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Brazilian Journal of Chemical Engineering

Print version ISSN 0104-6632On-line version ISSN 1678-4383

Braz. J. Chem. Eng. vol.33 no.4 São Paulo Oct./Dec. 2016

http://dx.doi.org/10.1590/0104-6632.20160334s20150264 

Selected papers from the XI Latin American Symposium on Anaerobic Digestion (DAAL-2014)

EVALUATION OF POTENTIAL METHANE GENERATION IN THE INVESTIGATION OF AN ABANDONED CONTAMINATED LANDFILL IN SANTIAGO, CHILE

I. Cortés1  * 

S. Montalvo2 

1Centro Nacional del Medio Ambiente, Larraín 9975, La Reina, Santiago, Chile. E-mail: isel.cortes.nodarse@gmail.com; lqa.cenma@gmail.com

2Departamento de Ingeniería Química, Universidad de Santiago de Chile.


Abstract

This study presents the environmental evaluation of an abandoned and potentially contaminated landfill using analyses for the presence of heavy metals and for methane generation potential. The site is located in the city of Santiago, Chile, and was used as a rural landfill for domestic, industrial and construction waste until 1978, but is now in a heavily urbanized area and surrounded by houses. Analyses performed on 24 samples taken in and around the site show Potential Methane Generation (PMG) values between 1.6% and 11.3% of maximum projected levels. These low values, compared to those of an active landfill, indicate that waste material stored in the site has a low capacity to generate methane. Concentrations of heavy metals in the surface and deep soil are similar to typical levels for these metals in normal soil, according to international USEPA standards, and do not present imminent risk to human health. The use of the PMG test technique for the study of the health risk of an abandoned landfill is a new contribution to the Chilean evaluation methodology and management program for Abandoned Sites with Potential Presence of Contaminants (SAPPC). As part of the environmental management strategy for the site, two of the five operable units studied were transformed into a park after this study.

Keywords: Abandoned landfill; Methane; Solid waste; Contaminated sites

INTRODUCTION

Studies related to the potential presence of contaminants in soils at a site are varied and usually develop as a prior and fundamental step in the evaluation of remedial alternatives, recovery of the site for different uses, or both, depending on the characteristics of the location. However, there is no definitive, common methodology applied to all situations. To deal with this limitation, several comparative models have been developed to establish the presence of abnormal levels of contaminants at a specific site under study (Aslibekian and Moles, 2003; Muhlbachova et al., 2015; Rodríguez et al., 2015; Wen et al., 2015; Khan et al., 2008). For example, since 1995 in the United Kingdom it has been known that soils within 1 to 3 km of metal smelters may contain up to 15 times the natural values of Pb in the soil and also may present high concentrations of Cd at distances as far as 40 km from the originating industrial activity (Aslibekian and Moles, 2003).

In polluted soils, interactions between heavy metals, organic matter content and microorganisms have been correlated (Muhlbachova et al., 2015). Increasing concentrations of metals in the urban environment have been studied, wherein concentrations of Cd, Ni and Cr measured in plant leaves in 2012 exceeded those reported in 1941 for the same species by factors of 10, 13 and 16, respectively (Rodríguez et al., 2015). The increase of these pollutants in the urban atmosphere was related to human activity changes during a period of more than 70 years. The anaerobic biodegradation of domestic and industrial waste in landfill sites goes through a complex process and therefore it is not easy to estimate the biological conversions involved. Measurements at these sites must be performed carefully taking into account different waste sources such as pharmaceutical residues, plastic products, antibiotics, and complex organic compounds (Wen et al., 2015; Khan et al., 2008; Kumar et al., 2004; Aguilar-Virgen et al., 2011; Aguilar-Virgen et al., 2012; Angelidaki and Sanders, 2004; Stergar and Zagorc, 2002; ISO 11734, 2012; Kolstad et al., 2012; Gartiser et al., 2007; El-Mashad et al., 2012; Angelidaki et al., 2006).

