Indoor and Outdoor Nanoparticle Concentrations in an Urban Background Area in Northern Sweden: The NanoOfﬁce Study

: In recent years, nanoparticles (NPs) have received much attention due to their very small size, high penetration capacity, and high toxicity. In urban environments, combustion-formed nanoparticles (CFNPs) dominate in particle number concentrations (PNCs), and exposure to those particles constitutes a risk to human health. Even though ﬁne particles (<2.5 µ m) are regularly monitored, information on NP concentrations, both indoors and outdoors, is still limited. In the NanoOfﬁce study, concentrations of nanoparticles (10–300 nm) were measured both indoors and outdoors with a 5-min time resolution at twelve ofﬁce buildings in Umeå. Measurements were taken during a one-week period in the heating season and a one-week period in the non-heating season. The measuring equipment SMPS 3938 was used for indoor measurements, and DISCmini was used for outdoor measurements. The NP concentrations were highest in ofﬁces close to a bus terminal and lowest in ofﬁces near a park. In addition, a temporal effect appeared, usually with higher concentrations of nanoparticles found during daytime in the urban background area, whereas considerably lower nanoparticle concentrations were often present during nighttime. Inﬁltration of nanoparticles from the outdoor air into the indoor air was also common. However, the indoor/outdoor ratios (I/O ratios) of NPs showed large variations between buildings, seasons, and time periods, with I/O ratios in the range of 0.06 to 0.59. The reasons for high indoor inﬁltration rates could be NP emissions from adjacent outdoor sources. We could also see particle growth since the indoor NPs were, on average, almost twice as large as the NPs measured outdoors. Despite relatively low concentrations of NPs in the urban background air during nighttime, they could rise to very high daytime concentrations due to local sources, and those particles also inﬁltrated the indoor air.


Introduction
Nanoparticles have recently received much attention due to their very small size and high penetration rate [1]. The nanoparticle itself is a submicroscopic particle that measures less than 100 nanometers (nm) on at least one of its dimensions [2]. However, the term is sometimes also used for larger particles up to 500 nm [3,4]. Some nanoparticles are known as ultrafine particles (UFPs), which are defined by their aerodynamic size of <100 nm in all particle dimensions. Particles up to 300 nm are especially important since they are capable of diffusing rapidly in human airway mucus through the mucus pores [5,6]. Due to their small size and relatively large area in relation to volume, nanoparticles are believed to exert higher toxicity than larger particles [7].
Currently, there is no monitoring required or limit values set for nanoparticles or UFPs in ambient air. According to EURO 6, the only emission standard in terms of number of particles in vehicle exhaust is 6 × 10 11 particles per travelled km, and the need to tighten this standard has been discussed [8]. and asthma symptoms have also been analyzed in four panel studies with asthma patients in Finland and Germany. A decrease in peak expiratory flow and an increase in daily symptoms and medication use were found for elevated daily nanoparticle concentrations and for elevated daily concentrations in PM 2.5 . In three out of these four panel studies, the associations were strongest for the nanoparticles [36].
Despite the potentially detrimental health effects caused by nanoparticles, the number of exposure assessments is still quite limited, especially for indoor environments. By analyzing the nanoparticle concentrations and characteristics indoors and the nanoparticle concentrations and characteristics in close connection outdoors, it is possible to get a better idea of which sources and which mechanisms control the indoor concentrations. The indoor/outdoor relationships (I/O relationships) of nanoparticle concentrations have been analyzed in a few studies. In general, the I/O ratios and correlation coefficients between indoor and outdoor concentrations have been shown to be high for nanoparticles [37][38][39]. Additionally, higher number concentrations of particles were measured in residences close to highways compared to the number concentrations measured in residences located farther away from highways [40], indicating the importance of nanoparticle infiltration.
The aim of this study was to measure the concentrations of nanoparticles in indoor and outdoor environments, to study the temporal and spatial variation in particle concentrations, to study the infiltration of ambient nanoparticles indoors, and to discuss indoor and outdoor sources of nanoparticles. In the NanoOffice study, we focused on office buildings, which constitute the workspace for a large occupational group in the European Union [41,42]. The wider scope of the NanoOffice study was to identify nanoparticle levels in offices and relate them to ambient air quality, technical characteristics of the buildings, and employees' perception of indoor air quality in northern Sweden.

