Risk Assessment and Air Quality Study during Different Phases of COVID-19 Lockdown in an Urban Area of Klang Valley, Malaysia

: Globally, the COVID-19 pandemic has had both positive and negative impacts on humans and the environment. In general, a positive impact can be seen on the environment, especially in regard to air quality. This positive impact on air quality around the world is a result of movement control orders (MCO) or lockdowns, which were carried out to reduce the cases of COVID-19 around the world. Nevertheless, data on the effects on air quality both during and post lockdown at local scales are still sparse. Here, we investigate changes in air quality during normal days, the MCOs (MCO 1, 2 and 3) and post MCOs, namely the Conditional Movement Control Order (CMCO) and the Recovery Movement Control Order (RMCO) in the Klang Valley region. In this study, we used the air sensor network AiRBOXSense that measures carbon monoxide (CO), nitrogen dioxide (NO 2 ), sulfur dioxide (SO 2 ) and particulate matter (PM 2.5 and PM 10 ) at Petaling Jaya South (PJS), Kelana Jaya (KJ) and Kota Damansara (KD). The results showed that the daily average concentrations of CO and NO 2 mostly decreased in the order of normal days > MCO (MCO 1, 2 and 3) > CMCO > RMCO. PM 10 , PM 2.5 , SO 2 and O 3 showed a decrease from the MCO to RMCO. PJS showed that air pollutant concentrations decreased from normal days to the lockdown phases. This clearly shows the effects of ‘work from home’ orders at all places in the PJS city. The greatest percentage reductions in air pollutants were observed during the change from normal days to MCO 1 (24% to 64%), while during MCO 1 to MCO 2, the concentrations were slightly increased during the changes of the lockdown phase, except for SO 2 and NO 2 over PJS. In KJ, most of the air pollutants decreased from MCO 1 to MCO 3 except for CO. However, the percentage reduction and increments of the gas pollutants were not consistent during the different phases of lockdown, and this effect was due to the sensor location— only 20 m from the main highway (vehicle emissions). The patterns of air pollutant concentrations over the KD site were similar to the PJS site; however, the percentage reduction and increases of PM 2.5 , O 3 , SO 2 and CO were not consistent. We believe that local burning was the main contribution to these unstable patterns during the lockdown period. The cause of these different changes in concentrations may be due to the relaxation phases during the lockdown at each station, where most of the common activities, such as commuting and industrial activities changed in frequency from the MCO, CMCO and RMCO. Wind direction also affected the concentrations, for example, during the CMCO and RMCO, most of the pollutants were blowing in from the Southeast region, which mostly consists of a city center and industrial areas. There was a weak correlation between air pollutants and the temperature and relative humidity at all stations. Health risk assessment analysis showed that non-carcinogenic risk health quotient (HQ) values for the pollutants at all stations were less than 1, suggesting unlikely non-carcinogenic effects, except for SO 2 (HQ > 1) in KJ. The air quality information showed that reductions in air pollutants can be achieved if trafﬁc and industry emissions are strictly controlled.


