### 682 volume 119 | number 5 | May 2011 • Environmental Health Perspectives 

# Research

Declining or comparatively low cognitive function in older adults is associated with loss of independence in activities of daily living (Greiner et al. 1996; McGuire et al. 2006), nursing home admission (Gaugler et al. 2007; Joray et al. 2004), hospitalization (Chodosh

et al. 2004), and mortality (Bassuk et al. 2000; Nguyen et al. 2003). The burden associated with deficits in cognitive function is expected to grow as the global population ages (Ferri

et al. 2005), but few interventions to prevent, delay, or halt the progression of cognitive decline are currently available. The potential relationship between exposure to common environmental toxicants and cognition in older adults has received relatively little con

sideration compared with non environmental risk factors, despite evidence that many toxi

cants may be neurotoxic and the modifiable nature of many environmental exposures. Air pollution may exert adverse effects on central nervous system (CNS) function. Inautopsy studies of dogs and people, CalderónGarcidueñas et al. ( 2002

, 2003

, 2004

, 2008b) found evidence of increased levels of inflam

matory mediators, β -amyloid deposition, and markers of oxidative damage to DNA, as well as evidence of blood

– brain barrier disruption

, in the brains of those from a city with high lev

els of air pollution compared with those from a city with low levels. Children and dogs residing in a highly polluted city were also more likely to exhibit white matter hyperintensities in the prefrontal cortex than were those residing in a city with lower levels (Calderón-Garcidueñas

et al. 2008a). Although this ecological evidence is insufficient to conclude that air pollution is the causal agent, other lines of evidence sup

port this claim. In animal studies, exposure to ozone has been linked to neuroinflammation, lipid peroxidation, and memory deficits (Blockand Calderón-Garcidueñas 2009; DoradoMartinez et al. 2001), effects that may be medi

ated by the induction of systemic inflammation. Controlled animal experiments demon strate that ultrafine particulate matter (PM) , a com

ponent of traffic-related air pollution, can translocate to the brain via the olfactory nerve or systemic circulation (Elder et al. 2006; Oberdörster et al. 2004; Peters et al. 2006), where it may promote CNS dysfunction. In animal studies, exposure to fine or ultrafine PM has been associated with CNS inflamma

tion and lipid peroxidation (Campbell et al. 2005; Kleinman et al. 2008; Zanchi et al. 2008), neuronal degeneration (Veronesi et al. 2005), and behavioral changes (Zanchi et al. 2008). Alternately, the cardiovascular effects of air pollution (Brook 2007; Pope and Dockery 2006) may lead to CNS dysfunction through promotion of vascular brain pathology. One potential manifestation of CNS dys

function in older adults is cognitive impair

ment. We hypothesized that exposure to black carbon (BC), a marker of traffic-related air pollution, would be associated with cog

nitive function in a cohort of older men, because traffic-related air pollution is a major source of exposure to ultrafine PM , which may induce CNS dysfunction.



### Materials and Methods Study sample. We drew the study sample from participants of the U.S. Department of Veterans Affairs (VA) Normative Aging Study (NAS), an ongoing longitudinal cohort study of men established in 1963 (Bell et al. 1972). Participants in the NAS are invited to undergo an in-person examination every 3 years. In addition to a physical examina

tion and laboratory tests, participants provide information on medical history, lifestyle, and demographic factors at each study visit and, starting in 1993, have been asked to complete a battery of cognitive tests. At each visit, par

ticipants provided written informed consent as approved by the VA Boston Healthcare System Institutional Review Board (IRB).

Address correspondence to M.C. Power, Harvard School of Public Health, EOME, Landmark Center, 3rd Floor East, P.O. Box 15697, Boston, MA 02215 USA. Telephone: (617) 721-9984. Fax: (617) 384- 8994. E-mail: mcpower@hsph.harvard.edu

Supplemental Material is available online (doi:10. 1289/ehp.1002767 via http://dx.doi.org/).

We thank S. Melly for his help creating Figure 1 and J. Weuve for her contribution to the develop

ment of this work.

