INTRODUCTION
The Mexico City Metropolitan Area (MCMA) is a complex megacity with a mixture of CO2 emission sources, where atmospheric radiocarbon (14C) variability is influenced mainly by changes in fossil fuel combustion and biomass burning from residential combustion, agricultural burning and wildfires in the mountains surrounding the valley, common during the dry season (winter and spring) (Beramendi-Orosco et al. Reference Beramendi-Orosco, González-Hernández, Martínez-Jurado, Martínez-Reyes, García-Sámano, Villanueva-Díaz, Santos-Arévalo, Gómez-Martínez and Amador-Muñoz2015, Reference Beramendi-Orosco, González-Hernández, Martínez-Reyes, Morton-Bermea, Santos-Arévalo, Gómez-Martínez and Villanueva-Díaz2018). Previous studies have reported Δ14C levels in MCMA up to 75‰ and 27‰ higher than regional background values during the hot and dry season (Vay et al. Reference Vay, Tyler, Choi, Blake, Blake, Sachse, Diskin and Singh2009 and Beramendi-Orosco et al. Reference Beramendi-Orosco, González-Hernández, Martínez-Jurado, Martínez-Reyes, García-Sámano, Villanueva-Díaz, Santos-Arévalo, Gómez-Martínez and Amador-Muñoz2015, respectively), attributed to the release of 14C-enriched CO2 resulting from the burning of soil organic matter during agricultural and wild fires in the basin, suggesting this is a significant CO2 emission source as it cancels out the 14C dilution resulting from the vast amount of fossil fuels burned this metropolitan area with high population density. These observations could result in an underestimation of the atmospheric fossil CO2 concentration in the MCMA, hampering the direct use of 14C as a tracer of fossil CO2 emissions in such a complex urban area (Beramendi-Orosco et al. Reference Beramendi-Orosco, González-Hernández, Martínez-Reyes, Morton-Bermea, Santos-Arévalo, Gómez-Martínez and Villanueva-Díaz2018).
According to the latest published emissions inventory, in 2018 the MCMA emitted more than 66 million tons of CO2, mainly from the transport sector (65.4%) with diesel and gasoline as the main fuels. Other important CO2 sources are from the industrial sector, contributing with nearly 20% of the total emissions, and domestic combustion of natural gas, liquid propane gas and biomass, estimated to contribute up to 5.2%. Emissions from electricity generation and distribution accounts for 4.5% and the remaining 5% is attributed to other sources, including forest fires, landfills, and open combustion (SEDEMA 2021).
The greenhouse gases and other contaminants emitted within the MCMA are not easily dispersed because the basin is a closed valley surrounded by mountains and, depending on meteorological conditions, can result in air stagnation usually during the dry months (November–May), causing an increase in the concentration of air pollutants, mainly ozone and particulate matter (PM10 and PM2.5). The local environmental authority operates an atmospheric monitoring system (SIMAT) consisting of 24 automated monitoring stations distributed throughout the MCMA that analyse the concentration of CO, NO2, O3, SO2, PM10, and PM2.5 (criteria pollutants) on an hourly basis. When the concentration of a particular air pollutant surpasses an established air quality threshold depending on the pollutant, restrictions are imposed to industries and particular vehicles to reduce emissions until the pollutants concentration decrease again to acceptable levels. These restrictions usually last for one or two days depending also on changes of the meteorological conditions promoting ventilation of the valley. The SIMAT, however, does not include measurements of CO2 concentration, making it difficult to identify changes in emission sources of this greenhouse gas and evaluate the effect of the actions taken to improve air quality and meet the reduction targets of greenhouse-gas emissions.
To stop the spread of the COVID-19 epidemic, the Mexican government imposed restrictions from March 2020, starting with a partial lockdown (phase 1) closing schools and universities on 20th of March 2020, extending to all non-essential activities with a significant reduction in private and public transport services on 31st of March (phase 2), and further restrictions with a complete lockdown imposed on 21st of April, when the country started the phase of higher risk of COVID-19 transmission (phase 3). This complete lockdown lasted up to 31st of May. From 1st of June some non-essential activities were gradually opened with some restrictions in place up to 2021, and schools and universities remaining closed up to September 2021 (Table 1). From this point, the government implemented a colour-coded system according to the epidemic risk level, with red indicating extremely high risk advising population to stay at home and imposing some restrictions in non-essential activities; orange for high epidemic risk with non-essential activities open only to 75% capacity; yellow to denote moderate risk with non-essential activities operating to 50% capacity, and green for low risk with no restrictions (Secretaría de Salud 2020). These social distancing measures for stopping the COVID-19 propagation, resulted in an important reduction of the urban activities, mainly reflected in traffic and public transport. The volume of fossil fuels sold by the national petroleum company, PEMEX, in the MCMA reflect these changes, with a decrease of 45%, 49% and 35% during April, May and June 2020, respectively, in comparison to the volume sold during the same months in 2019 (SENER, 2022). This is in accordance with the fact that 50% of the fossil fuels consumed in the MCMA are used by the transport sector (SEDEMA 2021).
