As of 1996 there were 88,000 kindergartens through twelfth grade (K-12) public schools in the United States providing daily housing for almost 46 million students and 2.7 million teachers as well as for extracurricular programs, daycare centers, and community programs (USDE, 2000). There is evidence that many school districts in the United States (GAO, 1995) and schools in other countries have significant and serious indoor environmental problems. From the educational standpoint, the indoor air quality (IAQ) and ventilation in school buildings may affect the health of the children and indirectly affect learning performance. Surprisingly, given the magnitude of the school population, information on IAQ in schools is very limited. Although a number of individual studies of IAQ, ventilation, and health symptoms in schools exist, a comprehensive examination of the existing research has not been compiled. We reviewed the existing published literature on IAQ, ventilation, and IAQ- and building-related health problems in schools. The objectives of this review were to:
1identify the most commonly reported building-related health symptoms involving schools;
2assemble, evaluate, and summarize existing measurement data on ventilation, carbon dioxide (CO2) concentrations and key indoor air pollutants most likely to be related to these symptoms, [e.g. volatile organic compounds (VOCs) and biological contaminants]; and
3summarize existing information on causal relationships between pollutant exposures and health symptoms in schools.
The scientific literature until 1999, published in journals and conference proceedings was searched through a number of electronic databases including Airbase from the Air Infiltration and Ventilation Center, Applied Science and Technology Index; Chemical Abstracts; Concentration of Indoor Pollutants (CIP) Database developed by Lawrence Berkeley National Laboratory; Current Contents; Education Resource Information Center; General Science Index; Inside Information; Inspec; Medline; and Toxline. A wide range of search terms related to buildings, ventilation, IAQ, and health and attendance outcomes in schools were used to explore these databases. A number of document sets were manually searched including: American Society of Heating, Refrigerating, and Air-Conditioning Engineers (ASHRAE) IAQ Conference Proceedings; ASHRAE Journal; ASHRAE Transactions; and US Environmental Protection Agency (EPA) Radon Proceedings. The EPA's School Evaluation Program (SEP) data collected in the early 1990s from 12 schools in Florida, Kansas, New Mexico, and Washington with elevated indoor radon was also examined. In all, over 300 peer-reviewed articles were reviewed and those containing studies of schools including either quantitative evaluations of ventilation or indoor concentrations of CO2, VOCs, or biological contaminants, and/or evaluations of building-related health issues were included. The papers were carefully reviewed and those studies with clear methodological flaws were excluded.
Additionally, although not discussed here, 77 Health Hazard Evaluation Reports (HHERs) on educational facilities from the National Institute for Occupational Safety and Health (NIOSH) and 70 reports on IAQ investigations of schools in California obtained through requests for information to various California state authorities were reviewed. We present this extended review in Daisey and Angell (1998).
Measurements of ventilation rates and CO2 concentrations in schools
Ventilation rates have rarely been measured in schools, although inadequate ventilation is often suspected to be an important condition leading to reported health symptoms. The ASHRAE Standard 62-1999 (ASHRAE, 1999) recommends a minimum ventilation rate of 8 l/s-person (15 cfm/person) for classrooms. Given typical occupant density of 33 per 90 m2 (1000 ft2) and a ceiling height of 3 m (10 ft), the current ASHRAE standard would require an air exchange rate of about 3 air changes per hour (ACH) for a classroom.
Average ventilation rates and ranges reported in the scientific literature for US and European schools are shown in Figure 1. Three studies were performed in non-complaint schools. Some studies provided only aggregated data while others included data for individual schools. Some data are for the same schools under different conditions such as pre- and post-radon mitigation.
Turk et al. (1987b, 1989) reported ventilation measurements made in six non-complaint schools in the US Northwest – two in Portland, Oregon and four in Spokane, Washington. Schools ranged from 3–25 years in age, 1–3 stories; all had mechanical ventilation systems of some type. Ventilation rates, calculated on a whole building volume basis, ranged from 4.5 l/s-person to 31 l/s-person. The whole or average building rate, however, includes unoccupied areas such as hallways and gymnasiums, and, as the authors point out, this average rate overestimates the local ventilation rate of occupied classrooms. For example, in one of the elementary schools, the whole building ventilation rate was 4.5 l/s-person while the ventilation rate in an occupied classroom was only 1.6 l/s-person.
