2.00 m long, 1.00 m wide and 1.00 m deep was dug. Three wetlands were designed to accommodate floating plants, with a seeding density of 100% and the other three, conditioned with plant density of 50%. Assigning densities was randomized, and for this draws wetland was performed (Figures 2-4). Feeding wetlands with influent, was performed by derivatization with PVC pipe 50 mm in diameter and valve manifold system from a stabilizing pressure tank 1000 L with automatic floating, to maintain a constant load height of 1.2m in flow wetlands. This tank was fed, from the settling tank sludge. The experiment was factorial with two fixed factors: plant population density and HRT. Plant population density levels with two categories: 50% (D1) and 100% (D2), surface coverage of wetlands. Meanwhile HRT in continuous laminar flow, with two levels of categories: measured at 4 days (HRT 1) and one day (HRT 2), respectively in the period between 24.8.2013 and 29.8.2013 with waste effluent temperatures varying between 5 and 15 °C. In a second stage, the experiment was repeated for TSS, in the period between 30.11.2013 and 12.05.2013, with wetland temperatures varying between 16 and 23 °C. Thus, two treatment groups with 3 repetitions per every plant density were evaluated together with two hydraulic retention times were formed.    Table 1. For statistical analysis, a General Linear Model (GLM), 16 with two fixed factors and interaction purposes, to study the combined influence of both factors (density and HRT) was applied, resulting in no significant DENSITY *HRT interaction; consequently the General Linear Model analysis (GLM) with two fixed model without interaction factors for each of the variables BOD 5 , COD, TSS, Nt, Pt and total coliforms was repeated to obtain a better grade of adjustment (Table 2).  v. Density has no effect on Total Coliforms, probability p=0.232; However, HRT has high influence on the removal of Total Coliform (p=0.000).

Influent characteristics shows in
vi. The determination coefficient R 2 indicates that both the density and the HRT contribute 67.3%, 69.8%, 91.3%, 44.1% to the removal of BOD 5 , COD, PT and Total Coliforms, respectively.
In order to facilitate the preparation of conclusions about the behaviour of each of the variables under study, illustrative charts with the results of the experiment and the raw data obtained from laboratory report were developed.

BOD 5 (biochemical oxygen demand)
Parameter Influent: 134.6 (mg O 2 L -1 ) Plotting raw data of BOD 5 obtained from laboratory tests, you can see the result of the experiment together ( Figure 5).

COD (Chemical Oxygen Demand)
Parameter Influent: 263.2 (mg O 2 L -1 ) Graphing the raw data obtained from the COD laboratory tests, you can see the result of the experiment together ( Figure 6):

TSS (total suspended solids) in winter season
Parameter influent: 510 (mg L -1 ) Plotting raw data of TSS obtained from laboratory tests, you can see the result of the experiment together ( Figure 7): In the above graph it shows that all samples have similar values, except the wetland H3 50% with HRT2, which has an anomalous value justified by the laboratory, high turbidity reported in that sample.
Descriptive for the dependent variable statistical TSS during winter indicate that: a. For 50% and 100% of plant density and HRT1 and HRT2, obtained averages were greater than influent of 510 mg L -1 .

TSS (total suspended solids) in spring
Parameter influent: 224 (mg L -1 ) Plotting raw data of TSS obtained from laboratory tests, you can see the result of the experiment together ( Figure 8):  c. It also shows that the influent parameter in the spring is 224 mg L -1 , significantly lower than the influent during the winter of 510 mg L -1 .

Total Nitrogen
Influent parameter: 38.53 (mg L -1 ) Plotting raw data obtained from the NT laboratory analysis, you can see the result of the experiment as a whole (Figure 9):

Total Phosphorus
Parameter Influent: 2.4 mg L -1 Plotting raw data of PT obtained from laboratory tests, you can see the result of the experiment together ( Figure 10 b. For 100% plant density, TRH1 and TRH2 results showed no influence of the independent variables on the removal of total phosphorus.

Conclusions
From the results presented, we conclude that (Table 3): i. The Density of plant cover significantly influences the BOD 5 and COD, obtaining better performance at lower % coverage of macrophytes (Lemnas).
ii. The Hydraulic Retention Time also significantly influences the BOD 5 and COD, yielding better performance at longer hydraulic retention times.
iii. There is no evidence that both the Density and the Hydraulic Retention Time have influence on Total Suspended Solids  vi. The Density of plant cover significantly influences the Total Phosphorus obtaining better performance at lower % coverage of plants.
vii. The Density of plant cover does not significantly influence the removal of total coliforms.
viii. The Hydraulic Retention Time influences and is highly significant on the removal of total coliforms having been obtained in this experiment, yields of 96% to longer Hydraulic Retention Time.
ix. It would probably be necessary to experiment with longer Hydraulic Retention Time to those adopted for this experiment, in order to obtain variations in the results of NT and TSS. 17