Introduction
The COVID-19 pandemic caused by the SARS-CoV-2 virus resulted in over 4.7 million deaths along with many losing their source of income and various other negative effects. Ambient air pollutants, such as carbon monoxide (CO), sulfur dioxide (SO 2 ), nitrogen dioxide (NO 2 ), ozone and particulate matter (PM 10 and PM 2.5 ), are common air pollutants measured by many countries as they represent the status of ambient air quality. Poor air quality can result in various human health issues, such as respiratory problems and carcinogenic effects [1][2][3][4].
However, despite the many negative effects of the pandemic, there have also been positive effects, such as the impacts on the environment. In an attempt to control the spread of the virus, many countries worldwide, including Malaysia, enforced lockdowns, also known as Movement Control Orders (MCOs), which inadvertently caused some positive changes to the environment [5][6][7]. Many countries have recorded cleaner air quality readings as a result of these lockdowns [7][8][9][10].
Air quality measurements have been carried out by air quality monitoring networks and satellite observations to determine the extent to which air quality levels changed during the lockdowns implemented in most countries. For example, previous observations showed that these air pollutants were significantly decreased throughout whole continents and countries, such as the United States [11], Asia [12], Europe [13] and Australia [14]. In Malaysia, studies have been conducted and showed similar results [4,5,9,12,13]. The air quality measurements also differed in each study.
Observations by using satellite observations in Europe showed that the NO 2 tropospheric column concentrations showed a decrease of −20% to −38% [14]. A study using surface observations and machine learning to retrieve the NO 2 concentration data during lockdown showed that the lockdowns were responsible for a decrease of 50% NO 2 [15]. Observations using data from the European Commission Atmospheric Observatory of Ispra (regional background) and from the regional environmental protection agency (ARPA) air monitoring stations in Milan showed NO 2 concentrations decreased due to the lockdowns Sustainability 2021, 13, 12217 3 of 22 by −30% and −40% on average at the urban and regional levels, respectively [16]. The study also used forecast model data from the Copernicus Atmosphere Monitoring Service (CAMS), which indicated similar reductions of NO 2 concentrations as a consequence of the lockdowns of −30% and −40% on average at the urban and regional background sites, respectively [16].
In Malaysia, studies by [9,12] used observation data from reference monitoring stations owned by the Department of Environment Malaysia (DOE). However, the use of air quality sensor networks for the identification of a reduction in air pollutants is still absent. Observations using the low-cost air quality sensor (LAQS) network in Klang Valley showed a more than 50% reduction of PM 10 , PM 2.5 and CO during MCO 1 [5]. However, the PM 10 , PM 2.5 and CO air pollutant data were limited and only monitored during MCO 1. Thus, this study will continue the previous observations [5].
In the current study, the air pollutants measured were CO, NO 2 , SO 2 , O 3 , PM 10 and PM 2.5 over an urban area of the Klang Valley, during normal days and different phases of the lockdown period, using the LAQS. The meteorological and wind trajectory influences were evaluated using ERA5 data. Finally, this study will provide information on the health risks associated with these air pollutants and provide evidence-based knowledge for formulating achievable air quality management strategies for pollution control.

Low-Cost Air Quality Sensor Deployment
Details of the AiRBOXSense system have been published in a previous work [17]. The specific requirements of AiRBOXSense were reliability and durability while being low cost, portable and easy to install by the user. AiRBOXSense collects, analyses and shares air quality data using a wireless communication network [17]. Using the Internet of Things (IoT) allows data to be sent to remote cloud storage, such as Thingspeak, periodically as well as providing near-real-time visualization of numerical and graphical values over time. The electrochemical sensor (EC) for CO, NO 2 , SO 2 and O 3 and the optical particle sensor (OPC-N2) for PM measurements were manufactured by Alphasense (Alphasense Ltd., Great Notley, Braintree, UK).
The uncertainties (based on uncorrected and standard gas mixing ratios) of each of the sensors were ±2 ppb, ±2 ppb, ±1.5 ppb, ±2 ppb and ±3.2 ppb for CO, NO 2 , SO 2 , O 3 and PM (PM 2.5 and PM 10 ), respectively. Details of the AiRBOXSense calibration, configuration and operation were described in our previous work [17]. Three AiRBOXSense sensors were deployed at locations in Petaling Jaya South (PJS), Kelana Jaya (KJ) and Kota Damansara (KD) (see Figure 1).

MCO, CMCO and RMCO
In Malaysia, the Malaysian government ordered the first Movement Control Order (MCO) on 18 March 2020 as shown in Table 1. This was later extended and then relaxed to different phases known as the Conditional Movement Control Order (CMCO) and Re-

MCO, CMCO and RMCO
In Malaysia, the Malaysian government ordered the first Movement Control Order (MCO) on 18 March 2020 as shown in Table 1. This was later extended and then relaxed to different phases known as the Conditional Movement Control Order (CMCO) and Recovery Movement Control Order (RMCO). The MCO started on 18 March and continued to 3 May 2020; the CMCO started on 4 May, continuing until 9 June 2020; and the RMCO started on 10 June 2020, continuing until 31 March 2021. The MCO can be seen as an unplanned air quality experiment to study the effects on air quality of extraordinary reductions in anthropogenic activities. Furthermore, MCOs may help to identify an air quality baseline target to achieve in normal conditions. The main restriction imposed during MCO was the general prohibition of large gatherings and daily activities across the nation and the closure of all government and private premises except for essential services [4]. The MCO later transitioned to the CMCO, with slightly more relaxed restrictions that allowed the resumption of most economic sectors and interstate travel for work purposes only [18]. The RMCO was later introduced with more relaxed restrictions, considering the downward trend of daily COVID-19 cases at the time. The implementation of the RMCO saw the resumption of daily activities while abiding to social distancing protocols and interstate travel was allowed, except for areas under an Enhanced Movement Control Order (EMCO). An EMCO is implemented in specific locations with a high infection rate and, hence, consists of much more stringent restrictions whereby such areas are completely closed off for non-residents.