Turk et al. (1993) also reported ventilation rates measured in two schools in Sante Fe, New Mexico, which were being mitigated for high radon concentrations. Twelve pre- and post-radon mitigation ventilation rates were below 3 ACH with one exception.
Nielsen (1984) reported ventilation measurements made in a random selection of 11 schools in Denmark. Measurements were made in two classrooms for three consecutive days. The average ventilation rate was 6.4 l/s-person with a range of 1.8–15.4 l/s-person.
Carbon dioxide concentrations are often used as a surrogate of the rate of outside supply air per occupant. Indoor CO2 concentrations above about 1000 ppm are generally regarded as indicative of ventilation rates that are unacceptable with respect to body odors. Concentrations of CO2 below 1000 ppm do not always guarantee that the ventilation rate is adequate for removal of air pollutants from other indoor sources (Apte et al., 2000; Seppänen et al., 1999).
It is difficult to adequately characterize indoor CO2 concentrations because they are a function of occupancy and ventilation rate, both varying as a function of time. Grab samples or other short-term measurements may be inadequate to provide information on the long-term ventilation conditions in schools. There is a great variability in the methods used to characterize the indoor CO2 concentrations in the papers discussed below.
Figures 2 and 3 present the average and ranges of CO2 concentrations reported in the scientific literature for US and Canadian schools, and for European schools, respectively, for both complaint and non-complaint schools. In many of these reports, concentrations are near or only slightly above the ASHRAE standard of 1000 ppm, regardless of complaint or non-complaint status. CO2 concentrations well above 1000 ppm were also reported for some non-complaint schools.
Brennan et al. (1991) reported mid-afternoon CO2 measurements in a non-random study of nine US non-complaint schools. Concentrations ranged from about 400 to 5000 ppm (mean = 1480 ppm). The CO2 concentrations exceeded the 1000 ppm ASHRAE ventilation standard in 74% of the rooms.
The average CO2 concentrations for three non-complaint schools in Alberta, Canada were below 1000 ppm although some measurements exceeded this concentration (Cousins and Collett, 1989). In one portable classroom the average CO2 concentration was 1950 ppm. The number of classrooms studied at each school was not provided.
Turk et al. (1993) reported slightly elevated CO2 concentrations for two schools in New Mexico prior to and after radon mitigation. Fisher et al. (1994) and Thorne (1993) show similar elevated indoor CO2 concentrations prior to radon mitigation, with reductions to levels below 1000 ppm post-mitigation.
The CO2 concentration measurements reported for a number of mostly non-complaint European schools were near or above 1000 ppm (Figure 3). Two Swedish schools (Norback, 1995) had average concentrations of 1420 and 1850 ppm. Median CO2 concentrations were 1070 ppm (range 800–1600 ppm) in a study of 10 Swedish non-complaint schools, and 1100 ppm (range 875–2150 ppm) in 11 schools with higher prevalence of sick building syndrome (SBS) symptoms (Willers et al., 1996). Nielsen (1984) reports a measurement showing a CO2 range of 500–1500 ppm (average = 1000 ppm) in 11 Danish schools. Many of the European measurements were made with colorimetric indicator tubes over a very short time interval.
Potting et al. (1987) reported an epidemiological study involving 339 students in three Dutch complaint schools (14 classrooms) and four schools without teacher complaints (207 controls). All schools were constructed after 1980. Classroom CO2 levels in all of the schools exceeded the Dutch standard of 1200 ppm during 27–97% of the school time. One classroom had concentrations >2500 ppm CO2 73% of the time while levels were 1100 ppm in another room at the beginning of a school day.
Smedje et al. (1996, 1997) reported average and ranges of indoor CO2 concentrations for 96 classrooms in 38 Swedish schools randomly selected from a population of 130 schools; 61% of them had mechanical supply and exhaust air systems while the remainder had natural ventilation. Concentrations averaged 990 ppm CO2 for the 38 schools, but were above 1000 ppm for 41% of the measurements (maximum = 2800 ppm).