Materials and Methods
The number concentration and size distribution of nanoparticles were measured during two one-week periods in the city of Umeå in northern Sweden. The measurement locations consisted of one outdoor location and 12 indoor locations in a total of 10 office buildings ( Figure 1). These two one-week periods consisted of one week of measurements during the heating season and one week of measurements during the non-heating season. During these measurement periods, the windows were closed, and no employees were in the rooms where the measurements were performed due to noise annoyance caused by the measurement device. The office buildings were selected to include new, retrofitted and old buildings with various ventilation systems and different energy consumption. The office buildings were also chosen according to different distances from a busy street as the main sources of CFNPs. The busy street was defined as Petrus Laestadius street with a daily traffic flow of more than 700 buses, 100 trucks, and 2500 passenger cars [43].
At the same time as measurements were performed indoors in the selected office buildings, ambient air quality was monitored at a separate measurement point in the nearby outdoor environment. The study area with the locations of buildings and the outdoor measurement point is presented in Figure 1. Technical characteristics of the buildings are presented in Table 1.
The measurements were performed using the SMPS 3938 indoors and DISCmini outdoors. The SMPS 3938 (SMPS = Scanning Mobility Particle Sizer Spectrometer, TSI Inc., Shoreview, MN, USA) measures the size distribution of sub-micrometer particles. It combines electrical mobility sizing with single-particle counting to deliver nanoparticle concentrations in separate size channels. It consists primarily of an impactor to remove large particles (outside the size range of interest), a charger to neutralize the charges on particles, a controller to control flows and high-voltage, and a differential mobility analyzer (DMA) that separates particles based on their electrical mobility, as well as a condensation particle counter (CPC) placed downstream of the classifier that counts particles as they exit the DMA. The SMPS equipment is considered the "gold standard" for characterizing At the same time as measurements were performed indoors in the selected office buildings, ambient air quality was monitored at a separate measurement point in the nearby outdoor environment. The study area with the locations of buildings and the outdoor measurement point is presented in Figure 1. Technical characteristics of the buildings are presented in Table 1.  850  2  2002  118  MVHR  F7  790  3  1992  139  MVHR  F7  700  4  1968  106  MVHR  F7  500  5, 6, 7 2  1978  154  MVHR  F7  860, 920, 970  8  1966  121  MVHR  F7  570  9  1963  286  MVHR  F7  680  10  1960  270  MVHR  M6  250  11 3  1935  160  MVHR  F7 and F9  130  12 1969 206 MVHR F7 550 1 Building 1 is security classified, and no detailed technical data are available (NA = not available). 2 Buildings 5, 6, and 7 refer to measurement points located in different parts of the same building where measurements were performed in different parts of the building. 3 Completely renovated in 2014.
The SMPS was placed in offices near employees' regular workspaces ( Figure 2). It was equipped with advanced aerosol neutralizer 3088 (TSI Inc.), DMA 3081 (TSI Inc.), and CPC 3788 (TSI Inc.). Altogether, 95 different size fractions were measured in the range between 10 and 300 nm. The sampling interval was 5 min. nanoparticles, and it has been widely used in studies in exposure assessments focusing on inhalation toxicology and industrial hygiene [44].
