Office buildings are among the most important types of commercial buildings. In 2012, offices represented 18% of floor space and 20% of energy consumption of commercial buildings in the US, and this building stock keeps growing (EIA 2012). It is a relatively uniform building type, characterised by high energy use due to artificial lighting, information and communication technology (ICT) equipment and air-conditioning (AC) (Pérez-Lombard et al. 2008). The increasing need for office floorspace is generally coupled with service sector growth (Deetman et al. 2020), observed in most important emerging economies (UN 2021). Consequently, this building type is responsible for a significant share of building-related greenhouse gas (GHG) emissions.
Life-cycle assessment (LCA) is a method used to assess the potential environmental impacts of a product from the extraction of raw materials through manufacturing and use to the eventual disposal of the product (ISO 2006). The method is widely applied to study the environmental performance of buildings, including the assessment of GHG emissions over the life-cycle stages, also known as the carbon footprint (Pandey et al. 2011). Numerous studies have been conducted on life-cycle energy use (Cole & Kernan 1996; Dimoudi & Tompa 2008; Junnila et al. 2006; Kofoworola & Gheewala 2009; Wang et al. 2018; Yohanis & Norton 2002) and GHG emissions (Airaksinen & Matilainen 2011; Asdrubali et al. 2013; Chau et al. 2012; Dimoudi & Tompa 2008; Eberhardt et al. 2019; Frischknecht et al. 2019; Junnila et al. 2006; Kofoworola & Gheewala 2008; Kumanayake et al. 2018; Lessard et al. 2018; Suzuki & Oka 1998; Wallhagen et al. 2011; Yan et al. 2010; Ylmén et al. 2019) of office buildings, with some focused on material-related impacts (Chau et al. 2012; Dimoudi & Tompa 2008; Eberhardt et al. 2019; Yan et al. 2010). The available estimates of life-cycle emissions of office buildings vary significantly, as shown in Table S1 in the supplemental data online.
Previous research shows that operational energy use and production of materials are the two most important life-cycle stages for energy consumption (Cabeza et al. 2014; Chau et al. 2015; Karimpour et al. 2014; Ramesh et al. 2010; Sartori & Hestnes 2007) and GHG emissions (Chau et al. 2015; Fenner et al. 2018; Seo & Hwang 2001) of buildings. Operational energy use in offices was found to be influenced by ventilation rate (Heiselberg et al. 2009), cooling set point (Lam & Hui 1996a), cooling efficiency (Lam & Hui 1996a), window-to-wall ratio (WWR) (Wong et al. 2019), shading (Carvalho et al. 2010) and solar heat gain coefficient (SHGC) (Carvalho et al. 2010). Material-related emissions are strongly impacted by the lifetime of the building (Häfliger et al. 2017) and the service life of the components of which it is made (Chau et al. 2012; Häfliger et al. 2017; Hoxha et al. 2014; Morales et al. 2020; Ruuska & Häkkinen 2015). A comprehensive sensitivity analysis of residential buildings in Switzerland found that electricity mix, ventilation rate and heating system type were the most important parameters influencing life-cycle GHG emissions (Heeren et al. 2015). Pannier et al. (2018) investigated sensitivity analysis methods by modelling life-cycle emissions of a single-family house in France. Each method showed that Intergovernmental Panel on Climate Change (IPCC) time horizon, electricity mix and building lifetime were the three most influential factors.
One way to decrease the operational energy use of office buildings is to implement passive cooling strategies. Mixed-mode ventilation (MMV) is a combination of natural ventilation and mechanical cooling. It allows one to maintain acceptable thermal conditions with reduced energy consumption compared with conventional mechanical cooling systems (Arnold 1996). Implementation of MMV strategies in office buildings offers some energy savings in all climate zones, a literature review for the period 1996–2016 by Salcido et al. (2016) suggested. Later research, meanwhile, indicates that hot and humid climates have negligible natural ventilation potential, while desert and semi-arid climates exhibit a higher potential if one assumes occupants’ ability to adapt to thermal conditions (Chen et al. 2017). Some recent studies investigated the influence of building design parameters on the energy use of MMV buildings (Gokarakonda et al. 2019; Neves et al. 2019). Among parameters specific to naturally ventilated spaces, the important ones turned out to be zone depth (Gokarakonda et al. 2019) and window opening effective area (Neves et al. 2019), the latter being the most influential when external shading is low (Neves et al. 2019).
To the authors’ knowledge, a systematic parametric variability analysis for life-cycle GHG emissions of office buildings in developing countries has not yet been conducted. Addressing this research gap is particularly important considering that emerging economies are expected to rapidly increase their building stock (IEA 2017) and energy use for cooling (IEA 2018) in the coming decades. These countries likely represent the majority of future office building stock additions. With hot climates being typical for many emerging economies, it also appears relevant to investigate the potential of MMV strategies for GHG emissions reduction.
Brazil was chosen for this study because it is one of the biggest emerging economies and represents a whole range of hot climates. Alves et al. (2017) performed a comprehensive analysis of office building stock in Belo Horizonte, Brazil, and found that typical office buildings built before the 2000s had a cellular floor layout with an ‘E’, ‘H’ or ‘U’-shaped floor plan; they also usually relied on MMV systems. Newer buildings showed an increase in open office spaces and in the use of central AC cooling systems (with no natural ventilation available), which caused higher energy use intensity (Alves et al. 2017). Recent work on Brazilian office buildings improved the understanding of their energy performance (Alves et al. 2017; Borgstein & Lamberts 2014; Lamberts et al. 2015; Wong et al. 2019) and possible energy savings (Alves et al. 2018; Carvalho et al. 2010; Neves et al. 2019). In Brazil, whole-building LCA studies are limited to university buildings (Gomes et al. 2018) and residential housing (Evangelista et al. 2018; Morales et al. 2019; Paulsen & Sposto 2013). A material flow analysis performed by Condeixa et al. (2017) shows that national standards (ABNT 2006; Sinduscon-MG 2007) and industry averages (PINI 2010) may be used to model the material requirements of representative buildings.
The present paper uses archetypes for office buildings in hot climates. Archetypes are often used in the literature to describe subdivisions of building stocks, e.g. to model energy or material demand of regional or national building stocks (Heeren et al. 2013; Heeren & Hellweg 2019; Swan & Ugursal 2009). Office building archetypes were used (1) to estimate their life-cycle GHG emissions; (2) to find key drivers of these impacts in both mixed-mode (MM) and fully AC buildings; and (3) to identify strategies to reduce the impacts.
The framework involves defining office building archetypes, selecting a sample of 1000 building variations, modelling building energy use, material demand and GHG emissions, and performing a sensitivity analysis. The system boundaries include life-cycle stages associated with production and the construction process, replacement, operational energy use and end-of-life (see Section 2.5).