Human activities in Chile have generated locations known as Abandoned Sites with Potential Presence of Contaminants (SAPPC), such as old landfills, uncontrolled dumpsites, or industrial waste sites. When abandoned, these sites may be converted to new land uses without additional regulation. Studies of contaminants in soils at these and other sites have been performed considering the type and extent of pollutants in the involved area (Romero et al., 1999; Ginocchio et al., 2004; Molina et al., 2009; Escudey et al., 2007; Badilla-Ohlbaum et al., 2001; Palma-Fleming et al., 2000). The systematic evaluation of SAPPC in Chile began only 5 years ago, in 2010, and has targeted defined areas that have been environmentally impacted by one or more potentially polluting activities, which ended at some point without a proper site closure process.

In 2012, the Chilean Government began to apply a national methodology (Chilean Government, 2012) to identify and confirm the presence of contaminants at these sites. This methodology contains an ordered sequence of activities whose first step is the application of criteria to identify and prioritize SAPPC sites within each region. Subsequently, in step two, the Preliminary Investigation collects and analyses site historical information. In step three, the Confirmatory Investigation collects and analyses site samples. See Figure 1.

Figure 1 Illustration of the Chilean SAPPC.Evaluation Methodology developed and conducted by the Ministry of Environment 

The Confirmatory Investigation of the SAPPC methodology, as shown in Figure 2, is designed to determine representative concentrations of pollutants present at the potentially contaminated site, which are then compared with reference criteria to confirm whether or not the suspected contaminant levels pose a preliminary risk to potential receptors.

Figure 2 Flow Diagram for the SAPPC Confirmatory Investigation. 

Suitable methods of analysis for this study were selected for quantifying the presence of heavy metal contaminants. To evaluate an abandoned landfill under the SAPPC methodology, it is crucial to establish the levels of landfill gas (biogas, consisting of CH4, CO2, H2S, N2). However, the current Chilean SAPPC methodology does not contain details about how to establish these levels.

This paper presents a case study including the evaluation of Potential Methane Generation (PMG) in the Confirmatory Investigation of an abandoned landfill in the city of Santiago, Chile. This study of PMG as a methodology for determining the landfill gas levels is an important contribution to the advancement of the Chilean SAPPC Evaluation Methodology.

METHODS

The SAPPC known as La Cañamera in Santiago, Chile, had an area of 25 hectares and received residential, industrial and construction waste between 1962 and 1978. Wastes deposited there were from five municipalities located in the southern part of the city and were placed using a rudimentary landfill technique that did not include the use of impermeable barriers or other special protective measures. After the closure of the landfill, the land was parceled out and used for different objectives, including the construction of residential housing. It was expected that soils in a landfill such as this one might contain heavy metals, gas and other pollutants.

The test area was divided into six operable units, taking into account the different uses and owners of each sector. 30 representative sampling points were identified throughout the area, with each sample point consisting of a surface zone, a trash zone and a deep soil zone. 80 soil samples and 24 trash samples were collected for later evaluation of PMG, metal concentrations, pH levels and extrinsic toxicity. The extrinsic toxicity was measured using the Toxicity Characteristic Leaching Procedure (TCLP) according to USEPA Test Method 1311, established in the Resource Conservation and Recovery Act (RCRA) of the United States and in the Chilean regulations for industrial wastes.

Abandoned landfills are characterized by a heterogeneous distribution of domestic and industrial waste. Similarly, the generation of methane or landfill gas is a problem in these sites and can manifest weakly at the surface while the sub-surface trash can retain a significant capacity for generating gas via anaerobic biological conversion. The presence of heavy metals is related to their environmental persistence following deposition of metal-containing wastes from industrial and domestic sources.