The SMPS was placed in offices near employees' regular workspaces ( Figure 2). It was equipped with advanced aerosol neutralizer 3088 (TSI Inc.), DMA 3081 (TSI Inc.), and CPC 3788 (TSI Inc.). Altogether, 95 different size fractions were measured in the range between 10 and 300 nm. The sampling interval was 5 min. The DISCmini (Testo SE & Co KGaA, Titisee-Neustadt, Germany) is a handheld nanoparticle counter used to measure number concentration and average diameter of nanoparticles. The measuring principle of the DISCmini is based on electrical charging of the particles. Positive air ions generated in a corona discharge are mixed with the aerosol. The charged particles are then detected in two stages by electrometers. The first detector stage utilizes a pile of steel grids; small particles will preferentially deposit on it by diffusion and are detected as an electrical current. The remaining particles end up in a second stage, the filter stage, and are also detected as an electrical current. The ratio of these two currents is a measure of the average particle size determined during the instrument calibration [45]. In the current study, the device was equipped with a heated probe ( Figure 3). The probe was provided by ExIS AB, and it has been used by Grimm Inc. on the EDM 164 family of instruments. To measure the aerosol correctly at relative humidity levels above around 50%, it must be 'dried'. A simpler solution is to use heated inlet solution, as has been suggested by ExIS AB, the distributor of DISCmini and Grimm instruments in Sweden [46]. The DISCmini (Testo SE & Co KGaA, Titisee-Neustadt, Germany) is a handheld nanoparticle counter used to measure number concentration and average diameter of nanoparticles. The measuring principle of the DISCmini is based on electrical charging of the particles. Positive air ions generated in a corona discharge are mixed with the aerosol. The charged particles are then detected in two stages by electrometers. The first detector stage utilizes a pile of steel grids; small particles will preferentially deposit on it by diffusion and are detected as an electrical current. The remaining particles end up in a second stage, the filter stage, and are also detected as an electrical current. The ratio of these two currents is a measure of the average particle size determined during the instrument calibration [45]. In the current study, the device was equipped with a heated probe ( Figure 3). The probe was provided by ExIS AB, and it has been used by Grimm Inc. on the EDM 164 family of instruments. To measure the aerosol correctly at relative humidity levels above around 50%, it must be 'dried'. A simpler solution is to use heated inlet solution, as has been suggested by ExIS AB, the distributor of DISCmini and Grimm instruments in Sweden [46]. The heated inlet is approximately 0.5 m in length. It comprises a sampling head (35 mm), a heated pipe and connectors for the sample outlet and power. The stainless steel pipe in the heated pipe is polished, and since it is a straight pipe (from inlet head to instrument), the particle losses were expected to be low. The pipe is also electrically conductive, which avoids triboelectric effects. Heating of the pipe reduces thermophoretic losses (the heater cable increases a temperature of around 20 °C) [46].
The DISCmini has been used in several previous studies for measuring UFPs outdoors. For example, it was used in a study conducted in the city of Utrecht in the Netherlands in which UFPs were measured in front of fast-food restaurants in a largely pedestrian area in the city center [47]. The DISCmini equipment was also used in a study conducted in Montreal, Canada, in which spatiotemporal variations in outdoor UFP number concentrations and mean particle diameters were measured [48].
As two different devices were used, the measured size fractions of the SMPS were set to be similar to those of the DISCmini (10-300 nm). The correspondence between these two devices was tested by analyzing the correlation between the measurement results from the SMPS and DISCmini during parallel measurements in stationary conditions with real-life measurements indoors in Building 10 before the measurement campaigns. During the parallel measurements, the Pearson correlation coefficient was very high (R = 0.98), which is consistent with the results in previous studies by Meier et al. [49] and Ferrero et al. [50].
In the data analysis, the diurnal cycles and the temporal and spatial trends of the nanoparticle concentrations were analyzed. The correlation analysis was made with IBM SPSS statistics v26 [51]. The heated inlet is approximately 0.5 m in length. It comprises a sampling head (35 mm), a heated pipe and connectors for the sample outlet and power. The stainless steel pipe in the heated pipe is polished, and since it is a straight pipe (from inlet head to instrument), the particle losses were expected to be low. The pipe is also electrically conductive, which avoids triboelectric effects. Heating of the pipe reduces thermophoretic losses (the heater cable increases a temperature of around 20 • C) [46].
The DISCmini has been used in several previous studies for measuring UFPs outdoors. For example, it was used in a study conducted in the city of Utrecht in the Netherlands in which UFPs were measured in front of fast-food restaurants in a largely pedestrian area in the city center [47]. The DISCmini equipment was also used in a study conducted in Montreal, Canada, in which spatiotemporal variations in outdoor UFP number concentrations and mean particle diameters were measured [48].