Three building archetypes were created, representative of Brazilian office buildings. The design and operational parameters are listed in Table 1. The material data and main design features (such as building size and floor layout) were based on commercial building types described in national standard NBR 12721 (ABNT 2006), further specified by the Syndicate of Construction Industry (Sinduscon-MG 2007). Buildings denoted in NBR 12721 (ABNT 2006) as CSL-8, CSL-16 and CAL-8 correspond to archetypes I, II and III, respectively. These archetypes were defined by considering the current real estate market and they serve as a tool to estimate construction costs (Sinduscon-MG 2007). The structural elements were modelled according to typical construction practices in Brazil (Morishita et al. 2011). The area of internal walls was determined based on the amount of brick per 1 m2 according to NBR 12721 (ABNT 2006), reduced by the amount of brick needed for external walls. Other data in Table 1 were chosen based on national standards, technical reports and other studies on Brazilian office buildings (ABNT 2008; Alves et al. 2017; ANVISA 2003; CB3E et al. 2015; CIBSE 2004).
|ARCHETYPE I||ARCHETYPE II||ARCHETYPE III|
|Number of floors||8||16||8|
|Building footprint (m)||20 × 30||20 × 30||20 × 30|
|Gross floor area (m2)||4,800||9,600||4,800|
|Floor height (m)||2.8||2.8||2.8|
|Number of elevators||2||3||2|
|External wall structure||2.5 cm plaster
+ 9 cm brick +
2.5 cm plaster
|2.5 cm plaster +
13.5 cm brick +
2.5 cm plaster
|2.5 cm plaster
+ 9 cm brick +
2.5 cm plaster
|Internal wall structure||2.5 cm plaster + 9 cm brick + 2.5 cm plaster|
|Roof structure||10 cm concrete + 6 cm air + 0.6 cm fibre cement roof tile|
|Floor structure||Internal: 1.25 cm acoustic ceiling + 10 cm concrete + 0.5 cm carpet
External: 20 cm concrete + 0.5 cm carpet
|Internal wall area per floor (m2)||179.9||144.6||40.2|
|Glazing thickness (mm)||6||6||6|
|Glazing thermal transmittance (W/(m2.K))||5.782||5.782||5.782|
|Internal loads schedule||0600–1800 hours on weekdays||0600–1800 hours on weekdays||0600–1800 hours on weekdays|
|Occupant density (people/100 m2)||11||11||11|
|Lighting use intensity (W/m2)||10.5||10.5||10.5|
|Equipment use density (W/m2)||14||14||14|
|Mechanical ventilation: fresh air intake (L/s/person)||7.5||7.5||7.5|
Among the parameters significantly affecting the emission performance of buildings in hot climates, 10 parameters were selected based on findings of prior research (Borgstein & Lamberts 2014; Carvalho et al. 2010; Häfliger et al. 2017; Heeren et al. 2015; Hoxha et al. 2014; Lam & Hui 1996a; Lamberts et al. 2015; Morales et al. 2020; Neves et al. 2019; Ruuska & Häkkinen 2015; Wong et al. 2019). Each parameter was assigned a list of possible input values (Table 2). For example, a city was selected from among 12 Brazilian cities reflecting a whole range of climatic conditions, as represented by cooling degree-hours (CDH). The electricity mix is dependent on the region (see Figure S1 and Table S8 in the supplemental data online). Shading was modelled as a window overhang, and its values ranged from 0 (no shading) to 1 (overhang depth equal to window height). Window opening effective area represents the share of windows that can be opened for natural ventilation; when this share is zero, the building is fully AC.
|PARAMETER||POSSIBLE INPUT VALUES||EXPLANATION OF THE CHOSEN VALUES|
|CITY||CDH||ELECTRICITY MIX (kg CO-eq/kWh)|
|Citya||São Paulo||14,172||0.233||The 12 largest cities with at least two in each region of Brazil (for a map with the selected cities, see Section 2 in the supplemental data online)|
|Rio de Janeiro||45,016||0.233|
|Building archetype||I, II, III||Archetypes defined in NBR 12721 (ABNT 2006)|
|Window-to-wall ratio (WWR)||30%, 50%, 70%, 90%||Full range of possible values|
|Solar heat gain coefficient (SHGC)||0.2, 0.4, 0.6, 0.8||Full range of possible values|
|Window opening effective area||0.0b, 0.1, 0.3, 0.5, 0.7, 0.9||Full range of possible values|
|Shading||0.0, 0.2, 0.4, 0.6, 0.8, 1.0||Full range of possible values|
|Cooling set point (°C)||22, 23, 24, 25||Based on Lamberts et al. (2015)|
|Coefficient of performance (COP)c||2.0, 2.5, 3.0, 3.5, 4.0||Based on Inmetro (2017) and Lamberts et al. (2015)|
|Building lifetime (years)||50, 75, 100||Recommended minimum of 50 years (ABNT 2013), but 100 years is assumed as a maximum for a concrete structure|
|Component service time multiplier||75%, 100%, 125%||Assumed based on the literature (see Section 3.2 in the supplemental data online)|
The parameters were sampled using Latin hypercube sampling (LHS), a method widely used in building energy research (Tian et al. 2018). It uses stratified sampling to ensure that the chosen sample uniformly covers the parameter space (McKay et al. 1979). The components of the different variables are matched at random, making this a quasi-random method. A sample of 1000 building variations was selected out of the 3,732,480 possible combinations. The chosen sample size (1000 iterations) leads to model convergence for GHG emissions of all life-cycle stages, with the approximate relative error at < 5% (see Section 4 in the supplemental data online).
Building energy simulations were performed in EnergyPlus 9.2.0 (US Department of Energy 2019). The climate of the chosen Brazilian cities was simulated using weather files with a typical meteorological year (Climate.OneBuilding 2021), based on data collected from weather stations of the National Meteorological Institute of Brazil (INMET) (Roriz 2012). EnergyPlus input files were created with the help of open-source code developed by Santesso (2018). Thermal properties of materials were based on national-specific data (Morishita et al. 2011) and built-in EnergyPlus material datasets (ASHRAE 2005). Heating and cooling systems were modelled as ideal systems that meet the loads but consume no energy. MMV was modelled according to Neves et al. (2019), where the cooling regime is a function of office occupancy, thermal satisfaction of the occupants, and indoor and outdoor temperature. The sensor ‘Zone Thermal Comfort ASHRAE 55 Adaptive Model 90% Acceptability Status’ is used to check if the indoor climate is within comfortable limits. The mechanical cooling (heating, ventilation and air-conditioning—HVAC) system is activated if the zone is occupied and fewer than 90% of occupants are satisfied with the thermal conditions. The natural ventilation mode is activated (i.e. windows are opened) when all three conditions are met: the zone is occupied, the indoor operative temperature is higher than the outdoor temperature, and more than 90% of occupants are satisfied with the thermal conditions. In any other case—e.g. when the zone is unoccupied—the HVAC system is off, and the windows are closed.
The model included material demand for construction and replacement. The material intensity data are available in Section 3.1 in the supplemental data online. The replacement factor ri was determined for each building component i:
where BL is the building lifetime; CLi is the service life of component i (see Section 3.2 in the supplemental data online); and m is the component service life multiplier. When the service life of a component is equal to the building’s lifetime, there are no replacements. The component service life multiplier can be 75%, 100% or 125%, representing faster, typical or slower replacement cycles, respectively.
The energy simulation included aspects aimed at reflecting the material intensity. The focus was on materials that could significantly influence the building’s thermal response, i.e. by being a part of the building envelope or influencing thermal inertia (for the effect of thermal inertia on GHG emissions, see Heeren et al. 2015). Floor covering and acoustic ceiling were modelled as construction layers in the energy simulation. As WWR varied, the material intensity of glass and brick was adjusted (see Table S3 in the supplemental data online). Finally, the simulation included thermal mass in the form of internal walls, calculated based on the amount of brick per 1 m2 according to NBR 12721 (ABNT 2006), reduced by the amount of brick needed for external walls.
GHG emissions were modelled using LCA methodology, according to European Standard EN 15978 (European Standards, 2011). This work covered modules A1–A5 (production and construction process), B4 (replacement), B6 (operational energy use), and C1–C4 (end of life). The system boundary was in line with the boundaries for each considered module, as defined by EN 15978 (for the list of building components, see Table S3 in the supplemental data online). The functional unit was defined as ‘1 m2 of the gross floor area (GFA) of a building during one year of its operation’. GHG emissions were calculated using GWP100 metrics, as given by the IPCC (2013) method. Life-cycle inventory (LCI) data were sourced from the ecoinvent v3.7.1 database (allocation cut-off) (Weidema et al. 2013), except for the acoustic ceiling for which industry data were used (Knauf A/S 2016). Material emissions were calculated based on material intensity (see Table S3 in the supplemental data online). For the replacement stage, the material intensity was multiplied by the replacement factor (equation 1). The system processes selected for this study are of the market type, so they include transportation (Weidema et al. 2013), thus covering module A4—Transport to the building site. Process requirements for construction and demolition were limited to energy use and machinery wear, as documented in Section 3.3 in the supplemental data online. It is assumed that the material intensities include on-site material losses; the underlying data serve as a tool to estimate construction costs (Sinduscon-MG 2007), which likely include the cost of wasted material. Operating energy use emissions were calculated based on EnergyPlus simulation results (see Section 3.4 in the supplemental data online). It was assumed that all waste is transported by lorry to a waste-processing facility located 11 km from the construction site (Condeixa et al. 2014). For waste processes of the market type, the transportation distance was changed to 11 km. For LCI datasets, see Section 3.5 in the supplemental data online.