Potential Methane Generation was evaluated according to the principles described in the 2009 Columbian Technical Standard NTC4233 "Environmental Management. Water quality. Evaluation of the ultimate anaerobic biodegradability of organic compounds in digested sludge. Method by measurement of the biogas production", with some minor modifications for solid residue evaluation. The method consists of carrying out the anaerobic digestion of solid residues in 500 ml batch reactors at 35° C, which have been previously inoculated with microorganisms adapted to these residues. A solution of trace micronutrients was used in this study to ensure the best conditions for anaerobic digestion. The main compounds of this solution were MnCl2.4H2O, H3BO, ZnCl2, CuCl2, Na2MoO4, CoCl2.6H2O, NiCl2.6H2O and Na2SeO3, according to the requirements for methanogenic archaea microorganisms (Milán et al., 2010; Ortner et al., 2014; Pereda et al., 2006).

Figure 3 shows the experimental procedure setup schematic for one reactor. To achieve the anoxic conditions inside the reactor, the system was flushed with nitrogen gas for 20 minutes before the beginning of digestion, thereby eliminating any oxygen that might have been present in the reactors. The pH of the reactor medium was adjusted with NaOH to 7 ± 0.2. Methane production during digestion was measured by displacement of a saturated solution of NaOH during 35 days of anaerobic digestion. The measured methane volume was compared with the expected theoretical volume. In this case, it was determined that the amount of landfill-waste methane generated would be 170 L per kg of waste. Since the reactor would work with 100 g of waste, it would therefore be expected to generate a maximum biogas volume of 17 L. The Potential Methane Generation (PMG) result was expressed as a percentage of the theoretical value.

Figure 3 Experimental setup for the anaerobic reactor. 

The CH4 and H2S levels in the biogas were determined using a Gas Chromatograph, model Perkin Elmer GC Clarus 500/580. The determination of metal concentrations in both the soil samples and garbage samples was performed using a Perkin Elmer Optima 3000 ICP according to standard protocols based on official methods of the US-EPA (US-EPA, 1992; US-EPA-a, 2007; US-EPA-b, 2007; US-EPA-c, 2007). Figure 4 shows the physical installation for the experimental anaerobic digesters

Figure 4 View of anaerobic reactors in a thermostatically controlled bath (35 ºC). 

Potential Methane Generation was calculated as PMG(%) = (Vg(L)·100)/17 L.

RESULTS AND DISCUSSION

Figures 5 to 9 contain the location maps and results tables for the operable units in the study. Each table includes a short description of the current land-use for the unit and the thickness of each excavated layer according to the following description: Layer 1-Unconsolidated solid surface material, Layer 2-Trash, Layer 3-Deep soil. Other tabulated results include the pH range in each layer, range of PMG % and range of H2S in Layer 2, and the metal concentration range in each layer. The results observed for Operable Unit Parcels 3 and 4 (Figure 7), and Operable Unit Residential Within Abandoned Landfill (Figure 9) are not shown, but are similar to the results shown for the other units.

Figure 5 Location and Results for Operable Unit Parcel 5. 

Table 1 Range of Values for Operable Unit Parcel 5 

Layer 1 Layer 2 Layer 3
Thickness (cm) 40-70 40-280 40-210
pH 6.57-7.53 6.65-7.98 6.85-7.23
PMG (%) - 0-6.0 -
H2S (%) - <0.02 -
Cd mg/kg <0.06-0.85 <0.06-2.63 <0.06-0.64
Zn mg/kg 18.1-148.2 341-1156 29.6-515
Cr mg/kg 13.4-28.3 10.9-420.6 11.2-253
As mg/kg <2.39-22.8 <2.39-23.3 <2.39-12.6
Cu mg/kg 44.4-128,1 242-1085 49.5-392
Pb mg/kg 10.9-28.8 102-1478 15.2-243.4
Al mg/kg 3159-16076 4924-18562 4729-11764
Se mg/kg <1.8 <1.8 <1.8
Ni mg/kg <0.38-18.0 <0.38-29.0 <0.38-21.3
V mg/kg 198.9-182 74.4-138.8 95.1-198.2
Ba mg/kg 10-50.1 24.9-249 26.6-59.2
Co mg/kg 11.8-29.9 11.8-24.5 12.9-30.7
Mo mg/kg <0.31-1.32 1.29-9.94 <0.31-3.35
B mg/kg <0.46-99.4 <0.46-144.8 1.98-180.4
Fe mg/kg 9288-57523 8025-76629 1655-41467
Mn mg/kg 232-871 339-990 307-844
Hg mg/kg 0.04-59.7 0.41-12.7 0.05-1.07

Figure 6 Location and results for Operable Unit Current Park. 