Chronology of COVID-19 lockdown phases and restrictions and in Mexico City Metropolitan Area. (Data from https://www.gob.mx/salud/documentos/comunicados-tecnicos-diarios-COVID19)
A previous work reported an evaluation of the effect of the COVID-19 lockdown phases 2 and 3 on the concentration of criteria air pollutants in the MCMA (Hernández-Paniagua et al. Reference Hernández-Paniagua, Valdez, Almanza, Rivera-Cárdenas, Grutter, Stremme, García-Reynoso and Ruiz-Suárez2021), finding that during phase 2 only NO2 decreased significantly (between 10% and 23%), while O3 increased up to 40%. During phase 3, NO2, PM10, and PM2.5 decreased by 43%, 20%, and 32%, respectively, and O3 decreased in relation to phase 2, but did not show a significant decrease in comparison to the baseline.
To gain a better understanding of changes in CO2 emissions in MCMA during the COVID-19 pandemic, we report atmospheric 14C concentrations from CO2 monthly-integrated samples taken between January 2019–December 2021 at the southern area of the MCMA and explain the variations in terms of the COVID-19 lockdown phases and epidemic risk level.
METHODOLOGY
Study Area and Sampling Site
The MCMA has an area of 7866 km2 located in a high-altitude (∼2300 m.a.s.l.) closed basin surrounded by mountains, including the Popocatépetl active volcano located at 50 km southeast. According to the latest emissions inventory for the MCMA, in 2018 there were 21.69 million inhabitants, 6.3 million households, 6.01 million registered vehicles, and more than 1900 regulated industries, located mainly in the northwestern and central areas (SEDEMA 2021). About 64% of the area can be classified as urban whereas 34% correspond to conservation areas, including rural soils, forests, and shrublands, mainly located on the mountains to the South, East and West. The climate is tempered by altitude and influenced by tropical air masses during summer (May to October) and mid-latitude cold air masses from North America during winter (Jauregui Reference Jauregui2004). The mean annual temperature is 16°C and the annual precipitation, concentrated in summer months, is 400–500 mm in the northern part of the basin and 700–1200 mm in the central and southern parts (Jauregui Reference Jauregui2004; INEGI 2014).
The sampling point is located on the rooftop of a 3-story building inside the main campus of the Universidad Nacional Autónoma de México (UNAM), located at the southern end of the urban area of Mexico City (Figure 1). The campus comprises 700 Ha, of which about 237 Ha correspond to the “Pedregal de San Angel” ecological reserve. The campus is located over a basaltic substratum deposited during the eruption of the Xitle volcano. Vegetation at the reserve has a xerophilous scrubland aspect, with most species showing resistance to drought. Most plant species are herbaceous or shrubby, although it is also possible to find 7-m trees (Rzedowski and Rzedowski Reference Rzedowski and Rzedowski2005; Castillo et al. Reference Castillo-Argüero, Martínez-Orea, Romero-Romero, Guadarrama-Chávez, Níñez-Castillo, Sánchez-Galien and Meave2007). Elsewhere, vegetation is dominated by introduced species in gardens and roads.
Map of Mexico City and its Metropolitan Area (white line) showing location of sampling point (star). Modified from SEDEMA (http://www.aire.cdmx.gob.mx/default.php?opc=%27ZaBhnmM=%27).
Sampling Procedure and 14C Analysis
Integrated samples were collected by pumping air (20 mL min–1) through a column with 1 L of a 0.7M NaOH solution (carbonate-free, Sigma-Aldrich Mexico) for about 30 days during day-time only, at a height of 9 m from ground level at a well-ventilated point on the rooftop of the building housing the preparation laboratory. To avoid contamination with atmospheric CO2 not corresponding to the sampling period, the NaOH solution was prepared in situ immediately before sampling started, and captured CO3 2- was precipitated also in situ as BaCO3 by adding an excess of BaCl2 solution immediately after sampling stopped. The precipitated barium carbonate was recovered from solution within a few hours, washed with bi-distilled water, and dried at 50°C in the laboratory located on the ground floor of the building where sampling was performed. Once dried, samples were stored in sealed glass jars inside a vacuum desiccator before being sent for analysis.