As two different devices were used, the measured size fractions of the SMPS were set to be similar to those of the DISCmini (10-300 nm). The correspondence between these two devices was tested by analyzing the correlation between the measurement results from the SMPS and DISCmini during parallel measurements in stationary conditions with real-life measurements indoors in Building 10 before the measurement campaigns. During the parallel measurements, the Pearson correlation coefficient was very high (R = 0.98), which is consistent with the results in previous studies by Meier et al. [49] and Ferrero et al. [50].
In the data analysis, the diurnal cycles and the temporal and spatial trends of the nanoparticle concentrations were analyzed. The correlation analysis was made with IBM SPSS statistics v26 [51]. Table 2  in comparison with the outdoor concentrations measured at the same time. During the heating season, the average size of the nanoparticles indoors (arithmetic mean) was larger in comparison with the outdoor size in 11 out of the 12 cases; and during the non-heating season, the average size of the nanoparticles indoors was larger in comparison with the average size measured outdoors in all 12 cases. The correlation coefficients between indoor and outdoor concentrations showed large variations from 0.89 to −0.15, but with generally low values (Table 2). Many different sources contributed to the nanoparticles measured indoors and outdoors. CFNPs originating from vehicle exhaust are an important outdoor source that can infiltrate the indoor air, but there are also a number of indoor sources that generate nanoparticles, such as cooking, smoking, burning candles, and using electrical appliances [52]. In Table 3 the maximum and minimum nanoparticle concentrations are presented for the one-week measurement periods in Buildings 1-12 during the heating and the non-heating seasons. The maximum and minimum nanoparticle concentrations measured outdoors during the corresponding one-week periods are also presented. Table 2 shows that the average nanoparticle concentrations measured outdoors during the heating season were in most cases higher in comparison with the average nanoparticle concentrations measured during the non-heating season. The mixing layer can greatly affect the differences in nanoparticle concentrations during the different seasons and during the different weeks. Meteorological data during the measurement periods are presented in Appendix A, Table A1. As Umeå is situated in northern Sweden, periods of low temperature (min −21.9 • C during the measurement period) and low wind speed (min 1.7 m/s during the measurement period) occurred.

Measurement Results
During these two one-week measurement periods, there were large daily variations in nanoparticle concentrations. For example, Figure 4 presents the 5-min average nanoparticle number concentrations measured in Building 11, where relatively high indoor concentrations were found during one week in the heating season and during one week in the non-heating season. Building 11 is located close to a bus terminal where the impact of nanoparticles from the outdoor air is high. During these two one-week periods, the concentrations fluctuated sharply both outdoors and indoors. In general, the concentrations were higher on weekdays during the daytime; however, in several cases, high concentrations also appeared in the late evenings. Thus, it is difficult to determine any clear temporal trend. concentrations fluctuated sharply both outdoors and indoors. In general, the concentrations were higher on weekdays during the daytime; however, in several cases, high concentrations also appeared in the late evenings. Thus, it is difficult to determine any clear temporal trend. In Figure 5, the number concentration of particles in different size classes are presented for three office buildings during the heating and the non-heating seasons (see Buildings 7,8,and 11 in Tables 2 and 3). Building 7 represents an older office building, 970 m from a busy street. In Building 7, the highest nanoparticle concentrations during both the heating and the non-heating seasons are shown at a size of about 50 nm. Building 8 represents an older office building, 570 m from a busy street. In Building 8, the highest nanoparticle concentrations during both the heating and the non-heating seasons are shown at the size of about 65 nm. Building 11 represents an older office building, 130 m from a busy street and 170 m from a bus terminal. The particle concentrations during the heating season were very high, especially for particles in the size range of 12-15 nm. However, during the non-heating season, the particle concentrations in the different size fractions in Building 11 were quite similar to those in the other buildings. In Figure 5, the number concentration of particles in different size classes are presented for three office buildings during the heating and the non-heating seasons (see Buildings 7,8,and 11 in Tables 2 and 3). Building 7 represents an older office building, 970 m from a busy street. In Building 7, the highest nanoparticle concentrations during both the heating and the non-heating seasons are shown at a size of about 50 nm. Building 8 represents an older office building, 570 m from a busy street. In Building 8, the highest nanoparticle concentrations during both the heating and the non-heating seasons are shown at the size of about 65 nm. Building 11 represents an older office building, 130 m from a busy street and 170 m from a bus terminal. The particle concentrations during the heating season were very high, especially for particles in the size range of 12-15 nm. However, during the non-heating season, the particle concentrations in the different size fractions in Building 11 were quite similar to those in the other buildings.