Meteorological Parameters
The temperature and relative humidity (RH) were measured using AiRBOXSense. The sensor probes for temperature and RH were AF5485 sensors (SEEED, China). Wind data was obtained from the European Centre for Medium-Range Weather Forecasts (ECMWF) via the toolbox on the Copernicus Climate Change Service website [19]. The wind speed was at 10 m at about ground level with a time resolution of one hour and a horizontal resolution of 1.5 • × 1.5 • . As the three stations are close together, they are all within the same 1.5 • grid area and, hence, have the same wind speeds and directions. Previous air pollutant concentration studies in Klang Valley, Malaysia have shown that the reduction in motor vehicles on the roads was the main cause of changes during the MCO compared to the influences from meteorological factors [5,9,12]. In addition, a study showed weak correlations between air pollutant concentrations and meteorological factors in the Klang Valley [20]. However, it is worth studying the correlations between meteorological factors and air pollutant concentrations during different phases of the MCO. In this study, we will consider the correlations of meteorological factors, such as the temperature and relative humidity, which will be discussed in Section 3.5.
The wind speed and direction showed different patterns during the different lockdown phases. Most of the winds were from the south-east (SE) during the lockdown over the Petaling Jaya areas as shown in Figure 2. The air pollutants were expected to originate from the Kuala Lumpur (KL) region, which is the capital of Malaysia, Seri Kembangan (SB) and Puchong. The pollutant concentrations were mostly affected by vehicular and industrial emissions.

Petaling Jaya South (PJS)
In this study, only normal day data was available for the PJS station. Table 2, Figure  3a-f how the average daily concentrations data and time series of measured air pollutants over the PJS area. These observations were similar to the previous study by [5] in the same region. The daily averages of PM10 and PM2.5 during normal days were 21.68 μgm −3 and 10.4 μgm −3 , respectively. The highest maximum concentration was recorded for CO with a maximum value of 1191.08 ppb.
Meanwhile, the O3, NO2 and SO2 daily averages were 53.51 ppb, 18.11 ppb and 78.70 ppb, respectively. However, PM2.5 and PM10 recorded decreases from MCO 1 to RMCO to MCO 2, while NO2 and O3 concentrations increased from MCO 1 to RMCO to MCO 2. All pollutant concentrations were still below the Malaysian Ambient Air Quality Standards (MAAQS) air quality guideline values except for NO2, which was high during RMCO with recorded a daily average of 53.7 ppb (MAAQS daily average is 42.5 ppb, as shown in Table  3).
During MCO 1, most of the pollutant concentrations showed significant reductions compared to the normal days as shown in Table 4. These observations were also shown by [9] and [21] to be due to the decreased number of vehicles and the temporary closure The KL area mainly experiences a combination of vehicular and industrial emissions, while SB and Puchong are mainly heavy industrial areas. During CMCO and RMCO, the winds were mostly from a southerly direction, from SB and Puchong areas. During MCO 2, the wind speed increased to 3.0 ms −1 but the wind directions were from the SE, which is similar to the MCO period. During the MCO 3, wind directions were from the Putrajaya area.