Samples for the period January 2019–June 2021 were analyzed by accelerator mass spectrometry (AMS) at the Centro Nacional de Aceleradores (CNA), Seville, Spain. Prior to measurement, samples were graphitized using a Carbonate Handling system coupled to an AGE system. Analysis was performed using a MICADAS system. Samples for the period July–December 2021 were analyzed at the Keck Carbon Cycle AMS facility at University of California Irvine. All 14C results are reported as Δ14C corrected for both isotopic fractionation and decay between 1950 and year of sample collection (Stuiver and Polach Reference Stuiver and Pollach1977). The error quoted corresponds to the ± 1σ reported by each laboratory, but the actual uncertainty of the data may be higher due to other factors that were not accounted for, such as minor contamination or variability in sample preparation procedures.
RESULTS
Radiocarbon concentrations for integrated CO2 samples collected in MCMA for the period January 2019–December 2021 are plotted in Figure 2 and tabulated in the supplementary file. Niwot Ridge Δ14C preliminary data, considered the regional background values (Lehman and Miller Reference Lehman and Miller2019; Lehman et al. Reference Lehman, Miller, Wolak, Southon, Tans, Montzka, Sweeney, Andrews, LaFranchi, Guilderson and Turnbull2013), are also plotted for comparison as discussed below.
Δ14C values for integrated CO2 samples collected in MCMA (open circles) and for Niwot Ridge as regional background values (gray triangles, data from Lehman and Miller [Reference Lehman and Miller2019] and Lehman et al. [Reference Lehman, Miller, Wolak, Southon, Tans, Montzka, Sweeney, Andrews, LaFranchi, Guilderson and Turnbull2013]). Average Δ14CNWR values with the corresponding 95% confidence interval (dark triangles and solid lines) were calculated for estimating the mean background value during the same sampling period in MCMA. Vertical lines mark dates of lockdown phases and red code periods (extremely high epidemic risk).
Comparison with Background Δ14C Values
Radiocarbon observations for MCMA are, except for two samples, lower than background values and vary over a wide range from -44.15‰ to 2.25‰, which appears to be a result from a complex mixture of CO2 emission sources with different 14C concentration and changes in the volume of fossil fuels consumption in MCMA. All data obtained for samples collected during 2019 and 2021 are significantly lower than data reported for NWR. For the period January–December 2019, values reported for Niwot Ridge range between –7.5‰ (May) and +7.5‰ (August); whereas values found for Mexico City range between –44‰ (December) and –13‰ (October). For 2021, the reported data for NWR cover only up to June with values ranging from –10‰ (May) to –1.5‰ (March), while values for samples from MCMA range from –32.89‰ (November) to –10.27‰ (January-February). On the other hand, Δ14C values for samples collected in MCMA during the period March–September 2020, when more strict lockdown restrictions were in place, are of the same magnitude as the data reported for Niwot Ridge. For 2020, the NWR values range between –9‰ (February) and 4.5‰ (June) while for MCMA range between –27.74‰ (January) and 2.2‰ (June), with values for May and July of the same order as the background values. This suggests that the increase in atmospheric 14CO2 concentration in MCMA to values similar to those registered at a background site is a result of the significant reduction in fossil fuels consumption associated with the different phases of the lockdown and epidemic risk level during the COVID-19 pandemic in Mexico. To explore this further, the volume of fossil fuels sold for vehicle traffic (gasolines and diesel) reported by the Mexican Petroleum company (PEMEX) is plotted in Figure 3 together with the difference between the background and observed values (ΔΔ14CNWR-MCMA) and the correlation plot comparing both, the Δ14C and ΔΔ14CNWR-MCMA to the volume of fossil fuels. The Pearson correlation coefficient between the sales of fossil fuels and Δ14C values is r=–0.4675 (p<0,01) and a r=0.7328 (p<0.001) is obtained when comparing against ΔΔ14CNWR-MCMA, confirming the potential of 14C as a tracer of fossil CO2 in the atmosphere of this complex urban area. Furthermore, the fact that the correlation between ΔΔ14CNWR-MCMA and fuels use is higher than the correlation between Δ14C and fuels use, demonstrates that when the long-term trend is removed by subtracting background, the local impact of fossil fuels on the atmosphere becomes much clearer.