A multivariate regression analysis was used to quantify the sensitivity of the impact to each parameter. Before the regression analysis, all the variables were standardised according to formulas from Bring (1994):
where Bi is the standardised regression coefficient (SRC) for parameter i. The bigger the absolute value of coefficient Bi, the more sensitive y is to the changes in parameter i. Numeric data were used to represent categorical variables. Two variables substituted the variable city: climate represented by CDH, and electricity mix represented by emission intensity (kg CO2-eq/kWh). Variable building type was redefined by two binary variables: Archetype II and Archetype III. Each of these binary variables had a value of 1 if a given sample item was of the given building type, and 0 otherwise. Consequently, SRCs for variables Archetype II and Archetype III reflected the change in the dependent variable y associated with switching the building type from archetype I to archetypes II or III, respectively. The regression analysis calculated 95% confidence intervals (CIs) for the standardised coefficients.
The archetype modelling approach was used to estimate life-cycle GHG emissions of office buildings located in Brazil. The median impact was approximately 39 kg CO2-eq/m2 GFA/year, with an interquartile range of 26 (31–57) kg CO2-eq/m2 GFA/year (Table 3). Operational energy use (B6) contributed most to GHG emissions of all simulated buildings, with a median 67% contribution. Consequently, this module was also the main source of variation in the total impact. The median contribution of material production and transport to the construction site (A1–A4) was 15%, corresponding to 448 kg CO2-eq/m2 GFA and with a 95% CI of [363, 500]. Building component replacement (B4) constituted a median of 13% of the total impacts, with emissions of 391 kg CO2-eq/m2 GFA and 95% CI [140, 938]. The emissions of other considered life-cycle modules were negligible.
|GHG EMISSIONS (kg CO2-eq/m2 GFA/year)|
To better understand the composition of life-cycle GHG emissions, the components of the most impactful modules were investigated (Figure 1). Material production and transport to the site (A1–A4) showed the biggest contribution of steel, concrete, aluminium, lime and plywood, with these five materials responsible for around three-quarters of GHG emissions of this life-cycle stage. Material replacement emissions (B4) were the highest for paint, responsible for median 37% of this module’s GHG emissions. Paint, followed by five other items (AC devices, floor covering, aluminium, doors and ceramic tiles), made up a median of 96% of GHG emissions associated with material replacement. Operational energy use (B6) was composed of medians of 17% cooling, 13% equipment and 17% lighting. In a great majority of cases, emissions from heating were negligible. Cooling was the energy end use causing the most significant variations in GHG emissions. As this module was the most impactful, cooling demand represented the main factor determining the differences in GHG emissions of the buildings. For further details on the composition of the emissions, see the supplemental data online.
How can cooling strategies influence GHG emissions? Addressing this matter required a comparison of the emissions of fully AC and MM buildings (Figure 2). In all cities except Goiânia, buildings with a MM cooling strategy were associated with lower emissions. In some cases, possible emission savings were significant (e.g. Rio de Janeiro, Recife). Goiânia was an exception to this trend, likely due to a sampling error—closer inspection of the results revealed a bias in cooling efficiencies, making the AC buildings relatively less polluting. Nonetheless, MM office buildings seemed to be an effective alternative to buildings relying solely on mechanical cooling, reducing median emissions by 10%.
A multivariate regression analysis was performed for MM and AC buildings (Table 4) to identify the key drivers of life-cycle GHG emissions. The linear models explained > 96% of the variance in total emissions (adjusted R2 > 0.96). The SRCs were lower for AC buildings, and the 95% CI was wider. The electricity mix was the most important parameter, with a strong correlation for both cooling strategies. Climate ranked second in importance for MM buildings and third for AC buildings. Cooling efficiency proved to be another influential factor, its effect being stronger for AC buildings. MM buildings showed a stronger correlation with material-related factors (building lifetime and component service life) due to their lower operational energy use, making material-related emissions relatively more impactful. On the other hand, the impact of AC buildings was more sensitive to parameters closely related to operational energy use (WWR, SHGC, shading). Window-opening effective area ranked fifth for buildings with an MMV system and was an architectural design feature of the greatest importance to their GHG emissions.
|INDEPENDENT VARIABLE||MIXED-MODE BUILDINGS||FULLY AIR-CONDITIONED BUILDINGS|
|ADJUSTED R2 = 0.966||ADJUSTED R2 = 0.963|
|STANDARDISED COEFFICIENTS||95% CI||STANDARDISED COEFFICIENTS||95% CI|
|Electricity mix||0.79||(0.77, 0.80)||0.79||(0.75, 0.82)|
|Climate (CDH)||0.23||(0.21, 0.25)||0.22||(0.19, 0.26)|
|Archetype II (versus Archetype I)||0.09||(0.08, 0.11)||0.06||(0.02, 0.10)|
|Archetype III (versus Archetype I)||0.07||(0.06, 0.08)||0.02||(–0.02, 0.05)|
|Window-to-wall ratio (WWR)||0.02||(0.00, 0.03)||0.03||(0.00, 0.06)|
|Solar heat gain coefficient (SHGC)||0.06||(0.05, 0.07)||0.07||(0.04, 0.10)|
|Window opening effective area||–0.09||(–0.11, –0.08)||–||–|
|Shading||–0.04||(–0.05, –0.02)||–0.05||(–0.08, –0.02)|
|Cooling set point||–0.07||(–0.08, –0.05)||–0.07||(–0.10, –0.04)|
|Cooling efficiency||–0.17||(–0.19, –0.16)||–0.23||(–0.26, –0.20)|
|Building lifetime||–0.08||(–0.09, –0.07)||–0.06||(–0.10, –0.03)|
|Component service life multiplier||–0.10||(–0.11, –0.08)||–0.08||(–0.11, –0.05)|
The eight-floor archetype with cellular floor layout, denoted as archetype I, turned out to be the least emission intensive—the change to any other building type was associated with an increase in GHG emissions (Table 4). The taller archetype had slightly lower operational energy use, but its emissions were still higher due to higher requirements for materials such as steel, concrete and paint. The archetype with an open floor layout (archetype III) had higher life-cycle emissions than archetype I, mainly due to its higher aluminium demand.
The sensitivity of the total life-cycle GHG emissions shown in Table 4 is mostly determined by module B6 (operational energy use) due to its high importance for overall emissions (Table 3). For the results by the life-cycle stage, Section 5.3 in the supplemental data online.
How does the effectiveness of the MM cooling strategy change under different climatic conditions? To answer, SRCs were calculated for MM buildings in each city. The importance of various parameters changed with increasing CDH. For a few parameters, these changes could be approximated by a linear relationship (Figure 3). Buildings in milder climates (with a low CDH) showed more dependence on building lifetime, showing the major role of material emissions for buildings with small cooling needs. As the climate gets hotter, the need for cooling increases, so the relative importance of the cooling set point and the cooling efficiency also increases. The cooling efficiency gained significance at a much faster rate, suggesting that MM office buildings in hotter climates may share some similarities with AC buildings (cf. Table 4).