Petaling Jaya South (PJS)
In this study, only normal day data was available for the PJS station. Table 2, Figure 3a-f how the average daily concentrations data and time series of measured air pollutants over the PJS area. These observations were similar to the previous study by [5] in the same region. The daily averages of PM 10 and PM 2.5 during normal days were 21.68 µgm −3 and 10.4 µgm −3 , respectively. The highest maximum concentration was recorded for CO with a maximum value of 1191.08 ppb.  Table 3).  Table 5, Figures 4 and 5 show the average daily concentrations data and time series of measured air pollutants over the KJ area. The daily averages of PM10 and PM2.5 during normal days were 11.07 μgm −3 and 5.62 μgm −3 , respectively. The highest maximum concentration was recorded for CO with a maximum of 452.49 ppb. The daily average concentrations for O3, NO2 and SO2 were 49.13 ppb, 29.24 ppb and 43.28 ppb, respectively. Even so, all pollutant concentrations were still below the MAAQS values, except for SO2, During MCO 1, most of the pollutant concentrations showed significant reductions compared to the normal days as shown in Table 4. These observations were also shown by [9,21] to be due to the decreased number of vehicles and the temporary closure of industries during the MCO in Malaysia. During CMCO, air pollutant concentrations increased by 40.3%, 22.9%, 5.51%, 3.22%, 0.41% and 31.3% for PM 10 , PM 2.5 , SO 2 , NO 2 , O 3 and CO, respectively. These observations can be expected from the increased numbers of vehicles and industries operating during this period. Meanwhile, during RMCO, small increases were seen during this period (see Table 4). During RMCO, most activities were allowed by the government, which led to the increment of the pollutant concentrations.  Table 3).

Kelana Jaya
During MCO 1, most pollutant concentrations showed a decrease transitioning from the MCO to CMCO, as shown in Table 6. The concentrations decreased by 0.58%, 13.81%, 5.23% and 15.63% for PM 10 , PM 2.5 , SO 2 and O 3 , respectively, whereas an increase was observed for both NO 2 and CO at 0.79% and 65.74%, respectively. Such results show that there was an increase in traffic during the transition, which led to the NO 2 and CO increases from the MCO to CMCO in KJ, as these are the main pollutants of vehicular emissions from the Damansara-Puchong Highway (LDP) where the AiRBOXSense was located (~30 m from LDP).
At the same time, the reductions in PM 10 , PM 2.5 , SO 2 and O 3 show that businesses and residents in Kelana Jaya were still in the process of transitioning by adhering to the standard operating procedure (SOP) and remaining at their homes and premises. During the RMCO, a significant decrease was observed at 78.47%, 64.19%, 30.36% and 29.01% for PM 10 , PM 2.5 , SO 2 and NO 2 , respectively, whereas O 3 and CO showed an increase of 29.51% and 7.91%, respectively. Even though, during the RMCO, the numbers of vehicles and operational industries were expected to increase, the majority of industries were still implementing a work from home (WFH) policy for their staff. The observed decreases in PM 10 , PM 2.5 , SO 2 and NO 2 during the RMCO can be seen as an attempt by the local people to stay safe, even after the restrictions were relaxed by the government, consequently, contributing to the decreased activity and usage of vehicles.     Table 7 and Figure 6 show the average daily concentration data and time series of measured air pollutants over the KD area. The daily average PM10 and PM2.5 during normal days were 21.68 μgm −3 and 10.4 μgm −3 , respectively. The highest maximum concentration was recorded for CO with a maximum of 1191.08 ppb. The O3, NO2 and SO2 daily  Table 7 and Figure 6 show the average daily concentration data and time series of measured air pollutants over the KD area. The daily average PM 10 and PM 2.5 during normal days were 21.68 µgm −3 and 10.4 µgm −3 , respectively. The highest maximum concentration was recorded for CO with a maximum of 1191.08 ppb. The O 3 , NO 2 and SO 2 daily averages were 53.51 ppb, 18.11 ppb and 42.37 ppb, respectively. Nevertheless, all pollutant concentrations were still below MAAQS values, except for SO 2 and NO 2 , which were high during RMCO with daily averages of 48.49 ppb and 53.69 ppb, respectively (MAAQS daily averages were 30.5 ppb and 42.5 ppb for SO 2 and NO 2 , respectively, as shown in Table 3). During MCO 1, all pollutant concentrations for the MCO, CMCO and RMCO were significantly lower in comparison to the readings from a normal day as shown in Table 7. Similar observations were also reported in [9,12]