Difference between calculated average background values and observed values (ΔΔ14CNWR-MCMA) with the lockdown phases indicated by vertical lines (top panel). Volume of gasolines and diesel sales in the MCMA (Secretaría de Energía, data taken from https://sie.energia.gob.mx/bdiController.do?action=cuadro&cvecua=PMXE2C03) (center panel) and correlation plot comparing the volume of fossil fuels sales to the Δ14C (black circles and black solid line) and to the ΔΔ14CNWR-MCMA (gray triangles and gray dashed line) (bottom panel).
Atmospheric 14CO2 Variations in MCMA during 2019
Samples collected during 2019 have Δ14C values ranging between –44.15‰ and –13.17‰ (Figure 2). Higher values were found for samples collected during April, September, and October, although differences are of the same magnitude as the analytical uncertainty reported by the laboratories. On the other hand, significantly lower values were found for samples collected during January, May and December. The dispersion of values confirms the complexity of emission sources in the MCMA previously reported (Beramendi-Orosco et al. Reference Beramendi-Orosco, González-Hernández, Martínez-Jurado, Martínez-Reyes, García-Sámano, Villanueva-Díaz, Santos-Arévalo, Gómez-Martínez and Amador-Muñoz2015, Reference Beramendi-Orosco, González-Hernández, Martínez-Reyes, Morton-Bermea, Santos-Arévalo, Gómez-Martínez and Villanueva-Díaz2018). The apparently higher values found for April may be a result of the 14C-enriched CO2 released form the numerous forest and agricultural fires around MCMA (Figure 4), whereas higher values found for September and October 2019 seem to be related to the contribution from soils heterotrophic respiration at the end of the rainy season, as during these months the number of fires is low (Figure 4). By contrast, lower values found for May 2019 may be attributed to air stagnation and low ventilation of emissions in the valley during an extraordinary four-days period (14–17 May 2019) when pollution levels were extremely higher than the recommended guidelines. The low values found for January and December 2019 may be related to both, an increase in fossil fuels consumption for domestic combustion during winter, and pollutants accumulation during days with meteorological conditions that promote air stagnation. This is also in accordance with the low number of fires registered around MCMA during these months (Figure 4), suggesting the contribution of 14C-enriched CO2 from this source is low.
Fires and hot spots registered around the Mexico City Metropolitan Area during some sampling periods. Images taken from NASA’s Fire Information for Resource Management System (FIRMS) available at https://firms.modaps.eosdis.nasa.gov/.
Atmospheric 14CO2 Variations in MCMA during the COVID-19 Pandemic
For samples collected during 2020, Δ14C values range between –17.7‰ and +2.25‰ (Figure 2), with a rising trend immediately after the beginning of the lockdown phase 1 (20th March, Table 1), reaching the higher values during the lockdown phases 2 and 3 (April – June). From 1st of July, when the non-essential activities gradually opened according to the epidemic risk level, Δ14C values follow a decreasing trend until December 2020. For samples collected during 2021, Δ14C values range between –32.89‰ and –10.27‰; with a general decreasing trend and apparent peaks for samples collected during January–February, May, and October, although variations are of the same order as the analytical uncertainty, they may be a result of changes in the epidemic risk level, as discussed next.
The Δ14C variations seem to be related to changes in fossil CO2 emissions associated to the different stages of lockdown and epidemic risk (Table 1). First, for April 2020, the number of fires around MCMA registered is similar to those registered during April 2019 (Figure 4); however, the Δ14C value obtained for the sample collected during April 2020 is higher, suggesting this could be partly attributed to the 14CO2 emitted by the fires and partly to the decrease in the emission of fossil fuels-derived CO2 during the lockdown phases 1 and 2. This is in good agreement with the reduction in gasolines and diesel sales in the MCMA, 47% if compared to same month in 2019 (Figure 3). The higher Δ14C values were obtained for samples collected between May and June 2020, during the complete lockdown period of phase 3 and extremely high level of epidemic risk, reflecting a significant decrease in fossil CO2 emissions and in good agreement with the 52% and 38% decrease in fossil fuels consumption in MCMA during May and June, respectively. Interestingly, results for the samples collected during lockdown phases 2 and 3 are also in accordance with the reduction in NO2 found by Hernández-Paniagua et al. (Reference Hernández-Paniagua, Valdez, Almanza, Rivera-Cárdenas, Grutter, Stremme, García-Reynoso and Ruiz-Suárez2021), ranging between 10 and 23% during phase 2 (20 March–21 April) and 43% during phase 3 (21 April–31 May) and attributed to the significant reduction in motor vehicle emissions.