Outdoor Nanoparticles and Their Infiltration Indoors
Indoor nanoparticle concentrations are driven by both indoor and outdoor sources. The indoor sources, such as indoor combustion, office equipment, etc., emit particles directly into the indoor air, whereas outdoor particles are deposited indoors mainly through infiltration or ventilation. In the current study, the average indoor concentrations were lower in comparison with the outdoor concentrations in all cases. During the outdoor peak concentrations, the indoor concentrations were usually also higher, indicating that outdoor infiltration affects the indoor concentrations of nanoparticles. In one of the studied buildings close to a bus terminal (Building 11), the indoor concentrations measured on weekdays during daytime turned out to be higher in comparison with the indoor concentrations measured during nighttime and on weekends, again indicating emissions of CFNP. The Pearson correlation coefficients between indoor and outdoor concentrations ( Table 2) show large variations, but seven R-values in the range of 0.41-0.89 indicate that infiltration occurs. The large variations in the correlation coefficients can be caused by meteorological factors in terms of wind speed and the mixing layer. However, there were also several periods with relatively high indoor concentrations in connection with relatively low outdoor concentrations, which indicates that the indoor sources are also of crucial importance for the nanoparticles measured indoors.
The importance of outdoor air in terms of indoor air quality has been shown in several earlier studies focusing on the I/O relationships of particles in school buildings in different areas. In a study from Brazil, particles in the size range of 10-420 nm were analyzed at rural and urban preschools in 2016−2017. The average I/O ratios of nanoparticle concentrations during the study period were 0.91 and 0.51 at the rural and the urban preschools, respectively. The I/O concentration ratios were also higher during morning and afternoon rush hours, indicating the importance of the contribution of vehicle exhaust from the outdoor air as a source of nanoparticles indoors [39]. In our study, the lower I/O ratios could be explained by longer distances from busy streets and/or relatively high outdoor concentrations. The impact of traffic on indoor air quality has also been shown in four preschools in Bogota, Colombia, where the concentrations of PM 10 , PM 2.5 , and black carbon were higher in those schools located alongside major urban roads [53]. Based on measurements of UFPs in 39 naturally ventilated primary schools in Barcelona, Spain, traffic emissions were estimated to be an important source of nanoparticles both indoors and outdoors [37]. In Umeå, residential wood combustion also has an important role in affecting ambient air quality [54]; however, houses near the measuring sites have district heating connected to a boiler house situated outside the city.
The indoor-outdoor relationships of particles have also been examined in residential houses. In a study from Australia, the indoor-outdoor relationships for particles in different size classes were measured in 16 residential houses located in a suburban area of Brisbane. The I/O ratios of sub-micrometer particles were in the range of 0.78 to 1.07, leading to the overall conclusion that during normal ventilation conditions, the particle concentrations measured outdoors could be used to predict simultaneous particle concentrations indoors [55]. In homes in Oporto, Portugal, UFP concentrations were higher indoors than outdoors and were spatially varied, being highest in kitchens, lower in living rooms and lowest in bedrooms [56]. In a study from Somerville, Massachusetts, U.S., the PNC in the size range of 6-3000 nm was measured both indoors and outdoors at 18 homes located <1500 m from an Interstate Highway. It appeared that the indoor and outdoor PNCs of homes located <100 m from the highway were higher in comparison with homes located >1000 m away [40]. In addition, in the current study, nanoparticle concentrations in offices located <250 m from a busy street seemed to be higher compared to offices >500 m away. Furthermore, in the study by Fuller et al. [40], the I/O concentration ratios were generally high, with a median value of 0.95 pooled over all homes. In a regression model based on these indoor and outdoor PNCs, an increase in outdoor PNC was associated with an approximately equal increase indoors. A high correlation between I/O concentrations and high infiltration, especially during summer, has also been shown in Chinese cities [57]. In the current study, I/O ratios were significantly lower than in China.