In general, CO2 measurements in schools suggest that a significant proportion of classrooms probably do not meet the ASHRAE Standard 62-1999 for minimum ventilation rate, at least part of the time. Furthermore, although the data are sparse, it appears that this situation may be more acute in portable classrooms. Ventilation rate measurements support this observation. No evidence suggests that elevated CO2 levels were restricted to complaint schools. However, there have not been any representative surveys of school classrooms to provide information on the distributions of CO2 concentrations or ventilation rates in schools on 9 statewide, regional, or national basis. Concentrations of a variety of pollutants emitted by the occupants and building materials and furnishings will be higher under these conditions than if the ASHRAE ventilation standard was met. Of particular concern is the potential for increased risks of contracting certain communicable respiratory illnesses, such as influenza and common colds in classrooms with low ventilation rates (Fisk, 2001).
The most commonly measured pollutants in schools were total volatile organic compounds (TVOC), formaldehyde (HCHO), and biological contaminants. The VOCs are suspected as one of the causes of SBS. Measured values of TVOC can vary significantly depending upon the sampling and analysis methods used (Hodgson, 1995). Particularly high TVOC concentrations, above 1–2 mg/m3, indicate the presence of strong VOC sources and/or low ventilation.
Very few measurements of TVOCs in schools are reported in the archival scientific literature. For the US, only three papers were found which reported TVOC measurements and all involved complaint schools. The TVOC concentrations in two south-eastern US schools with reported humidity and mold problems ranged from about 1 to 23 mg/m3 in one school and averaged 1.6 mg/m3 in another (Bayer and Downing, 1992). Black and Worthan (1995) reported average TVOC concentrations of 0.45 and 0.2 mg/m3 under unoccupied and occupied conditions, for a problem school in Washington State after mitigation. Casey et al. (1995) reported TVOC measurements made in two Las Vegas, Nevada elementary schools during the cooling season. The ventilation systems for the classrooms had been disabled for unknown reasons and the only means of ventilation was infiltration. The TVOC levels before the installation and operation of heat recovery ventilators (HRVs) ranged from 0.8 to 2.0 mg/m3. With the HRVs operating, concentrations of TVOC were reduced to 0.75 and 0.45 mg/m3 in the two classrooms.
Cavallo et al. (1993) reported TVOC concentrations for 10 non-complaint schools in Italy. The median concentration reported for the Italian nurseries and kindergartens was 3.6 mg/m3 and lower for primary and secondary schools (0.26 mg/m3), but the upper end of the range was very high, 13.6 mg/m3. The average TVOC for 10 French schools was 0.98 mg/m3 (Laurent et al., 1993). Norback (1995) reported the range of average TVOC concentrations from 36 classrooms in six Swedish primary schools to be quite low, 0.07–0.18 mg/m3. Median TVOC (excluding limonene) concentrations were 0.19 mg/m3 (range 0.10–0.23 mg/m3) in a study of 10 Swedish non-complaint schools, and 0.11 mg/m3 (range 0.07–0.21 mg/m3) in 11 schools with higher prevalence of SBS symptoms, while outdoor concentrations averaged about 0.09 mg/m3 (Willers et al., 1996). Mean indoor and outdoor kindergarten TVOC concentrations were 0.09 and 0.05 mg/m3, respectively.
Acute symptoms from HCHO exposures indoors have sometimes been found including eye, nose and throat irritation as well as lower airway and pulmonary effects (Samet et al., 1988). Acute HCHO toxicity IAQ guidelines for various settings range from 60 to 100 μg/m3 (0.055–0.08 ppm, OEHHA, 1999; WHO, 1987; CDNHW, 1987). The most stringent current HCHO reference exposure level (REL), based upon possible cancer effects, is 3 μg/m3 (0.002 ppm; OEHHA, 2000). A recent study suggests that HCHO exposures at levels below current guidelines may lead to an increased risk of allergic sensitization of children to common aeroallergens (Garrett et al., 1999).
Two journal articles and one EPA publication reported HCHO measurements in US schools. Black and Worthan (1995) reported measurements made in a complaint school after mitigation. Average concentrations in the school were 0.01 ppm before and during occupancy. Sheldon et al. (1989a, b) measured HCHO in several public buildings including a non-complaint primary school in Washington, DC, finding one sample with a trace of HCHO (0.012 ppm), while all other samples were below the limit of detection (0.01 ppm). Turk et al. (1987a) reported HCHO measurements for six non-complaint schools in the Pacific Northwest where 10-day average concentrations were generally below 0.05 ppm.