From July, the Δ14C values follow a decreasing trend, suggesting an increase in fossil CO2 emissions, also in agreement with the trend in fossil fuels consumption (Figure 3) and the gradual activation of non-essential activities. Furthermore, there is an increase in Δ14C for the sample collected during January–February 2021, when the epidemic risk level returned to extremely high (red), with a reduction in fossil fuels consumption of 30% as compared to the volume sold during the same months in 2019 (Figure 3). The low number of fires detected around the MCMA during January 2021 (Figure 4) confirm that the increase in Δ14C is not related to the emissions of 14C-enriched CO2 released by forest and agricultural fires; but seems to be a consequence of the reduction in the fossil CO2 emissions from the transport sector associated to the restrictions to the non-essential activities. Samples collected between March and June 2021 have Δ14C values similar to the values found for samples collected during the same months in 2019, suggesting the fossil fuels consumption is still lower than before the COVID-19 pandemic, in good agreement with fossil fuels consumption (Figure 3). On the other hand, samples collected between July and December 2021 have lower Δ14C values than samples collected during the same months in 2019; this should not be interpreted as fossil CO2 emissions returning to pre-COVID-19 levels, as during these months the fossil fuels consumption was still lower than in 2019 (Figure 3). Although the NWR data do not cover this period, this decreasing trend in Δ14C values may be partly explained by the decreasing trend of Δ14C concentration in the background atmosphere registered at monitoring stations such as Niwot Ridge, Colorado (Lehman at al. Reference Lehman, Miller, Wolak, Southon, Tans, Montzka, Sweeney, Andrews, LaFranchi, Guilderson and Turnbull2013) or Jungfraujoch and other sites from the Heidelberg global network (Levin et al. Reference Levin, Hammer, Kromer, Preunkert, Weller and Worthy2022), resulting from the fossil CO2 emissions at a global scale.
CONCLUSIONS
We present a record of Δ14C values for integrated samples collected in the MCMA during the period January 2019–December 2021. Values found during January 2019–February 2020, before the COVID-19 pandemic, reflect the complexity of emission sources in the area, with fossil fuels combustion as the main CO2 source, but with other emission sources with high 14C concentration, such as fires during the dry season and heterotrophic respiration during the raining season, resulting in values with significant variations. Despite this complexity, it was possible to identify a change in fossil CO2 emissions resulting from the COVID-19 lockdown and the restrictions imposed to control transmission of the disease, mainly reflected in a reduction of vehicle traffic, and thus in the consumption of fossil fuels. This is reflected by the variations in Δ14C values obtained for samples collected after March 2020, clearly following the chronology of the restrictions imposed to control the spread of the COVID-19 epidemic. These restrictions, which significantly impacted the vehicle traffic, resulted in Δ14C values of the same order as the preliminary data for the background atmosphere at Niwot Ridge, confirming the transport sector as the main source of fossil CO2 and supporting the consideration that other non-fossil CO2 sources, such as biomass burning and respiration, do contribute to the complexity of emissions in the MCMA.
It is relevant to continue the 14CO2 monitoring programs and work towards a better understanding of the 14C dynamics in the MCMA, which can help to evaluate changes in emission sources and the impact of environmental programs to mitigate the pollution in the area and cut the greenhouse emissions.
ACKNOWLEDGMENTS
This research was funded by DGAPA–UNAM (project PAPIIT-IN109921). Financial support from CONACyT (Consejo Nacional de Ciencia y Tecnología – México) to the Laboratorio Nacional de Geoquímica y Mineralogía is gratefully acknowledged. We are grateful to Scott J. Lehman (INSTAAR, University of Colorado at Boulder) and John B. Miller (NOAA ESRL Global Monitoring Laboratory) who kindly provided NWR data and made constructive suggestions. Finally, comments from two anonymous reviewers helped to significantly improve this manuscript.
SUPPLEMENTARY MATERIAL
To view supplementary material for this article, please visit https://doi.org/10.1017/RDC.2023.76
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