The obtained range of GHG emissions for Brazilian office buildings is in line with values found in the literature for office buildings, generally ranging from just above 20 to over 100 kg CO2-eq/m2/year (Airaksinen & Matilainen 2011; Asdrubali et al. 2013; Frischknecht et al. 2019; Junnila et al. 2006; Kofoworola & Gheewala 2008; Kumanayake et al. 2018; Lessard et al. 2018; Suzuki & Oka 1998; Wallhagen et al. 2011; Ylmén et al. 2019). As expected, operational energy use was the single most important module for GHG emissions, also associated with the biggest variations.
The GHG emissions associated with modules A1–A4 (the material production and transport to the construction site) were generally similar to the values found in previous studies (Airaksinen & Matilainen 2011; Asdrubali et al. 2013; Frischknecht et al. 2019; Junnila et al. 2006; Kofoworola & Gheewala 2008; Kumanayake et al. 2018; Lessard et al. 2018; Ylmén et al. 2019). The only significantly higher values were those of more massive structures, due to either height (Yan et al. 2010) or national regulations for earthquake-resistant structures (Suzuki & Oka 1998). Lower values were observed in cases with wooden walls (Wallhagen et al. 2011), improved material use options (Chau et al. 2015) or different modelling assumptions about the reinforcing steel (Dimoudi & Tompa 2008; Eberhardt et al. 2019). The studies assume different building lifetimes, so their construction impacts were compared considering the entire building lifetime, and not on a per year basis (see Section 1 in the supplemental data online).
This study confirms that the main contributors to GHG emissions of the material production stage are steel and concrete, often followed by brick and limestone (a constituent of cement plaster and cement mortar) (Dimoudi & Tompa 2008; Fenner et al. 2018; Junnila et al. 2006; Kofoworola & Gheewala 2008; Kumanayake et al. 2018; Morales et al. 2019; Seo & Hwang 2001; Ylmén et al. 2019). High levels of aluminium-related GHG emissions associated with window frames or curtain wall systems were also found elsewhere (Meneghelli 2018; Morales et al. 2019; Najjar et al. 2019; Taborianski & Prado 2012). Another hotspot of material production emissions was plywood. Although few whole-building LCA studies consider this material, their results confirm its significant environmental impact (Kylili et al. 2017; Sinha et al. 2016).
The material replacement emissions were statistically smaller than initial material emissions (a median 48% contribution to embodied emissions). Research shows that material replacement impacts often dominate over initial material impacts in buildings with a lifetime of over 50 years (Cole & Kernan 1996; Ding 2007; Häfliger et al. 2017; Yohanis & Norton 2002), although this is not always the case (Opher et al. 2021; Wiik et al. 2018; Williams et al. 2012). However, frequent fit-outs in office buildings represent a potentially significant contribution to the total impacts (Forsythe & Wilkinson 2015). Therefore, the model may underestimate replacement-related impacts. What may be considered surprising, replacement material emissions were dominated by paint (Figure 1), a material whose contribution to initial emissions was < 5%. However, the importance of paint increases due to the high frequency of replacement, shown also by other researchers (Eberhardt et al. 2019; Morales et al. 2020; Rauf & Crawford 2015).
The largest variations in GHG emissions could be observed for the operational energy stage (module B6), which is partly a consequence of the parameter choice (see Section 5.3 in the supplemental data online). As shown by the sensitivity analysis (Table 4), the emission intensity of electricity is the key driver for GHG emissions. Climate was the second most important because it influences the amount of cooling needed in the office space.
Cooling efficiency was notably less important for GHG emissions of buildings with MMV (Table 4), which is a consequence of their decreased reliance on the HVAC system. However, the importance of cooling efficiency in MM buildings strongly increased with increasing CDH (Figure 3), suggesting that MM office buildings in hotter climates show increasing dependence on AC cooling. Additional investigation of building energy simulation results confirmed that the HVAC system was more active in MM buildings located in climates with a higher demand for cooling.
MM office buildings were more sensitive to parameters associated with material emissions (building lifetime and component service life multiplier) and less sensitive to those related to operational energy use (WWR, SHGC, shading) (Table 4). This pattern emerges because the MMV buildings generally had lower operational energy use, making material-related emissions relatively more impactful.
According to the sensitivity analysis, the eight-floor archetype with a cellular layout (archetype I) was the least polluting. The eight-floor archetype with an open floor layout (archetype III) showed different performance depending on the cooling strategy—the AC buildings were less emission intensive because the increase of material-related emissions was countered by decreased operational energy use, possibly caused by thermal inertia effects.
The findings of the sensitivity analysis are generally consistent with the literature. The remarkably high importance of electricity mix for life-cycle GHG emissions was shown by others (Blom et al. 2011; Frischknecht et al. 2019; Heeren et al. 2015; Obrecht et al. 2021; Pannier et al. 2018; Rossi et al. 2012). Heeren et al. (2015) reported a relatively small influence of climate on GHG emissions of Swiss buildings, but this discrepancy could be attributed to a smaller range in the analysed climate parameters. Lam & Hui (1996b) also noted the high importance of cooling set point and cooling efficiency for operational energy use in offices. The results confirm that window-opening effective area is the most important parameter influencing the cooling loads of MM office buildings, followed by SHGC, shading and, eventually, WWR (Neves et al. 2019).
MM office buildings offered an average 14% emission reduction compared with fully AC buildings. The potential savings differed among cities, but there was no pattern, possibly due to insufficient sample size and associated sampling errors. MM buildings in hotter climates showed an increasing dependence on AC cooling systems, so the relative benefits of introducing the MMV system seem to be smaller. In milder climates, energy demand for cooling is comparatively lower, so the savings potential is limited. Consequently, the implementation of MM buildings in moderate climates offers the highest energy savings, which had been noted by other researchers as well (Chen et al. 2017; Ward et al. 2012). Switching to MM buildings in cities with a high carbon intensity of electricity could also offer more significant GHG emission savings.
The findings are mainly applicable to office buildings located in warm and hot climates, ranging from around 10,000 to 80,000 CDH. Applying the results to other regions should be done with caution because the emission intensity of energy carriers and construction materials may substantially differ among countries (Frischknecht et al. 2019), leading to vastly different GHG emissions even if the building’s lifetime is accounted for (Frischknecht et al. 2020). Despite these differences, the collected data suggest that many regions could benefit from replacing fully AC office buildings with MM ones.
Non-negligible sampling errors could be observed, e.g. in the case of AC buildings in Goiânia whose emissions were similar to those of MM buildings, but likely underestimated (Figure 2). LHS has the advantage of covering the parameter space uniformly, making it better than conventional sampling methods such as Monte Carlo (Saltelli 2008). However, the chosen sample size (1000 building variations) did not sufficiently cover the parameter space, especially for AC buildings (a subset of 167 buildings). The small sample size was also why AC buildings had a wider range of 95% CI for their standardised coefficients.
The results of the sensitivity analysis (Table 4) were influenced by the chosen range of parameter values (Table 2) because the standardisation of regression coefficients depends directly on standard deviations of parameters. Some parameters had a full span of physically possible values, but others could have had more significance if a wider range were used. For example, component service life ranged from 75% to 125% of the standard values defined in Table S4 in the supplemental data online, but allowing for a broader range could make the component service life multiplier more important. Additionally, a wide range of possible CDHs made climate a more significant parameter.
LCI was not fully adapted to Brazilian reality and included global data for some essential processes, e.g. aluminium production. Material-related impacts could be overestimated, as environmental impacts in the Brazilian context are often smaller than the global average (Frischknecht et al. 2019; Morales et al. 2019, 2020).