Average HCHO concentrations reported for 10 schools in Milan, Italy (Cavallo et al., 1993) and 10 schools in Paris, France (Laurent et al., 1993) were also generally at or near 0.05 ppm. However, some concentrations reported in both studies were above the HCHO irritancy threshold.
Olsen and Dossing (1982) reported measurements of HCHO made in 10 Danish daycare centers. Seven were located in mobile buildings and three were in permanent buildings. The average HCHO concentration for the mobile buildings was 0.35 ppm (range: 0.20–0.45 ppm), approximately five times higher than the average of 0.065 ppm for daycare centers in permanent buildings. Mucous membrane irritation of eyes, nose and throat were three times more frequent among the staff in the mobile buildings than the permanent buildings.
Because of the nature of HCHO as both an acute toxicological agent and as a potential human carcinogen, it is important to consider the above data from both perspectives. Concentrations acceptably low for prevention of acute irritation symptoms may not protect against potential long-term cancer risk. The California Air Resources Board advises that HCHO concentrations be as low as possible because of the potential cancer risk from repeated exposures (CARB, 1991).
The term ‘bioaerosol contaminants’ refers to a diverse variety of agents from biological sources found in indoor environments. These contaminants include: (1) viruses; (2) bacteria, including endotoxins from bacteria; (3) allergens, including house dust mite allergens [(Dermatophagoides pteronyssinus allergen I (Der p I) and D. farinae allergen I (Der f I)], and allergens from animal dander [e.g. Felis dosmeticus allergen I (Fel d I)]; and (4) fungi which may contain allergens, toxins, and irritants.
There is evidence that low ventilation rates and other building characteristics can lead to increased incidence of respiratory diseases caused by viruses (Brundage et al., 1988; Fisk, 2001). No references were found for airborne viral measurements in schools, but total airborne bacteria have been reported in a number of studies. Bacterial endotoxins, present in house dust and airborne particulate matter are thought to cause a range of flu-like symptoms (Rylander et al., 1989; 1992), but no references to endotoxin measurements in schools were found.
Exposure to house dust mite allergens can cause asthma and trigger asthma attacks in sensitized subjects (Samet et al., 1988). House dust mites thrive under conditions of high relative humidities and allergies to them are more frequent in climates with mild humid winters (Reed and Swanson, 1986). Cat and dog allergens found in house dust cause symptoms in many allergic subjects, and can be shed from contaminated clothing in classrooms (Dybendal and Elsayed, 1989; Munir et al., 1993) causing symptoms in sensitized asthmatic children.
Exposures to mold spores in indoor air can also cause allergic reactions in sensitized subjects, with symptoms such as runny nose, watery eyes, cough, sneezing, and fevers. Water damage in a building often leads to the growth of molds and to airborne exposures to mold spores from genera such as Aspergillus, Alternaria, and Cladosporium. Water damage to buildings was the second most commonly reported building-related problem associated with indoor air problems in the NIOSH HHERs (see Daisey and Angell, 1998).
However, as discussed in Daisey and Angell (1998), NIOSH generally does not routinely recommend airborne bioaerosol monitoring as lack of findings does not rule out harmful exposures, while visible microbial growth on interior building surfaces usually serves as clear evidence of a potential biological problem. The guidelines published by the American Conference of Governmental Industrial Hygienists’ Committee on Bioaerosols share this interpretation; ‘One should use air sampling as a last resort. Air sampling rarely provides proof of inappropriate exposure to bioaerosols’ (ACGIH, 1995). Thus, given physical evidence, quantification of biological contamination can often be skipped in favor of remediation.
Morey (1984) suggested that concentrations above 1000 CFU/m3 indicate possible microbial contamination warranting further investigation. However, in California, a warmer climate, an average of 1400 CFU/m3 was reported for total bacteria in outdoor air (Gallup et al., 1993).
When identifications were made, the most commonly observed bacteria in the literature, were Micrococcus and Bacillus species and pigmented gram-negative rods such as Flavobacterium sp., and coryneforms. Maroni et al. (1993) reported finding principally species Staphylococcus (85% of samples), Micrococcus (72% of samples) and Difteroides (70% of samples) in Italian classrooms. Mouilleseux et al. (1993) reported finding Staphylococcus aurus (33%), Enterobacteria including Escherichia coli (6%); Streptococcus D (50.6%). Gallup et al. (1993) noted that increased counts of ‘normal’ bacteria were observed with increased dust levels, activity, and occupancy.