Considering the results of this current study, no general conclusions regarding the I/O concentration ratios and indoor infiltration can be made, as there were high temporal variations and large differences between the buildings.
To sum up, the nanoparticle concentrations indoors are influenced by the concentrations outdoors; nevertheless, the association seems to be complex and difficult to trace. In this study, the nanoparticle concentrations measured indoors were generally high in connection with outdoor peak concentrations. However, there were also some periods with relatively high indoor concentrations in connection with relatively low outdoor concentrations (Figure 4), which indicates that indoor sources are also a contributing factor, especially in Building 1.

Indoor Sources
Although CFNPs originating from traffic are an important source of nanoparticles that infiltrate indoors, as we can see in the current study, there are also a number of indoor sources that generate nanoparticles, such as cooking, smoking, candle burning, and electrical appliances [52]. Reche et al. [37] have described specific cases in which the indoor concentrations exceeded the outdoor concentrations, which could possibly be caused by cooking activities and surface chemistry reactions mediated by ozone.
Building activities have also been shown to be a significant source of nanoparticles. In the current study, the highest concentrations of indoor nanoparticles were found in recently opened office buildings. Measurements of ultrafine particles during building activities such as crushing, demolition and recycling concrete indicated that the majority of the number of newly formed particles were in the size range of <100 nm [58]. Newly built or renovated buildings can also emit volatile organic compounds (VOCs) [59]. Subsequently, VOCs can react with the indoor ozone and produce nanoparticles [60]. The particle levels are high indoors, which indicates that indoor sources are also important.
Nanoparticles originating from biological materials are also well represented in the indoor environment [61]. There are many indoor sources of these so-called bioaerosols, including mold on building materials, occupants, pets, indoor plants, and organic waste. As the measuring devices currently used do not enable study of the chemical composition of nanoparticles, we cannot draw conclusions about the role of bioaerosols.
Earlier studies have indicated that office equipment can also generate nanoparticles. Laser printers are commonly used in offices, and many studies have shown that they can release particles and produce adverse effects on indoor air quality. A test with printers in a clean chamber indicated that the emitted particles were dominated by particles in nanoscale [62]. It has also been shown in a chamber study that the nanoparticles emitted from laser printers have a bimodal number size distribution: one smaller mode with particles <10 nm and one larger mode in the size range of 40-100 nm. Nanoparticles in these two size distributions were detected even when the laser printers were activated without toner or paper. This indicates that the fuser unit, which is the device that that fixes toner on the paper with heat, is the primary source of nanoparticles emitted from laser printers [63]. From a health perspective, the particles emitted from laser printers are considered to pose relatively lower health risks in comparison with other particles, i.e., CDNPs, commonly found in the ambient air [21]. All offices in the current study had laser printers; however, none of them were in the same room where the measurements took place.

Processes That Determine the Particle Properties Indoors and Outdoors
An overall pattern of the measurement results in this study was higher number concentrations of particles measured outdoors, while the particle sizes measured indoors were larger in comparison with the particles measured outdoors. Outdoor air infiltration is assumed to be an important source of the nanoparticles measured indoors [55]. The buildings with old ventilation systems located close to heavy traffic are especially affected by nanoparticles originating outdoors [64].
Particles originating from combustion processes mainly occur in two size classes: nanoparticles in the size range of 1-5 nm and soot particles in the size range of 10-100 nm [10]. These two size ranges represent two different modes, referred to as nucleation mode and Aitken mode. In terms of particle number concentration per volume unit, most of the measured particles in the current study are represented in the Aitken mode (from around 10 to 100 nm), while in terms of particle mass per volume unit, the particles >100 nm dominate (called accumulation mode), since they are significantly larger but significantly fewer in number. The nucleation process is a gas-to-particle conversion in which nanoparticles are formed from gaseous molecules (homogeneous nucleation) and then grow larger by condensation of other gaseous molecules (heterogeneous nucleation) and by coagulation with other nucleated particles [63].