Table 2 Range of values for Operable Unit Current Park 

Layer 1 Layer 2 Layer 3
Thickness(cm) 9-10 120-190 80- 20
pH 7.65-7.99 7.48-7.73 7.69-7.94
PMG (%) - 0-5.8 -
H2S (%) - <0.02 -
Cd mg/kg 1.38-2.51 0.78-1.93 <0.06-1.24
Zn mg/kg 551-713 587-838 87.7-280
Cr mg/kg 122-236 43-468 25.5-79.4
As mg/kg 5.31-19.9 5.06-9.83 <2.39-5.29
Cu mg/kg 359-2411 99-2312 66.4-221
Pb mg/kg 301-807 30.4-1082 <0.27-104
Al mg/kg 4610-9501 5536-7367 3610-79663
Se mg/kg 7.81-18.2 6.87-16.6 4.56-14.9
Ni mg/kg 25.9-43.0 13.6-63.2 10.0-17.1
V mg/kg 83.9-116.2 62.6-102.3 92.6-120.4
Ba mg/kg 20.3-57.5 43.6-48.7 15.4-292.5
Co mg/kg 15.7-25.3 11.6-22.4 14.8-19.2
Mo mg/kg 9.71-16.5 2.64-4.11 <0.31-1.63
B mg/kg 100-297 114-241 75.5-150.4
Fe mg/kg 25693-46569 30547-40477 20766-40602
Mn mg/kg 487-640 567-6227 413-865,8
Hg mg/kg 0.60-2.88 0.65-65.4 0.12-32.0

Figure 7 Location of Operable Unit Parcels 3 and 4. 

Figure 8 Location and results for Operable Unit Property Reserve. 

Table 3 Range of values for Operable Unit Property Reserve 

Layer 1 Layer 2 Layer 3
Thickness(cm) 70-170 120-230 80-130
pH 7.03-7.54 6.36-6.96 6.85-8.16
PMG (%) - 2.3-11.3 -
H2S (%) - <0.02 -
Cd mg/kg <0.06-0.45 <0.06-9.02 <0.06
Zn mg/kg 72.9-130.4 264-1313 49.5-109
Cr mg/kg 21.9-32.6 101,7-853.3 19,1-34.8
As mg/kg <2.39-8.0 <2.39-15.4 <2.39-7.0
Cu mg/kg 52.3-95.7 199.6-1319.5 56.9-60.8
Pb mg/kg 15.4-44.4 178.5-360.7 5.69-35.8
Al mg/kg 7211-7930 4961-27085 6376-11788
Se mg/kg <1.8 <1.8 <1,8
Ni mg/kg <0.38-17.0 <0.38-21.5 <0.38
V mg/kg 124-131 68.7-108.3 121-146.2
Ba mg/kg 27.9-52.4 46.1-166.2 35-45
Co mg/kg 16.4-20.1 9.5-16.1 15.1-18.4
Mo mg/kg 0.51-2.92 3.9- 5.4 <0.31-1.63
B mg/kg 87.6-176 20-141 25.6-146.8
Fe mg/kg 21199-29789 32322-41350 19998-39490
Mn mg/kg 265-428 520-685 303-401
Hg mg/kg 0.06-0.18 0.65-1.16 0.12-0.68

Figure 9 Location of Operable Unit Residential Within Abandoned Landfill. 

Garbage was found in 24 of the 30 perforated pits, with differing levels of degradation, in thicknesses ranging between 40 and 370 cm across the sector. No garbage was found at the sample points located outside of the landfill boundary.