Concentrations of more than 2000 ng Der p I/g of dust may represent a risk for development of specific immunoglobulin E (IgE) to house dust mite allergen in genetically predisposed individuals (Verhoeff et al., 1994). Concentrations above 10,000 ng/g dust of cat or dog allergen are sufficient to cause sensitization and associated risk of asthma in exposed children (Platts-Mills et al., 1995).
Bates and Mahaffy (1996) reported measurements of allergens in carpet dusts collected from seven complaint and six non-complaint classrooms in six Florida schools before and after cleaning. All classrooms had level loop pile carpeting. The Der p I and Der f I were measured and the sum of both reported; Der p I was reported as the dominant species in all carpet dust samples. Before cleaning, five of the classrooms had levels of house dust mite allergen plus cat allergen above 2000 ng/g dust and two had levels above 9000 ng/g. The complaint room average Der p I and Der f I loadings were 5000±5000 ng/g dust and the non-complaint rooms were 210±210 ng/g dust. Cleaning substantially reduced the levels.
Floor dust in 60 classrooms in 10 Norwegian schools was analyzed for Fel d I, Der p I and Der f I. The Fel d I was detected in all classrooms and ranged from 40 to 1100 ng/g dust (Dybendal and Elsayed, 1992). On average, Fel d I loadings were 11 times higher in carpeted areas compared with smooth floors. The Der p I and Der f I loadings were very low. A significantly higher content of allergens per gram of dust was also found for carpeted than smooth floors, as measured by basophil histamine release.
Dust samples from furniture and floors in 29 classrooms in four Swedish schools were assayed for Fel d I and Canis familiaris dog allergen, Can f I (Munir et al., 1993). The Fel d I concentrations in chair, table, and floor samples were 1000, 500, and 100 ng/g dust, respectively. The Can f I loadings were higher than Fel d I in the chair and the floor samples. The authors concluded these two major allergens were potentially at levels sufficient to sensitize children and to induce asthma in most children who are allergic to cats or dogs. Cat and dog allergens in fine dust samples from 96 classrooms in 38 randomly selected Swedish schools averaged 132 ng/g while dog allergen averaged 625 ng/g with a maximum of 3900 ng/g dust (Smedje et al., 1996).
The range of measured allergens in dust presented in the four above-mentioned studies varied and was dependent on the specific allergen and the condition of the classrooms. Clearly, the floor surface type and level of cleaning were important factors in maintaining low allergen levels. Carpeted floors contained a significantly higher content of allergens per gram of dust and cleaning reduced the levels of mite allergen.
Rao et al. (1996) recently found that existing quantitative standards and guidelines for total fungi in indoor air range from < 100 CFU/m3 to >1000 CFU/m3 as the upper limit for non-contaminated indoor environments, based primarily on baseline data rather than health effects information. Limitations in the standards and guidelines include reliance on short-term grab samples analyzed only by culture, lack of standardized protocols for data collection, analysis and interpretation, and the lack of connection to human dose–response data. In addition, as the toxin concentration in spores is most likely independent of viability, measurements of culturable fungi may not adequately reflect the potential for health problems.
Average and maximum total viable molds measured in 96 classrooms in 38 randomly selected Swedish schools were 500 and 4500 CFU/m3, respectively (Smedje et al., 1996, 1997). Gravesen et al. (1986) measured viable molds in dusts from 36 carpeted rooms and 13 non-carpeted rooms in 21 Danish schools. Significantly greater (P=0.002) mold colony counts were found in the carpet dust (∼1900 CFU/g dust) than the bare floors (∼950 CFU/g dust). The most prevalent microfungal genera were Penicillium, Fusarium, Alternaria, and Cladosporium.