Other aspects not included in this work include the thermal comfort of office occupants, indoor air quality, occupant behaviour, design differences between the AC and MM buildings (with the associated material demand differences), and the influence of building shape. Humidity plays a vital role in the natural ventilation potential (Chen et al. 2017), but it was not considered. Some material–energy interactions were not accounted for, e.g. demand for aluminium associated with window size (WWR) or with the existence of shading devices, sometimes made of aluminium. Finally, this study did not include all the constituents of the life-cycle GHG emissions of a building. A simplified system boundary can potentially lead to underestimating emissions by up to 10% (Zhang et al. 2019). Drains, ventilation ducts and fire protection equipment were omitted.
The efforts to mitigate the climate change impacts of Brazilian office buildings should focus on the carbon intensity of the electricity mix. Although 65% of Brazilian electricity is based on hydropower, the share of natural gas has been steadily growing in the past decades (Ministry of Mines and Energy 2019). Development of wind and solar energy and electricity demand reduction are some actions that could reduce the CO2 emissions of electricity generation. Close to half of the country’s office space is located in two federal states (São Paulo and Rio de Janeiro) (IBGE 2019). Improvement of the electricity mix in such areas could yield the most considerable benefits for the life-cycle GHG emissions of Brazilian office buildings. Electricity demand could be reduced in office buildings themselves with the use of energy-efficiency strategies. This way, any parameter correlated with operational energy use could potentially be a part of the solution to increasing emissions from electricity generation in Brazil. Additionally, the efficiency of lighting and equipment could be improved, which would have yet another advantage: reduction of cooling needs by lowering internal heat gains. An implicit conclusion is that office buildings can profit greatly from on-site electricity production through photovoltaics because it improves electricity’s carbon intensity.
Among parameters influencing GHG emissions of office buildings, cooling efficiency was the most crucial design parameter. Highly efficient HVAC systems should be prioritised, especially in hotter climates. Decreased frequency of office fit-outs could also significantly decrease the GHG emissions, particularly for materials such as paint. Longer building lifetime is another option for a reduction in GHG emissions, given our assumptions that building lifetime does not impact initial material intensities. Building life extension would be relatively more effective in a milder climate. Brazilian policymakers may want to offer incentives for MM office buildings, because they were less emission intensive in every investigated city. The benefits are the biggest for high values of window-opening effective area. Better emission performance of archetype II suggests that reduction of aluminium use could yield additional emission savings, whose exact magnitude depends on modelling assumptions (Meneghelli 2018).
The authors express their sincere gratitude to Damasia Gonzalez dos Santos Oliveira, Pedrinho Goldman, Vanessa Gomes da Silva, Fernanda Belizário Silva and Camila Kramel for their valuable inputs which contributed to the authors’ understanding of the Brazilian construction industry. Furthermore, the authors thank Leticia Neves and colleagues for their work on energy performance of mixed-mode buildings, which was essential in the development of this work.
The authors have no competing interests to declare.
This work was funded by the Norwegian University of Science and Technology (NTNU) and the Research Council of Norway (grant number 300330).
The two supplemental data for this article can be accessed at:
ABNT. (2006). NBR 12721-2006. Avaliação de custos de construção para incorporação imobiliária e outras disposições para condomínios edilícios. Associação Brasileira de Normas Técnicas (ABNT). https://www.abntcatalogo.com.br/norma.aspx?ID=62882
ABNT. (2008). NBR 16401-3. Instalações de ar-condicionado—Sistemas centrais e unitários. Parte 3: Qualidade do ar interior. Associação Brasileira de Normas Técnicas (ABNT). https://www.abntcatalogo.com.br/norma.aspx?ID=572
ABNT. (2013). NBR 15575-1. Edificações Habitacionais—Desempenho. Parte 1: Requisitos gerais. Associação Brasileira de Normas Técnicas ABNT). https://www.abntcatalogo.com.br/norma.aspx?ID=195568
Airaksinen, M., & Matilainen, P. (2011). A carbon footprint of an office building. Energies, 4(8), 1197–1210. DOI: https://doi.org/10.3390/en4081197
Alves, T., Machado, L., de Souza, R. G., & de Wilde, P. (2017). A methodology for estimating office building energy use baselines by means of land use legislation and reference buildings. Energy and Buildings, 143, 100–113. DOI: https://doi.org/10.1016/j.enbuild.2017.03.017
Alves, T., Machado, L., de Souza, R. G., & de Wilde, P. (2018). Assessing the energy saving potential of an existing high-rise office building stock. Energy and Buildings, 173, 547–561. DOI: https://doi.org/10.1016/j.enbuild.2018.05.044
ANVISA. (2003). Resolução-RE Nº 09, de 16 de janeiro de 2003. Agência Nacional de Vigilância Sanitária (ANVISA). https://www.saude.mg.gov.br/index.php?option=com_gmg&controller=document&id=899
Arnold, D. (1996). Mixed-mode HVAC—An alternative philosophy. ASHRAE Transactions: Symposia, article CONF-960254. Winter meeting of the American Society of Heating, Refrigeration and Air Conditioning Engineers (ASHRAE). https://www.osti.gov/biblio/392497-mixed-mode-hvac-alternative-philosophy
Asdrubali, F., Baldassarri, C., & Fthenakis, V. (2013). Life cycle analysis in the construction sector: Guiding the optimization of conventional Italian buildings. Energy and Buildings, 64, 73–89. DOI: https://doi.org/10.1016/j.enbuild.2013.04.018
Blom, I., Itard, L., & Meijer, A. (2011). Environmental impact of building-related and user-related energy consumption in dwellings. Building and Environment, 46(8), 1657–1669. DOI: https://doi.org/10.1016/j.buildenv.2011.02.002
Borgstein, E. H., & Lamberts, R. (2014). Developing energy consumption benchmarks for buildings: Bank branches in Brazil. Energy and Buildings, 82, 82–91. DOI: https://doi.org/10.1016/j.enbuild.2014.07.028
Bring, J. (1994). How to standardize regression coefficients. American Statistician, 48(3), 209–213. DOI: https://doi.org/10.2307/2684719
Cabeza, L. F., Rincón, L., Vilariño, V., Pérez, G., & Castell, A. (2014). Life cycle assessment (LCA) and life cycle energy analysis (LCEA) of buildings and the building sector: A review. Renewable and Sustainable Energy Reviews, 29, 394–416. DOI: https://doi.org/10.1016/j.rser.2013.08.037
Carvalho, M. M. Q., La Rovere, E. L., & Gonçalves, A. C. M. (2010). Analysis of variables that influence electric energy consumption in commercial buildings in Brazil. Renewable and Sustainable Energy Reviews, 14(9), 3199–3205. DOI: https://doi.org/10.1016/j.rser.2010.07.009