M.C.P. is supported by a grant from the National Institute of Environmental Health Sciences (NIEHS; T32 ES007069). This study was supported by a grant from the U.S. Environmental Protection Agency (RD832416 and RD83479801) and by grants from the NIEHS (ES00002, ES015172, ES014663, ES005257, ES012044, and P01 ES009825). The Cognition and Health in Aging Men Project is supported by the Clinical Science Research and Development Service, U.S. Department of Veterans Affairs, the National Institutes of Health (grants R01-AG14345, R01- AG18436, 5-P42-ES05947, and R01-ES05257), the U.S. Department of Agriculture, Agricultural Research Service (contract 53-K06-510), and Veterans Affairs Merit Review and Research Career Scientist awards to A.S. The Veterans Affairs Normative Aging Study is supported by the Cooperative Studies Program/ Epidemiology Research and Information Center, U.S. Department of Veterans Affairs.

The views expressed in this article are those of the authors and do not necessarily represent the views of the U.S. Department of Veterans Affairs.

The authors declare they have no actual or potential competing financial interests.

Received 22 July 2010; accepted 20 December
2010. 

## Traffic-Related Air Pollution and Cognitive Function in a Cohort of Older Men

Melinda C. Power, 1,2 Marc G. Weisskopf, 1,2 Stacey E. Alexeeff, 1 Brent A. Coull, 3 Avron Spiro III, 4,5 and Joel Schwartz 1,2

1 Department of Environmental Health, 2 Department of Epidemiology, and 3 Department of Biostatistics, Harvard School of Public Health, Boston, Massachusetts, USA; 4 Veterans Affairs Boston Healthcare System, Boston, Massachusetts, USA; 5 Department of Epidemiology, Boston University School of Public Health, Boston, Massachusetts, USA

B ackground : Traffic-related particles induce oxidative stress and may exert adverse effects on central nervous system function, which could manifest as cognitive impairment.

O b jective : We assessed the association between black carbon (BC), a marker of traffic-related air pollution, and cognition in older men.

M ethods : A total of 680 men (mean ± SD, 71 ± 7 years of age ) from the U.S. Department of Veterans Affairs Normative Aging Study completed a battery of seven cognitive tests at least once between 1996 and 2007. We assessed long-term exposure to traffic-related air pollution using a vali

dated spatiotemporal land-use regression model for BC.

R

esults : The association between BC and cognition was non linear

, and we log-transformed BC estimates for all analyses [ ln(BC) ] . In a multivariable-adjusted model, for each doubling in BC on the natural scale, the odds of having a Mini-Mental State Examination ( MMSE ) score ≤ 25 was 1.3 times higher [ 95% confidence interval (CI)

, 1.1 to 1.6 ] . In a multivariable-adjusted model for global cognitive function, which combined scores from the remaining six tests, a doubling of BC was associated with a 0.054 SD lower test score (95% CI
, –0.103 to –0.006), an effect size similar to that observed with a difference in age of 1.9 years in our data. We found no evidence of heteroge

neity by cognitive test. In sensitivity analyses adjusting for past lead exposure, the association with MMSE scores was similar ( odds ratio = 1.3 ; 95% CI
, 1.1 to 1.7)

, but the association with global cognition was somewhat attenuated (–0.038 per doubling in BC ; 95% CI
, –0.089 to 0.012).

C onclusions : Ambient traffic-related air pollution was associated with decreased cognitive func

tion in older men.

K

ey words : aging, black carbon, cognitive dysfunction, epidemiology, particulate matter. Environ Health Perspect 119:682–687 (2011). doi:10.1289/ehp.1002767 [Online 20 December 2010]Traffic-related air pollution and cognition

Environmental Health Perspectives • volume 119 | number 5 | May 2011 

### 683 This study has been approved by the IRBs of the participating institutions. We limited the study sample to partici

pants of the NAS who completed cognitive testing between 1996 and 2007 and who lived within the range of our BC exposure model. These constraints ensured that both cogni

tive test data and an estimate of BC exposure before cognitive assessment were available for each study participant. We also excluded par

ticipants if they experienced a stroke before study start. In addition, we restricted the pres

ent study population to those self-reporting white race/ethnicity. Exposure assessment. Estimates of BC exposure at the residence of each partici

pant were used as a surrogate for individual exposure to traffic-related air pollution. We estimated BC exposures using a validated spatio temporal land-use regression model that, starting in 1995, provides daily estimates of BC concentrations throughout the greater Boston, Massachusetts, area, which roughly includes the area within Interstate 495; details of this model have been published previously (Gryparis et al. 2007). Briefly, daily aver

age BC estimates from 83 monitoring sites were used to develop a BC prediction model. Predictors in the final model include infor

mation on meteorological conditions (e.g.