Relationships between health symptoms, ventilation and other indoor environmental factors in schools
As of 1999, only two studies, both European, have investigated the relationships between symptom prevalences and ventilation rate or CO2 concentrations in schools. Myhrvold et al. (1996) studied 22 classrooms in five Norwegian schools renovated with the objective of improving IAQ. Pre- and post-renovation measurements were made, including health symptom questionnaires and performance tests administered to 550 students, and measurements of CO2 concentrations. These investigators found a statistically significant partial correlation (one-way ANOVA, P<0.001) between symptoms of headaches, dizziness, heavy headed, tiredness, difficulties concentrating, unpleasant odor, and high CO2 concentrations (1500–4000 ppm compared with concentrations below 1500 ppm). Health symptoms characterized as ‘irritations of the upper airways’ were also higher at higher CO2 concentrations (P=0.024). Reduced performance on the Swedish Performance Evaluation System test was also observed at higher concentrations of CO2.
On the other hand, an epidemiological study in three complaint and four non-complaint Dutch schools (14 classrooms total) assessed relationships between SBS symptom complaints of children and CO2 levels and indoor climate (Potting et al., 1987). The complaint of ‘bad odor of the air’ was associated with high CO2 levels.
The results of these two available studies in schools were inconsistent, as might be expected because ventilation rate and CO2 concentrations are only surrogates for the actual agents that might be causing the symptoms. Other study limitations include inadequate characterization of indoor ventilation rates, CO2 and indoor contaminant levels, and health outcome, as well as small sample sizes and inadequate control for confounding. A comprehensive review is available, however, on relations between ventilation rates and occupant health in 20 studies, mostly among adults in office and other work settings. This review found consistent relations between ventilation rates below 10 l/s per person ventilation rates and increased symptoms among occupants (Seppänen et al., 1999). Ventilation rates increased above 10 l/s per person, even up to 20 or 30 l/s per person, were associated in some, but not all, studies, with further significant reductions in occupant symptoms. Findings of studies using CO2 measurements to approximate ventilation rates generally agreed, but not as consistently. Corroborating the Seppänen et al. (1999) review conclusions, analysis of a large data set on adults in office buildings found statistically significant, dose-dependent, increases of up to a factor of six in the risk of building-related lower respiratory and mucous membrane irritation symptoms when average workday indoor CO2 concentrations increased by 420 ppm above outdoor levels, concentrations still below the ASHRAE 62-1999 standard of 1000 ppm (Apte et al., 2000). Although the office environment differs from school environments, similar exposure and occupant health response mechanisms are likely to occur.
Several studies have assessed relationships of various health outcomes among students with indoor environmental factors in schools. In a study of 579 asthmatic Danish children, Hansen et al. (1987) reported an increased severity of asthma in schools with carpet compared with those with no carpet. This association was especially strong and statistically significant (P=0.02) for the children who had no carpet in their rooms at home and had no pets.
Norback and Torgen (1987) compared 59 staff member questionnaire responses (94% response rate) in two Swedish schools with wall-to-wall carpeting against 133 from four schools without carpeting. A questionnaire was administered (n = 141) in 1982 and then again in 1986 after carpeting was removed. Results of the questionnaire for 1982 (Table 1) showed significantly higher frequency of health complaints in carpeted classrooms (P≤0.03). Four years later, 37 of the 59 staff in the two schools that had carpet removed and 81 of the staff in the four schools without carpeting were resurveyed. Some health complaints remained significantly higher among those that previously had carpeting (P≤0.02).
Table 1. Symptom frequenciesa among school personnel with wall-to-wall carpet in their classrooms in comparison with school personnel with hard plastic floor coverings, in 1982b
* Statistically significant differences (P≤0.001) between those carpeted and those with hard floor coverings in 1982.
Dryness in the throat
Smarting of the throat
Sensation of getting a cold
Koskinen et al. (1997) compared respiratory symptoms and infections in children (3–7-year-old) in two daycare centers with visible mold growth on interior walls (exposed children) with those in two reference daycare centers (non-exposed children). Parents recorded their children's (n = 229) health symptom status in diary questionnaires during two study periods. During the first period, the children in the two daycare centers with mold problems (exposed) had a significantly increased risk of sore throat, purulent and non-purulent nasal discharge, nasal congestion, hoarseness and common cold than those in the two reference daycare centers (non-exposed). During the second follow-up period, a significantly increased risk of purulent nasal discharge, nasal congestion, hoarseness and cough was observed for the exposed populations compared with the unexposed. Overall morbidity for respiratory symptoms and common cold were higher in the daycare centers with the mold than in the two reference daycare centers. This study was consistent with the results of an earlier comparative study of two daycare centers, one with and one without mold problems (Koskinen et al., 1995). In this earlier study, absenteeism in the mold-exposed daycare center was almost double that in the non-exposed daycare center.