CB3E, Eletrobras, PROCEL, & INMETRO. (2015). Catálogo de propriedades térmicas e óticas de vidros comercializados no Brasil. Universidade Federal de Santa Catarina. https://cb3e.ufsc.br/sites/default/files/projetos/etiquetagem/catalogo-propriedades-vidros-comercializados-brasil-13032015_v2.pdf
Chau, C. K., Hui, W. K., Ng, W. Y., & Powell, G. (2012). Assessment of CO2 emissions reduction in high-rise concrete office buildings using different material use options. Resources, Conservation and Recycling, 61, 22–34. DOI: https://doi.org/10.1016/j.resconrec.2012.01.001
Chau, C. K., Leung, T. M., & Ng, W. Y. (2015). A review on life cycle assessment, life cycle energy assessment and life cycle carbon emissions assessment on buildings. Applied Energy, 143, 395–413. DOI: https://doi.org/10.1016/j.apenergy.2015.01.023
Chen, Y., Tong, Z., & Malkawi, A. (2017). Investigating natural ventilation potentials across the globe: Regional and climatic variations. Building and Environment, 122, 386–396. DOI: https://doi.org/10.1016/j.buildenv.2017.06.026
CIBSE. (2004). Guide F—Energy Efficiency in Buildings. Chartered Institute of Building Services Engineers (CIBSE). https://www.cibse.org/knowledge/knowledge-items/detail?id=a0q3Y00000Hy6hcQAB
Climate.OneBuilding. (2021). Climate.OneBuilding.Org. http://climate.onebuilding.org/
Cole, R. J., & Kernan, P. C. (1996). Life-cycle energy use in office buildings. Building and Environment, 31(4), 307–317. DOI: https://doi.org/10.1016/0360-1323(96)00017-0
Condeixa, K., Haddad, A., & Boer, D. (2014). Life cycle impact assessment of masonry system as inner walls: A case study in Brazil. Construction and Building Materials, 70, 141–147. DOI: https://doi.org/10.1016/j.conbuildmat.2014.07.113
Condeixa, K., Haddad, A., & Boer, D. (2017). Material flow analysis of the residential building stock at the city of Rio de Janeiro. Journal of Cleaner Production, 149, 1249–1267. DOI: https://doi.org/10.1016/j.jclepro.2017.02.080
Deetman, S., Marinova, S., van der Voet, E., van Vuuren, D. P., Edelenbosch, O., & Heijungs, R. (2020). Modelling global material stocks and flows for residential and service sector buildings towards 2050. Journal of Cleaner Production, 245, 118658. DOI: https://doi.org/10.1016/j.jclepro.2019.118658
Dimoudi, A., & Tompa, C. (2008). Energy and environmental indicators related to construction of office buildings. Resources, Conservation and Recycling, 53(1), 86–95. DOI: https://doi.org/10.1016/j.resconrec.2008.09.008
Ding, G. K. C. (2007). Life cycle energy assessment of Australian secondary schools. Building Research & Information, 35(5), 487–500. DOI: https://doi.org/10.1080/09613210601116408
Eberhardt, L. C. M., Birgisdóttir, H., & Birkved, M. (2019). Life cycle assessment of a Danish office building designed for disassembly. Building Research & Information, 47(6), 666–680. DOI: https://doi.org/10.1080/09613218.2018.1517458
European Standards. (2011). EN 15978: Sustainability of construction works—Assessment of environmental performance of buildings—Calculation method (Pub. L. No. EN 15978, 2011). European Standards. https://www.en-standard.eu/din-en-15978-sustainability-of-construction-works-assessment-of-environmental-performance-of-buildings-calculation-method/
Evangelista, P. P. A., Kiperstok, A., Torres, E. A., & Gonçalves, J. P. (2018). Environmental performance analysis of residential buildings in Brazil using life cycle assessment (LCA). Construction and Building Materials, 169, 748–761. DOI: https://doi.org/10.1016/j.conbuildmat.2018.02.045
Fenner, A. E., Kibert, C. J., Woo, J., Morque, S., Razkenari, M., Hakim, H., & Lu, X. (2018). The carbon footprint of buildings: A review of methodologies and applications. Renewable and Sustainable Energy Reviews, 94, 1142–1152. DOI: https://doi.org/10.1016/j.rser.2018.07.012
Forsythe, P., & Wilkinson, S. (2015). Measuring office fit-out changes to determine recurring embodied energy in building life cycle assessment. Facilities. DOI: https://doi.org/10.1108/F-08-2013-0065
Frischknecht, R., Birgisdottir, H., Chae, C.-U., Lützkendorf, T., Passer, A., Alsema, E., Balouktsi, M., Berg, B., Dowdell, D., Martínez, A. G., Habert, G., Hollberg, A., König, H., Lasvaux, S., Llatas, C., Rasmussen, F. N., Peuportier, B., Ramseier, L., Röck, M., … Yang, W. (2019). Comparison of the environmental assessment of an identical office building with national methods. IOP Conference Series: Earth and Environmental Science, 323, 012037. DOI: https://doi.org/10.1088/1755-1315/323/1/012037
Frischknecht, R., Ramseier, L., Yang, W., Birgisdottir, H., Chae, C. U., Lützkendorf, T., Passer, A., Balouktsi, M., Berg, B., Bragança, L., Butler, J., Cellura, M., Dixit, M., Dowdell, D., Francart, N., Martínez, A. G., Gomes, V., Silva, M. G. D., Guimaraes, G., … Zara, O. (2020). Comparison of the greenhouse gas emissions of a high-rise residential building assessed with different national LCA approaches—IEA EBC Annex 72. IOP Conference Series: Earth and Environmental Science, 588, 022029. DOI: https://doi.org/10.1088/1755-1315/588/2/022029
Gokarakonda, S., van Treeck, C., & Rawal, R. (2019). Influence of building design and control parameters on the potential of mixed-mode buildings in India. Building and Environment, 148, 157–172. DOI: https://doi.org/10.1016/j.buildenv.2018.10.043
Gomes, V., Saade, M., Lima, B., & Silva, M. (2018). Exploring lifecycle energy and greenhouse gas emissions of a case study with ambitious energy compensation goals in a cooling-dominated climate. Energy and Buildings, 173, 302–314. DOI: https://doi.org/10.1016/j.enbuild.2018.04.063
Häfliger, I.-F., John, V., Passer, A., Lasvaux, S., Hoxha, E., Saade, M. R. M., & Habert, G. (2017). Buildings environmental impacts’ sensitivity related to LCA modelling choices of construction materials. Journal of Cleaner Production, 156, 805–816. DOI: https://doi.org/10.1016/j.jclepro.2017.04.052
Heeren, N., & Hellweg, S. (2019). Tracking construction material over space and time: Prospective and geo-referenced modeling of building stocks and construction material flows. Journal of Industrial Ecology, 23(1), 253–267. DOI: https://doi.org/10.1111/jiec.12739
Heeren, N., Jakob, M., Martius, G., Gross, N., & Wallbaum, H. (2013). A component based bottom-up building stock model for comprehensive environmental impact assessment and target control. Renewable and Sustainable Energy Reviews, 20, 45–56. DOI: https://doi.org/10.1016/j.rser.2012.11.064
Heeren, N., Mutel, C. L., Steubing, B., Ostermeyer, Y., Wallbaum, H., & Hellweg, S. (2015). Environmental impact of buildings—What matters? Environmental Science & Technology, 49(16), 9832–9841. DOI: https://doi.org/10.1021/acs.est.5b01735
Heiselberg, P., Brohus, H., Hesselholt, A., Rasmussen, H., Seinre, E., & Thomas, S. (2009). Application of sensitivity analysis in design of sustainable buildings. Renewable Energy, 34(9), 2030–2036. DOI: https://doi.org/10.1016/j.renene.2009.02.016
Hoxha, E., Habert, G., Chevalier, J., Bazzana, M., & Le Roy, R. (2014). Method to analyse the contribution of material’s sensitivity in buildings’ environmental impact. Journal of Cleaner Production, 66, 54–64. DOI: https://doi.org/10.1016/j.jclepro.2013.10.056