, wind speed), land use (e.g.

, traffic density), daily BC concentrations at a central monitor, and other descriptors (e.g.

, day of the week). Based on the training set, the model R 2 was 0.83, whereas the average correlation between predicted values and observed BC levels in four out-of-sample validation samples was 0.59. For the present study, addresses with predicted daily BC concentrations outside the range of the exposure measurements from the training set were excluded. To create a metric of long-term exposure, we took the average of the 365 daily estimate at the participant’s residential address prior to the date of the first cognitive assessment completed on or after 1 January 1996, the first date for which compu

tation of a prior 1- year average was possible. Cognitive testing. Since the onset of cog

nitive testing, the cognitive battery has been revised, reflecting both the addition and sub

traction of individual cognitive tests. Seven cognitive tests have been administered with relative consistency across the span of cogni

tive testing and were considered in this study : the Mini-Mental State Examination (MMSE), the digit span backward test, a verbal fluency task, constructional praxis, immediate recall of a 10-word list, delayed recall of a 10-word list, and a pattern comparison task. The MMSE assesses multiple cognitive domains and is widely used as a dementia screen

ing and research instrument (Tombaugh and McIntyre 1992) ; the six additional tests assess a variety of domains, including attention, memory, executive function, lan

guage, and visuomotor ability. All cognitive tests were drawn from established cognitive test batteries, including the Consortium to Establish a Registry for Alzheimer Disease (CERAD) battery (Morris et al. 1989), the Wechsler Adult Intelligence Scales for Adults, Revised (WAIS-R) (Wechsler 1981), the Neurobehavioral Evaluation System 2 (Letz 1991), and the Developmental Test of Visual-Motor Integration (Beery and Buktenica 1967). The present study includes cognitive data from study visits from 1996 to 2007. Therefore, the baseline visit for each study participant is defined as the first cognitive assessment completed on or after 1 January 1996. This restriction ensures that we have an estimate of BC exposure obtained before the cognitive test data used in our analyses. Most study participants have completed multiple waves of cognitive testing, and all available cognitive data obtained between 1996 and 2007 were used in analyses. Statistical analysis. Because we observed a ceiling effect for MMSE scores, with many men achieving the maximum score, we created a dichotomous variable for infe

rior MMSE performance for use in analyses. MMSE scores are commonly used to screen for dementia (Tombaugh and McIntyre 1992), but few men in our cohort exhibited scores that would typically trigger further evaluation (< 24). We therefore chose to label

scores ≤ 25 as “low” MMSE scores (18% of our observations). Cognitive test scores for the remaining six tests were z -transformed based on the mean and standard deviation of the individual test scores at baseline and were considered as continuous variables in analyses, with positive z -scores indicating better perfor

mance for all tests. We evaluated the association between BC and the odds of having a low MMSE score using logistic regression with generalized esti

mating equations and empirical variance esti

mates to account for repeat measures across individuals. For the remaining six tests, which yield seven unique scores (the pattern com

parison task produces two unique scores), we treated each cognitive test score as a repeat measure of global cognitive function in a ran

dom effects linear mixed model. This model included a random intercept for individual to account for repeat measures within individu

als and a random intercept for cognitive test score to account for use of seven different cognitive test score types as repeat measures of global cognitive function. This analysis pro

vides one hypothesis test for the association between BC and global cognitive function. We evaluated the presence of heterogeneity of BC effect across cognitive test score type by adding and testing the significance of a random slope for BC effect by cognitive test score type. If the slope were to be significant, this would indicate that the BC effect is dis

similar across cognitive test score types and the global analyses would be inappropriate. Final models were multivariable adjusted for potential confounders or predictors of cog

nitive function that are not plausible inter

mediates for a BC

– cognition relationship. We obtained data on these covariates from information collected at each NAS study visit. Final multivariable-adjusted models were adjusted for age at cognitive assessment as well as information on several variables at baseline: education (< 12, 12–16, > 16 years), alcohol intake (< 2 drinks/day, ≥ 2 drinks / day), physi