Relationships between health symptoms and measured exposures to environmental pollutants in schools
Most studies of health symptoms and pollutant exposures in classrooms have used surrogates of exposure (e.g. presence of molds on walls), have measured a single pollutant, or have assumed that whatever mitigation measures taken were effective in reducing or eliminating symptoms. We found only three epidemiological studies in schools in which multivariate regression analyses were used to more rigorously examine relationships between health symptoms and measured exposures to more than one pollutant. Table 2 summarizes key features of these studies.
Table 2. School studies in which multiple regression analysis was used to investigate relations between health symptoms and pollutant exposures (statistically significant associations are shown in bold italicized print
Type of study (reference)
Pollutant exposures measured
a Formaldehyde concentrations all low.
b VOCs = sum of concentrations of 15 VOCs, as well as subsets of these: aromatics, alkanes, terpenes, and butanols.
c RSP = respirable dust in air.
d 2-Methyl-isoborneol, 3-methylfuran, 2-heptanone, 1-octen-3-ol.
11 Swedish secondary schools, 28 classrooms, 627 students
Formaldehydea, sum of 14 VOCs, NO2, RSP, total bacteria and viable bacteria, total and viable molds, endotoxin in settled dust, cat and dog allergens in settled dust
In a longitudinal study on the effects of removal of wall-to-wall carpeting, Norback et al. (1990) reported on relationships between prevalences of SBS symptoms among personnel in six primary schools in Sweden, indoor exposures and personal factors. Chronic SBS symptoms (airway irritation or congestion; headache, tiredness, sensation of getting a cold, nausea; and eye irritation/swollen eyelids) reported in both 1982 and in 1986 were related to VOC concentrations, previous occupancy in a classroom with wall-to-wall carpeting, hyper-reactivity, and psychosocial factors. The incidence of new SBS symptoms (only eye irritation/swollen eyelids) reported in 1986 but not in 1982, was related to the concentration of respirable dust, current smoking, and the psychosocial climate.
In a large study of asthma symptoms in 1410 school employees in 38 Swedish schools, Smedje et al. (1996) found no statistically significant relationships (at the 95% confidence level) between asthma and many commonly measured environmental factors, e.g. CO2, air exchange rates, humidity. However higher concentrations of molds and of four microbial VOCs were significantly related to asthma in the 1410 school employees, even after controlling for other factors, i.e. allergies, stressful work situation, and recent repainting of homes. More recently, Smedje et al. (1997) reported statistically significant relationships between current asthma in secondary school pupils and school exposures to HCHO, VOCs (sum of 14 compounds, 1-week sample), viable bacteria (in air), viable molds (in air) and cat allergen in settled dust. Evidence of a dose–response relationship with these variables was also reported.
Summary and Conclusions
The available measurements of ventilation rates and CO2 concentrations in schools suggest that, based upon the current ASHRAE ventilation standard, many classrooms are not adequately ventilated. Although, results from the few studies in schools have been inconsistent in associating ventilation rates or CO2 concentrations and symptoms, a broad literature review for indoor environments more generally suggests a consistent relationship (Seppänen et al., 1999). These findings, mostly in adults, would apply to school children with two reasonable assumptions: that exposures in schools related to ventilation rates are similar to those in offices, and that children would be at least as sensitive as adults to these exposures. The findings of Seppänen et al. (1999), together with the data on ventilation inadequacy in current schools, strongly suggest a widespread environmental inadequacy in schools likely to be related to increased symptoms in schoolchildren. As the first line of defense against poor IAQ in classrooms is adequate ventilation, this should be a major focus of design or remediation efforts.