The overall pattern of higher number concentrations of particles measured outdoors but larger particle sizes measured indoors can largely be explained by the condensation and the coagulation processes: i.e., the particles are emitted mainly from the traffic outdoors, and as they penetrate into the buildings, condensation and coagulation of nucleated particles increase the average size while the number concentration decreases. This could also explain the relatively low correlation coefficients between the number concentrations indoors and outdoors. When comparing the concentrations of nanoparticles in different size fractions ( Figure 5), it appears, especially during the heating season, that the concentration of particles in the size range of 10-20 nm (Aitken mode) was particularly high in the office building close to a bus terminal. It is also shown in Figure 5 that there were relatively larger proportions of particles in the larger size classes in the buildings further away from the bus terminal.
In the current study, we could see differences in particle concentrations during the heating and the non-heating seasons, with higher average concentrations both indoors and outdoors during the heating season. This could be explained by several different factors. Firstly, more intense traffic in combination with a more stable atmosphere with lower wind speeds can partly explain the higher average nanoparticle concentration in the heating season during wintertime [65]. Secondly, nanoparticle formation processes are also influenced by the temperature. Increased particle formation from nucleation of exhaust from combustion engines has been shown to occur during cold days [39]. An increase in particle number concentration associated with decreasing temperatures has also been shown based on measurements in a street canyon in Stockholm during the period of 2002-2004. The increase in particle concentration associated with decreasing temperature was most noticeable for particles smaller than 40 nm [66]. The higher concentration of larger fine particles in winter compared to summer was previously identified in the OFFICAIR study [67].
The results presented in Figure 5, which shows the size fractions of nanoparticles measured indoors, give some indications that the factors mentioned above at least partially control the nanoparticle concentrations. During the heating season, the smaller size fractions (10-30 nm) of the indoor measurements in Building 11 ( Figure 5) show a relatively large number of particles in comparison with the indoor measurements in Building 7 and Building 8. Building 11 is located 130 m from a busy street and 170 m from a bus terminal. As shown in Table A1, the average temperature was relatively low during the measurement period for Building 11, but the wind speed during this week (1.7 m/s) was the lowest of all 24 weeks in which the measurements were performed. This might partly explain the relatively high concentrations of small particles (10-30 nm) measured indoors. The effect of low wind speeds and very low mixing layer heights on UFP dispersion has been discussed by Giemsa et al. [68].
In addition to the mechanisms described above, which mainly contribute to the nanoparticle concentrations during the heating season, there are also mechanisms that are most prominent during the non-heating season that benefit the formation of nanoparticles. Photochemically induced nucleation with the influence of sunlight is another formation mechanism that can contribute as much as local traffic to particle number concentration [69] and is most prominent during the summer [58]. However, Umeå is located at 63 degrees north latitude, and photochemically induced nucleation is probably significantly less prominent there in comparison with cities located closer to the equator.
Moreover, there are certain processes in addition to emissions that have a major impact on the PNC measured at different locations at different times within a city. Particle dynamics are particularly important to consider as they largely affect particles smaller than 20 nm [70]. Model calculations of PNC in Stockholm by Gidhagen et al. [71] show episodic losses of nanoparticles due to coagulation and dry deposition. Similar results based on calculations of PNC have been found in Oslo, Helsinki and Rotterdam by Karl et al. [72].

Strengths and Limitations of This Study
A main strength of this study is that it utilizes extensive datasets with continuous measurements of nanoparticles both indoors and outdoors at twelve different buildings that were chosen to represent different distances from busy streets. The measurements are also divided into two periods representing both the heating and the non-heating seasons, which is an advantage for understanding differences in the processes that create nanoparticles at different temperatures. Also, measurements lasted for a whole week-including working days and a weekend-and thus show fluctuations during different times and days of the week.
A limitation of this study is that the outdoor measurements were all performed at the same measurement point. In order to establish accurate relationships between indoor and outdoor concentrations, it would have been more beneficial to measure the outdoor concentrations in close proximity to each building. Unfortunately, this was not possible due to technical needs and restrictions from building owners. Thus, local outdoor sources of nanoparticles in close proximity to a building could not be detected from the outdoor measurement point. The highly variable and generally small correlation coefficients between the indoor and the outdoor concentrations (Table 2) can probably be at least partly explained by the lack of outdoor measurements in close proximity to the buildings where the indoor measurements were performed. Also, we used two different devices for measurements. Despite relatively good agreement between SMPS and DISCmini in some studies [49,50], several studies have also identified difference in number concentration when different devices were used [73,74].