Air Pollutant Correlations
In this section, the Spearman correlation test was chosen to investigate the correlations between each pollutant at all stations from the MCO to MCO 3 periods as shown in Table 9. Strong correlations between PM2.5 and PM10 were observed at all stations with r 2 of 0.9 (p < 0.01) suggesting that both were emitted from the same sources, mainly from vehicular and industrial emissions. Positive correlations (0.13 < r 2 < 0.48, p < 0.01) were obtained between NO2 and O3 at all stations. The relationship between O3 and NO2 has been investigated in many previous studies (e.g., [1] and [21]). Atmospheric O3 levels are determined by emissions of O3 precursors (such as volatile organic compounds (VOCs), NO2 and CO), atmospheric nitrogen oxide (NOx) photochemistry and transport [22,23]. These observations could be expected from the increased numbers of vehicles and increased industrial activity during this period in the KD area. On the other hand, during RMCO, significant increases were observed for most pollutants, with increases of 23.5%, 54.09%, 72.22% and 78.60% for PM 10 , SO 2 , NO 2 and CO, respectively, while small decreases of 12.46% and 0.99% were recorded for PM 2.5 and O 3 , respectively. During RMCO, the relaxed restrictions and increase in activities allowed by the government led to the increase in most of the pollutants. Finally, Figure 5 show overall average concentrations of all measured pollutants during different phases of lockdown at all sensor locations in the Klang Valley.

Statistical Analysis Air Pollutant Correlations
In this section, the Spearman correlation test was chosen to investigate the correlations between each pollutant at all stations from the MCO to MCO 3 periods as shown in Table 9. Strong correlations between PM 2.5 and PM 10 were observed at all stations with r 2 of 0.9 (p < 0.01) suggesting that both were emitted from the same sources, mainly from vehicular and industrial emissions. Positive correlations (0.13 < r 2 < 0.48, p < 0.01) were obtained between NO 2 and O 3 at all stations. The relationship between O 3 and NO 2 has been investigated in many previous studies (e.g., [1,21]). Atmospheric O 3 levels are determined by emissions of O 3 precursors (such as volatile organic compounds (VOCs), NO 2 and CO), atmospheric nitrogen oxide (NO x ) photochemistry and transport [22,23]. Positive correlations between CO and NO 2 at PJ, KJ and KD were observed with r 2 (p < 0.01) values of 0.23, 0.42 and 0.41, respectively. The positive correlation may be supported by the reaction of CO entering the cycle of oxidation and nitrogen monoxide (NO) being oxidized to NO 2 [24]. Table 10 shows the statistical Spearman analysis between air pollutants and meteorological factors (temperature and RH) at all stations. Of these meteorological factors, only KJ had positive correlations between SO 2 and temperature and RH with r 2 values 0.67 and 0.54, respectively. All air pollutants had weak correlations with temperature and RH at most of the stations, suggesting that the contributions of vehicular and industrial sources were not influenced by the temperature and RH. This finding is similar to that found by [25] over an urban area of Chengdu, China. They suggested that it may be related to the different physical characteristics, sources, wind speed, wind direction and compositions of the air pollutants. Table 10. Pearson's correlation coefficients (r 2 ) for air pollutants and meteorological factors (temperature and RH) at all stations.

Air Pollutants
Temp ( • C) Relative Humidity (%)  The non-carcinogenic risks due to exposure to NO 2 , SO 2 , CO, O 3 , PM 10 and PM 2.5 via the inhalation route at all three locations are shown in Tables 11-13. All exposure factor parameters for health risk assessment calculated in this study is stated in Table 14.
Inhalation was considered as the major route for exposure to the air contaminants. The calculated health quotients (HQ) for NO 2 , PM 10 and PM 2.5 across the exposed groups at all locations and different MCOs were less than 1 (HQ < 1). These findings indicated that the concentration levels for NO 2 , O 3 , PM 10 and PM 2.5 observed for KD, KJ and PJ during the period were unlikely to cause non-carcinogenic effects. However, the HQ of exposure to SO 2 in KJ during MCO, CMCO and RMCO among infants (0-1 years) and children (2-5 years) was greater than 1 (HQ > 1).     This suggests that infants (0-1 years) and children (2-5 years) have higher potentials to suffer non-cancerous effects due to exposure to SO 2 . These findings showed that infants (0-1 years) and children (2-5 years) are the part of the population that may be at risk of developing health related issues due to SO 2 exposure. Health risks are especially high for children because of their low tolerance to toxins [26,27]. Children have been shown to be more sensitive to environmental pollution than adults. They are considered a risk group due to many reasons, including the relatively higher quantity of air they inhale. A resting infant's air intake per unit weight is double that of an adult, and his or her immune system and lungs are not fully developed.
KD, KJ and PJ presented the highest HQ values for CO through the inhalation pathway across the different MCOs and exposed populations. Thus, the exposed groups at all study locations faced great potential for incurring non-cancerous effects of CO. The high HQ values indicates that the exposure to the ambient CO cannot be disregarded, and it's the health implications need further thorough investigation. An investigation by Iqbal and co-workers [28] suggested that CO is often not recognized, and its toxicity is generally underestimated and misdiagnosed owing to its non-irritating character.