Hygh, J. S., DeCarolis, J. F., Hill, D. B., & Ranji Ranjithan, S. (2012). Multivariate regression as an energy assessment tool in early building design. Building and Environment, 57, 165–175. DOI: https://doi.org/10.1016/j.buildenv.2012.04.021
IBGE. (2019). PNAD Contínua—2018 Características adicionais do mercado de trabalho. Instituto Brasileiro de Geografia e Estatística (IBGE). https://www.ibge.gov.br/estatisticas/multidominio/condicoes-de-vida-desigualdade-e-pobreza/17270-pnad-continua.html?edicao=26413&t=sobre
IEA. (2018). The future of cooling. International Energy Agency (IEA). https://www.iea.org/reports/the-future-of-cooling
Inmetro. (2017). Tabelas de consumo/eficiência energética. http://www.inmetro.gov.br/consumidor/pbe/condicionadores.asp
IPCC. (2013). Climate change 2013: The physical science basis. Contribution of Working Group I to the Fifth Assessment Report of the Intergovernmental Panel on Climate Change, (Eds.) T. F. Stocker, D. Qin, G.-K. Plattner, M. M. B. Tignor, S. K. Allen, J. Boschung, A. Nauels, Y. Xia, V. Bex & P. M. Midgley. Cambridge University Press. https://www.ipcc.ch/report/ar5/wg1/
ISO. (2006). ISO 14040:2006: Environmental management—Life cycle assessment—Principles and framework (Pub. L. No. ISO 14040). https://www.en-standard.eu/iso-14040-environmental-management-life-cycle-assessment-principles-and-framework/
Junnila, S., Horvath, A., & Guggemos, A. A. (2006). Life-cycle assessment of office buildings in Europe and the United States. Journal of Infrastructure Systems, 12(1), 10–17. DOI: https://doi.org/10.1061/(ASCE)1076-0342(2006)12:1(10)
Karimpour, M., Belusko, M., Xing, K., & Bruno, F. (2014). Minimising the life cycle energy of buildings: Review and analysis. Building and Environment, 73, 106–114. DOI: https://doi.org/10.1016/j.buildenv.2013.11.019
Knauf A/S. (2016). Environmental product declaration: Knauf Danoline Cleaneo Markant, Contur, Linear and Danopanel (perforated). The Norwegian EPD Foundation. https://www.epd-norge.no/bygningsplater-romdelingssystemer/knauf-danoline-cleaneo-markant-contur-linear-and-danopanel-perforated-article1279-318.html
Kofoworola, O. F., & Gheewala, S. H. (2008). Environmental life cycle assessment of a commercial office building in Thailand. International Journal of Life Cycle Assessment, 13(6), 498. DOI: https://doi.org/10.1007/s11367-008-0012-1
Kofoworola, O. F., & Gheewala, S. H. (2009). Life cycle energy assessment of a typical office building in Thailand. Energy and Buildings, 41(10), 1076–1083. DOI: https://doi.org/10.1016/j.enbuild.2009.06.002
Kumanayake, R., Luo, H., & Paulusz, N. (2018). Assessment of material related embodied carbon of an office building in Sri Lanka. Energy and Buildings, 166, 250–257. DOI: https://doi.org/10.1016/j.enbuild.2018.01.065
Kylili, A., Ilic, M., & Fokaides, P. A. (2017). Whole-building life cycle assessment (LCA) of a passive house of the sub-tropical climatic zone. Resources, Conservation and Recycling, 116, 169–177. DOI: https://doi.org/10.1016/j.resconrec.2016.10.010
Lam, J. C., & Hui, S. C. M. (1996a). Sensitivity analysis of energy performance of office buildings. Building and Environment, 31(1), 27–39. DOI: https://doi.org/10.1016/0360-1323(95)00031-3
Lam, J. C., & Hui, S. C. M. (1996b). Sensitivity analysis of energy performance of office buildings. Building and Environment, 31(1), 27–39. DOI: https://doi.org/10.1016/0360-1323(95)00031-3
Lamberts, R., Borgstein, E., Cursino, A., Schinazi, A., & De Dominicis, A. (2015). Benchmarking de escritórios corporativos e recomendações para certificação DEO no Brasil. Conselho Brasileiro de Construção Sustentável (CBCS). http://www.construcaospsustentavel.com.br/biblioteca/Madeira/deo_-_desempenho_energetico_operacional_em_edificacoes
Lessard, Y., Anand, C., Blanchet, P., Frenette, C., & Amor, B. (2018). LEED v4: Where are we now? Critical assessment through the LCA of an office building using a low impact energy consumption mix. Journal of Industrial Ecology, 22(5), 1105–1116. DOI: https://doi.org/10.1111/jiec.12647
McKay, M. D., Beckman, R. J., & Conover, W. J. (1979). A comparison of three methods for selecting values of input variables in the analysis of output from a computer code. Technometrics, 21, 239–245. DOI: https://doi.org/10.1080/00401706.2000.10485979
Meneghelli, A. (2018). Whole-building embodied carbon of a North American LEED-certified library: Sensitivity analysis of the environmental impact of buildings materials. Building and Environment, 134, 230–241. DOI: https://doi.org/10.1016/j.buildenv.2018.02.044
Ministry of Mines and Energy. (2019). BEN—Séries Históricas Completas 1970–2018. http://www.epe.gov.br/pt/publicacoes-dados-abertos/publicacoes/BEN-Series-Historicas-Completas
Morales, M., Moraga, G., Kirchheim, A. P., & Passuello, A. (2019). Regionalized inventory data in LCA of public housing: A comparison between two conventional typologies in southern Brazil. Journal of Cleaner Production, 238, 117869. DOI: https://doi.org/10.1016/j.jclepro.2019.117869
Morales, M., Reguly, N., Kirchheim, A. P., & Passuello, A. (2020). Uncertainties related to the replacement stage in LCA of buildings: A case study of a structural masonry clay hollow brick wall. Journal of Cleaner Production, 251, 119649. DOI: https://doi.org/10.1016/j.jclepro.2019.119649
Morishita, C., Sorgato, M. J., Versage, R., Triana, M. A., Marinoski, D. L., & Lamberts, R. (2011). Catálogo de propriedades térmicas de paredes e coberturas. Laboratório de Eficiência Energética em Edificações (LABEEE). https://www.academia.edu/14978441/Cat%C3%A1logo_de_propriedades_t%C3%A9rmicas_de_paredes_e_coberturas
Najjar, M. K., Figueiredo, K., Evangelista, A. C. J., Hammad, A. W. A., Tam, V. W. Y., & Haddad, A. (2019). Life cycle assessment methodology integrated with BIM as a decision-making tool at early-stages of building design. International Journal of Construction Management. DOI: https://doi.org/10.1080/15623599.2019.1637098
Neves, L. O., Melo, A. P., & Rodrigues, L. L. (2019). Energy performance of mixed-mode office buildings: Assessing typical construction design practices. Journal of Cleaner Production, 234, 451–466. DOI: https://doi.org/10.1016/j.jclepro.2019.06.216
Obrecht, T. P., Jordan, S., Legat, A., & Passer, A. (2021). The role of electricity mix and production efficiency improvements on greenhouse gas (GHG) emissions of building components and future refurbishment measures. International Journal of Life Cycle Assessment, 26(5), 839–851. DOI: https://doi.org/10.1007/s11367-021-01920-2
Opher, T., Duhamel, M., Posen, I. D., Panesar, D. K., Brugmann, R., Roy, A., Zizzo, R., Sequeira, L., Anvari, A., & MacLean, H. L. (2021). Life cycle GHG assessment of a building restoration: Case study of a heritage industrial building in Toronto, Canada. Journal of Cleaner Production, 279, 123819. DOI: https://doi.org/10.1016/j.jclepro.2020.123819
Pandey, D., Agrawal, M., & Pandey, J. S. (2011). Carbon footprint: Current methods of estimation. Environmental Monitoring and Assessment, 178(1–4), 135–160. DOI: https://doi.org/10.1007/s10661-010-1678-y
Pannier, M.-L., Schalbart, P., & Peuportier, B. (2018). Comprehensive assessment of sensitivity analysis methods for the identification of influential factors in building life cycle assessment. Journal of Cleaner Production, 199, 466–480. DOI: https://doi.org/10.1016/j.jclepro.2018.07.070