Another limitation of this study is that only the number concentration of nanoparticles was measured. With this applied methodology, it is not possible to distinguish the sources and chemical composition of the measured nanoparticles. This is an important issue that needs to be addressed in future studies. By knowing the chemical composition, it is easier to trace the various sources of nanoparticles, especially indoors [75][76][77].
We included in this study particles in the size range of 10-300 nm in order to have a similar size fraction covered by two different devices. Nanoparticles are often defined as particles <100 nm in diameter in at least one dimension. However, from a health perspective, particles in the size range up to 300 nm are important since they are capable of diffusing rapidly in human airway mucus through the mucus pores [5,6]. Nevertheless, the majority of the particles that were measured in this study were in the size range of 10-100 nm.
Another limitation of this study is that the particles in the size range of <10 nm (sub-10 nm) were not measured. However, these particles are not easy to measure, and the health effects associated with exposure to those particles are not very well known [78]. Modern technologies and wider use of biofuels reduces the total mass concentration of particles in the exhaust, but might increase the number concentration of sub-10 nm particles [79]. Particles in the size range of 1.3-10 nm can also be generated from brake wear [80]. Indoor laser printers are another source of sub-10 nm particles, where the emitted particles have a bimodal number size distribution with one smaller mode with particles <10 nm [57]. To sum up, particles smaller than 10 nm can arise from several sources, and these particles are also important to consider regarding their potential health effects in further studies.

Regulatory Outlook
In the current study, relatively high concentrations of nanoparticles were found (up to half a million particles per cm 3 in outdoor air); however, there are no limit values for nanoparticles/UFPs in ambient air. The World Health Organization is now reviewing and updating its air quality guidelines with a special focus on UFPs in future documents. Nevertheless, in epidemiological studies, the evidence of health effects associated with exposure to UFPs has been inconclusive, especially for short-term effects [32]. Further evidence of long-term health effects associated with exposure to UFPs has recently been published [33].
In occupational environments, a few recommended time-weighted average exposure limits for specific UFPs-such as titanium dioxide, silver, and nanofibers-exist, but overall, there are currently no regulations for UFPs in general in occupational environments such as offices [81][82][83]. Further implementation of workplace exposure limits for nanoparticles in the range of 0-100 nm have been proposed [84]. Occupational exposure limits for nanomaterials and nanoparticles have been discussed in van Broekhuizen et al. [85], and a set of 'Nano reference values' has been proposed in the Netherlands [86]. In office environments, the emissions from laser printers has been limited with the BLUE Angel Certification, which has set an emission limit value of 3.5 × 10 11 particles during 10 min of printing in monochrome mode [87]. Despite this, as discussed earlier, high levels of nanoparticles are released by printers, which could produce adverse effects on indoor air quality [62].

Conclusions
The current study identified the highest nanoparticle concentrations in offices close to a bus terminal and the lowest in offices near a park, indicating the influence of trafficinduced, combustion-formed nanoparticles (CFNPs). Also, a temporal effect appeared, usually with higher concentrations of nanoparticles found during daytime in the urban background area, whereas considerably lower nanoparticle concentrations were often present during nighttime. Infiltration of nanoparticles from the outdoor air into the indoor air was also common, as the nanoparticle concentrations measured indoors were generally high in connection with outdoor peak concentrations. However, overall conclusions are difficult to draw, since the I/O ratios showed large variations between buildings, seasons, and time periods. In general, the higher average nanoparticle concentrations during the heating season (both indoors and outdoors) could be explained by more intense traffic in combination with a more stable atmosphere with lower wind speeds, but also by increased particle formation from nucleation of exhaust during cold days.
Even though the indoor sources of nanoparticles have also been shown to be important, in the current study, high/low indoor particle concentrations usually appeared in connection with high/low outdoor concentrations. However, the highest concentrations of indoor nanoparticles were found in recently opened office buildings, which could be affected by new building conditions. As only the number concentrations of nanoparticles were measured in the current study, it was not possible to distinguish the sources and chemical composition of the measured nanoparticles. This is an important issue that needs to be addressed in future studies.