Carcinogenic Risk of PM 2.5
The cancer risk was only calculated for PM 2.5 due to the lack of availability of the inhalation unit risk (IUR) values for the other pollutants. Overall, the trend of cancer risk values was similar at all the study locations, across exposed groups and different types of movement control order. All sampling locations and exposed groups recorded a cancer risk (CR) value higher than the acceptable value at 1 × 10 −6 . This indicates that PM 2.5 is a contaminant that poses a risk to the exposed population at all study locations.
Thus, it is clear that exposure of populations to the fine particles should be of special concern. On top of that, this indicates that all the exposed population are at a higher risk of developing cancer in the near future owing to the inhalation of PM 2.5 . We found that the risk of developing cancer was higher among adults compared to children and infants. In this study, the exposure duration and averaging time were set equal to 30 years and 70 years respectively, for adults, whilst the corresponding values for infants and children were between 1-12 years and 70 years, respectively. As a result, the CR for children was lower due to the shorter exposure time. A similar outcome was documented in [28] as well as in [29].
In addition, the results also showed that the fine mode particles were likely to exhibit more potential health effects compared to coarse mode particles for all trace elements at all measurement sites. In this study, the proportions of fine particles have two important implications on the health effects of re-suspended dust episodes. First, fine particles can remain in suspension much longer than coarse particles and can, thus, can result in larger spatial impacts by the re-suspended PM. Secondly, the fine fraction of re-suspended particulate matter is more likely to comprise anthropogenic constituents that are potentially more toxic than the fine particles of purely crustal origin. This study agreed with the reviews by [30][31][32], which concluded that there tends to be a stronger relation between fine particles, PM 2.5 and most health effects than between PM 10 and effects on health.

Conclusions
This study showed that the levels of air quality during the different phases of lockdown were still within the guidelines set by the DOE. Differences in the number of vehicles and industrial activities played an important role in influencing the distribution of pollutant concentrations at each sensor location. The results showed that air pollutants over PJ increased from normal days > MCO > RMCO > MCO 1 > MCO 2. However, KJ recorded air pollutants decreasing during MCO to CMCO for PM 10 , PM 2.5 , SO 2 and O 3 , whilst, during CMCO to RMCO, there were slight decreases for PM 10 , PM 2.5 , SO 2 and NO 2 . In KD, a decrease of PM 2.5 during MCO to RMCO and decreases of PM 2.5 and O 3 during the CMCO to RMCO were observed.
Due to the relaxation of movement controls that were implemented by the government from CMCO to RMCO, there should have been increased air pollutant concentrations due to the increase in the number of vehicles and factories operating. However, most employers still practiced a WFH policy during this period of change. The emissions from vehicles and industrial emissions from KL and other nearby regions were expected to be the main sources of pollutants during these lockdown phases. The concentrations of air pollutants recorded at the three stations were not influenced by meteorological factors such as temperature and RH but were more likely influenced by wind direction and wind speed.
The health risk assessment analysis showed that the non-carcinogenic risks due to exposure to NO 2 , SO 2 , CO, O 3 , PM 10 and PM 2.5 via the inhalation route at all three locations were unlikely to pose non-carcinogenic effects, except for SO 2 in KJ (HQ > 1), which showed potential for encountering non-cancerous effects of exposure to SO 2 . Good air quality can be achieved if the number of vehicles on the roads and industrial emissions can be controlled. The use of continuous air quality sensors to measure real-time air pollutant concentrations in urban areas is a step that can be considered for the purpose of air quality control in the future.