In 8 of the 24 samples analysed, the biogas levels recorded were zero, indicating that in these areas the garbage had completely stabilized. The non-zero measured PMG values were between 1.6% and 11.3%. The maximum PMG value found (11.3%) belonged to a sample with the characteristic odor and oily black appearance of industrial garbage and was explained by the extended stabilization time expected for this type of garbage.

In general, all observed PMG values are low compared to an active landfill. This indicates that the trash has achieved an advanced state of degradation, but still maintains a low capacity to generate methane under appropriate conditions. These results are consistent with previous studies conducted at the site in 2004, and are relatively similar to those reported in the study by Kristman (2009) in the area called Parcel 5, showing that the garbage had a low capacity to decompose. It is important to take into account that there is ample evidence that La Cañamera received wastes more than 35 years ago and, as such, there is not expected to be any further increase in the anaerobic degradation rate of the garbage stored in the site.

At the end of each sample digestion process, the methane and hydrogen sulfide content of the resulting biogas was determined. The methane volume fraction varied between 50% and 55% while the hydrogen sulfide volume fraction was generally near the detection limit of 0.02%. The low H2S concentration in sanitary landfill biogas has been reported in other studies. Desideri et al. (2003) found that the concentration of hydrogen sulfide (0-200 ppm) and carbon monoxide (0-500 ppm) in sanitary landfill biogas was very small and therefore negligible for their study. Jaffrin et al. (2003) also found that the hydrogen sulfide concentration in sanitary landfill biogas was very low at only 100 ppm (0.01%). Themelis and Ulloa (2007) stated that sanitary landfill biogas has an H2S volume fraction less than 1%, while Nikiema et al. (2007) found a level of 0-0.2%. The low proportion of sulfur compounds present in municipal solid waste explains these low H2S concentrations (Zhou et al., 2014; Hla and Roberts, 2015).

For all the metals tested (Cd, Zn, Cr, Cu, Pb, Al, Ni, V, Se, As, Ba, B, Co, Mo, Mn, Fe, Hg), the highest concentrations were found in the garbage layer, when compared to the concentrations found in the unconsolidated solid surface and deep soil layers. This is because domestic and industrial wastes often contain metallic components.

The garbage layer in the site was covered with a layer of filler soil approximately one meter thick. The concentrations of heavy metals found did not exceed either the natural metal concentrations in Chilean soils or the human health risk standards defined by the United States Environmental Agency (USEPA) in its Superfund Site Remediation program.

At present, the operable units identified as Parcel 5 and Actual Park have been transformed into a park, while maintaining the contained garbage, and have chimneys installed for monitoring the emissions of methane gas that may be released from the trash layer. The land-use change management, for the other sectors of the site, is planned for execution at later dates due to differing legal and environmental action requirements.

The results obtained in this study are consistent with the general principles discussed by the WHO study of contaminated sites (WHO Regional Office for Europe, 2000). Therefore, this testing shows that the Potential Methane Generation (PMG) methodology should be added to the standard methodology for the assessment of contaminated soils in Chile.

CONCLUSIONS

Study development and analyses have identified PMG values between 1.6% and 11.3% in 16 of the 24 garbage samples taken at the landfill site. These values are low compared with an active landfill, which indicates that the trash stored in the site has achieved an advanced state of degradation, but still maintains a low capacity to generate methane under appropriate conditions.

Concentrations of heavy metals in the surface material layer that covers the trash and in the deep soil layer do not represent imminent risk to human health and do not exceed the normal levels of metals in soils.

The usefulness of the Potential Methane Generation (PMG) test for risk assessment of abandoned landfill sites has been demonstrated, which is an important contribution to the Chilean methodology for evaluation and management of SAPPC. After the completion of this study, the environmental management plan for the site transformed two of the operable units studied into a park.

This is an extended version of the work presented at the XI Latin American Symposium on Anaerobic Digestion (DAAL-2014), Havana, Cuba.

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Received: April 26, 2015; Revised: August 30, 2015; Accepted: August 31, 2015

*To whom correspondence should be addressed

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