The pollutants most commonly measured in schools were TVOC, HCHO and microbiological contaminants. In most cases, health symptoms were not measured in these studies. The majority of the HCHO measurements, particularly more recent measurements, were below 0.05 ppm. Although HCHO levels were generally low, recent research suggests that even low levels may lead to an increased risk of sensitization to allergens. Furthermore, HCHO is listed as a probable human carcinogen; therefore, HCHO levels in schools should be kept very low. The most commonly measured microbiological contaminants measured in schools were allergens in deposited dust (e.g. house dust mite allergen), fungi, and bacteria. Levels of specific allergens in deposited dust were often high enough to cause allergy symptoms in allergic occupants. Fungi have been measured in air and observed growing on surfaces. However, air measurements were generally low and are not recommended because of limitations of sampling and analyses methods. Bacteria have also been measured in some schools but were not generally speciated. Without speciation of bacteria such measurements are of little use as many species are relatively harmless. Lack of speciation also limits our ability to infer whether the bacteria may be the cause of health symptoms.
Indoor environmental quality (IEQ) related health symptom studies were rarely conducted up to 1999 when this review ends. It is likely that more studies in this important area will be conducted in time. Asthma and SBS were the most commonly reported health symptoms investigated in schools. The few studies in which exposure and symptoms were simultaneously investigated suggest that exposures to VOCs, molds and microbial VOCs, and allergens generally measured in classroom floor dust, are related to asthma, SBS and other respiratory symptoms. There is some indication in the literature that carpets in the classroom are a causal factor for health symptoms. The particular pollutants causing symptoms may differ among schools.
This review shows that the state of knowledge regarding IAQ in schools is very limited. With the possible exception of the early NIOSH investigations not reported in the peer-reviewed literature, there has been no consistent approach to evaluations of IAQ and health outcomes in schools. Many of the existing studies lack the rigor and quality necessary to adequately address the problem. In addition, although there is some effort to identify the IAQ problems in schools, there are no programs currently in place in the US at the national or state level to improve the indoor environmental quality in schools.
More studies are needed in which relations between symptoms and measured exposures to multiple specific pollutants are investigated. Furthermore, quantitative information is needed on exposure-health response relationships for specific pollutants suspected to cause health symptoms, in order to provide a sound basis for setting standards for schools and for insuring cost-effective mitigation measures. Improved methods for exposure measurements, particularly those that provide more speciation of fungi and bacteria and longer sampling times are needed. Finally, although there is evidence that many schools are not adequately ventilated, the extent of the problem is not known. Careful and thorough measurements of ventilation rates and/or CO2 levels in a representative sample of schools would provide much needed information on the fraction of schools with this problem.
In conclusion, although more studies are needed to determine the extent of IAQ problems in schools, evidence shows that ventilation rates in new and existing schools often do not meet the minimum ASHRAE guidelines, and this may be related to significant increases in symptoms among children and teachers in schools. It is clear that programs should be put in place to ensure that all schools provide necessary ventilation.
This research was supported by the California Environmental Protection Agency, Office of Environmental Health Hazard Assessments and by the Office of Energy Efficiency and Renewable Energy, Office of Building Technology, State and Community Programs, US Department of Energy under Contract No. DE-AC03-76SF00098. We would like to thank William Fisk, Al Hodgson, and Mark Mendell for their careful reviews of this manuscript.
We reviewed the literature on Indoor Air Quality (IAQ), ventilation, and building-related health problems in schools and identified commonly reported building-related health symptoms involving schools until 1999. We collected existing data on ventilation rates, carbon dioxide (CO2) concentrations and symptom-relevant indoor air contaminants, and evaluated information on causal relationships between pollutant exposures and health symptoms. Reported ventilation and CO2 data strongly indicate that ventilation is inadequate in many classrooms, possibly leading to health symptoms. Adequate ventilation should be a major focus of design or remediation efforts. Total volatile organic compounds, formaldehyde (HCHO) and microbiological contaminants are reported. Low HCHO concentrations were unlikely to cause acute irritant symptoms (<0.05 ppm), but possibly increased risks for allergen sensitivities, chronic irritation, and cancer. Reported microbiological contaminants included allergens in deposited dust, fungi, and bacteria. Levels of specific allergens were sufficient to cause symptoms in allergic occupants. Measurements of airborne bacteria and airborne and surface fungal spores were reported in schoolrooms. Asthma and ‘sick building syndrome’ symptoms are commonly reported. The few studies investigating causal relationships between health symptoms and exposures to specific pollutants suggest that such symptoms in schools are related to exposures to volatile organic compounds (VOCs), molds and microbial VOCs, and allergens.