Paulsen, J. S., & Sposto, R. M. (2013). A life cycle energy analysis of social housing in Brazil: Case study for the program ‘MY HOUSE MY LIFE’. Energy and Buildings, 57, 95–102. DOI: https://doi.org/10.1016/j.enbuild.2012.11.014
Pérez-Lombard, L., Ortiz, J., & Pout, C. (2008). A review on buildings energy consumption information. Energy and Buildings, 40(3), 394–398. DOI: https://doi.org/10.1016/j.enbuild.2007.03.007
Ramesh, T., Prakash, R., & Shukla, K. K. (2010). Life cycle energy analysis of buildings: An overview. Energy and Buildings, 42(10), 1592–1600. DOI: https://doi.org/10.1016/j.enbuild.2010.05.007
Rauf, A., & Crawford, R. H. (2015). Building service life and its effect on the life cycle embodied energy of buildings. Energy, 79, 140–148. DOI: https://doi.org/10.1016/j.energy.2014.10.093
Roriz, M. (2012). Arquivos Climáticos de Municípios Brasileiros. Associação Nacional de Tecnologia do Ambiente Construído. https://labeee.ufsc.br/downloads/arquivos-climaticos/formato-epw
Rossi, B., Marique, A.-F., & Reiter, S. (2012). Life-cycle assessment of residential buildings in three different European locations, case study. Building and Environment, 51, 402–407. DOI: https://doi.org/10.1016/j.buildenv.2011.11.002
Ruuska, A. P., & Häkkinen, T. M. (2015). The significance of various factors for GHG emissions of buildings. International Journal of Sustainable Engineering, 8(4–5), 317–330. DOI: https://doi.org/10.1080/19397038.2014.934931
Salcido, J. C., Raheem, A. A., & Issa, R. R. A. (2016). From simulation to monitoring: Evaluating the potential of mixed-mode ventilation (MMV) systems for integrating natural ventilation in office buildings through a comprehensive literature review. Energy and Buildings, 127, 1008–1018. DOI: https://doi.org/10.1016/j.enbuild.2016.06.054
Saltelli, A. (Ed.). (2008). Global sensitivity analysis: The primer. Wiley. DOI: https://doi.org/10.1002/9780470725184
Santesso, C. A. (2018). ParIDF: Python open source code developed to perform parametric simulations through EnergyPlus Building Energy Simulation (BES) software (Source code). Universidade de São Paulo. https://www.iau.usp.br/laboratorios/lca/index.php/trabalhos-conforto/
Sartori, I., & Hestnes, A. G. (2007). Energy use in the life cycle of conventional and low-energy buildings: A review article. Energy and Buildings, 39(3), 249–257. DOI: https://doi.org/10.1016/j.enbuild.2006.07.001
Seo, S., & Hwang, Y. (2001). Estimation of CO2 emissions in life cycle of residential buildings. Journal of Construction Engineering and Management, 127(5), 414–418. DOI: https://doi.org/10.1061/(ASCE)0733-9364(2001)127:5(414)
Sinduscon-MG. (2007). Custo unitário básico (CUB/m2): Principais aspectos. Sinduscon-MG. http://www.cub.org.br/cartilha-cub-m2
Sinha, R., Lennartsson, M., & Frostell, B. (2016). Environmental footprint assessment of building structures: A comparative study. Building and Environment, 104, 162–171. DOI: https://doi.org/10.1016/j.buildenv.2016.05.012
Suzuki, M., & Oka, T. (1998). Estimation of life cycle energy consumption and CO2 emission of office buildings in Japan. Energy and Buildings, 28(1), 33–41. DOI: https://doi.org/10.1016/S0378-7788(98)00010-3
Swan, L. G., & Ugursal, V. I. (2009). Modeling of end-use energy consumption in the residential sector: A review of modeling techniques. Renewable and Sustainable Energy Reviews, 13(8), 1819–1835. DOI: https://doi.org/10.1016/j.rser.2008.09.033
Taborianski, V. M., & Prado, R. T. A. (2012). Methodology of CO2 emission evaluation in the life cycle of office building façades. Environmental Impact Assessment Review, 33(1), 41–47. DOI: https://doi.org/10.1016/j.eiar.2011.10.004
Tian, W., Heo, Y., de Wilde, P., Li, Z., Yan, D., Park, C. S., Feng, X., & Augenbroe, G. (2018). A review of uncertainty analysis in building energy assessment. Renewable and Sustainable Energy Reviews, 93, 285–301. DOI: https://doi.org/10.1016/j.rser.2018.05.029
UN. (2021). GVA by kind of economic activity. National accounts. UNData. http://data.un.org/
US Department of Energy. (2019). EnergyPlus version 9.2.0 documentation. Engineering reference. US Department of Energy. https://bigladdersoftware.com/epx/docs/9-2/engineering-reference/
Versage, R., Borgstein, E., & Lamberts, R. (n.d.). Grau-horas de resfriamento GHR. Conselho Brasileiro de Construção Sustentável (CBCS). http://cbcs2.hospedagemdesites.ws/_5dotSystem/userFiles/CTEnergia-benchmark/CBCS_GHRs_v1%20(1).pdf
Wallhagen, M., Glaumann, M., & Malmqvist, T. (2011). Basic building life cycle calculations to decrease contribution to climate change—Case study on an office building in Sweden. Building and Environment, 46(10), 1863–1871. DOI: https://doi.org/10.1016/j.buildenv.2011.02.003
Wang, J., Yu, C., & Pan, W. (2018). Life cycle energy of high-rise office buildings in Hong Kong. Energy and Buildings, 167, 152–164. DOI: https://doi.org/10.1016/j.enbuild.2018.02.038
Ward, J. K., Wall, J., & Perfumo, C. (2012). Environmentally active buildings: The controls challenge. Architectural Science Review, 55(1), 26–34. DOI: https://doi.org/10.1080/00038628.2011.641735
Weidema, B. P., Bauer, C., Hischier, R., Mutel, C., Nemecek, T., Reinhard, J., Vadenbo, C. O., & Wernet, G. (2013). Overview and methodology. Data quality guideline for the ecoinvent database version 3 (Ecoinvent Report No. 1 (v3)). The ecoinvent Centre. https://lca-net.com/publications/show/overview-methodology-data-quality-guideline-ecoinvent-database-version-3/
Wiik, M. K., Fufa, S. M., Kristjansdottir, T., & Andresen, I. (2018). Lessons learnt from embodied GHG emission calculations in zero emission buildings (ZEBs) from the Norwegian ZEB research centre. Energy and Buildings, 165, 25–34. DOI: https://doi.org/10.1016/j.enbuild.2018.01.025
Williams, D., Elghali, L., Wheeler, R., & France, C. (2012). Climate change influence on building lifecycle greenhouse gas emissions: Case study of a UK mixed-use development. Energy and Buildings, 48, 112–126. DOI: https://doi.org/10.1016/j.enbuild.2012.01.016
Wong, I. L., Krüger, E., Loper, A. C. M., & Mori, F. K. (2019). Classification and energy analysis of bank building stock: A case study in Curitiba, Brazil. Journal of Building Engineering, 23, 259–269. DOI: https://doi.org/10.1016/j.jobe.2019.02.003
Yan, H., Shen, Q., Fan, L. C. H., Wang, Y., & Zhang, L. (2010). Greenhouse gas emissions in building construction: A case study of One Peking in Hong Kong. Building and Environment, 45(4), 949–955. DOI: https://doi.org/10.1016/j.buildenv.2009.09.014
Ylmén, P., Peñaloza, D., & Mjörnell, K. (2019). Life cycle assessment of an office building based on site-specific data. Energies, 12(13), 2588. DOI: https://doi.org/10.3390/en12132588
Yohanis, Y. G., & Norton, B. (2002). Life-cycle operational and embodied energy for a generic single-storey office building in the UK. Energy, 27(1), 77–92. DOI: https://doi.org/10.1016/S0360-5442(01)00061-5
Zhang, X., Zheng, R., & Wang, F. (2019). Uncertainty in the life cycle assessment of building emissions: A comparative case study of stochastic approaches. Building and Environment, 147, 121–131. DOI: https://doi.org/10.1016/j.buildenv.2018.10.016