cal activity [ < 12, 12 to < 30, ≥ 30 metabolic equivalent hours (MET-hr) per week ] , diabe

tes (yes/no), dark fish consumption ( less than once a week, equal to or greater than once a week), computer experience (yes/no), first language (English/not English), percentage of the participant’s census tract that is non white,
percentage of the adult residents in the par

ticipant’s census tract with at least a college degree, an indicator for whether the cognitive data were from the participant’s first cogni

tive assessment (yes/no), and an indicator for whether the participant was a part-time resi

dent of the greater Boston area (yes/no). We excluded data from study visits for which we lacked covariate information from all analyses (1.4% of study visits). We log-transformed BC estimates for use in all analyses after examination of restricted cubic splines indicated a log-linear relation

ship. We additionally explored interactions between BC and body mass index (BMI), hypertension, smoking status, and diabetes using multiplicative interaction terms and conducted sensitivity analyses further adjust

ing our multivariable models for smoking and BMI. We used R ( version 2.10.1; R Development Core Team 2010) to examine splines and SAS ( version 9.2 ; SAS Institute Inc., Cary

, NC) for all other analyses. Sensitivity analyses: potential confounding by lead. Exposure to lead may confound the relationship between BC and cognitive func

tion. Traffic-related exposures were a primary source of lead exposure in the era of leaded gasoline, and it is reasonable to expect that men with high current traffic-related air pol

lution exposures had high past traffic-related lead exposures. In addition, cumulative past lead exposure may have an adverse impact on cognitive function in older adults (Shih et al. 2006), even at low levels (Weisskopf et al. 2007; Wright et al. 2003). Thus, we conducted sensitivity analyses to determine the influence of potential confounding by exposure to lead. Tibia bone lead concentrations, a bio

marker for cumulative past lead expo

sures (Hu et al. 1998), were available forPower et al.



### 684 volume 119 | number 5 | May 2011 • Environmental Health Perspectives 363 participants (53.4%). Tibia bone lead concentrations were imputed for 299 partici

pants (44.0%) using a published prediction model developed in the NAS (reduced model) (Park et al. 2009). Missing data precluded imputation of bone lead concentrations for 18 participants (2.6%), and we excluded these participants from the sensitivity analyses. To test the sensitivity of our results to potential confounding by exposure to lead, we repeated the analyses described above additionally adjusting for bone lead concentration and imputation status (yes/no). 

### Results
A total of 680 men met the inclusion criteria for this study. Within this group, the number of men completing at least one wave of cogni

tive testing varied across the cognitive tests: MMSE ( n = 671 ), digit span backward test ( n = 663 ), verbal fluency task ( n = 670 ), con

structional praxis ( n = 626 ), immediate recall of a 10-word list ( n = 669 ), delayed recall of a 10-word list ( n = 667 ), and pattern compari

son task ( n = 645 )

. Table 1 summarizes the baseline charac

teristics of the cohort. The mean ± SD age of the study sample at baseline was 71 ± 7 years (range

, 51–97 years ), and most men had at least some college or graduate-level educa

tion (70.1%). On average, study participants completed 2.14 cognitive assessments (range

, 1–5). On the natural scale, 1-year average BC exposure estimates ranged from 0.03 to 1.77 μ g/m 3 ( m ean ± SD, 0.58 ± 0.28 μ g/m 3 ) and exhibited a skewed distribution. Figure 1 illustrates the substantial spatial variability of BC over the study area in the year 1995. Because the association between cogni

tive test scores and BC exposure estimates appeared log-linear, we log-transformed BC for use in all analyses and report associations for a doubling in BC concentration on the natural scale, or approximately a 0.69 unit change in ln(BC). BC exposure was signifi

cantly associated with the risk of having a low MMSE score [ multivariable-adjusted odds ratio (OR) = 1.3 for a doubling in BC
concentration ; 95% confidence interval (CI)

, 1.1–1.6; Table 2 ] . In the analysis of **Table 1.** Baseline characteristics of the cohort ( n = 680)

.

Characteristic n (%) BC concntration (mean ± SD) Age (years) 50–59 48 (7.1) 0.550 ± 0.288 60–69 284 (41.8) 0.574 ± 0.277 70–79 273 (40.1) 0.583 ± 0.267 80–89 72 (10.6) 0.605 ± 0.333 90–99 3 (0.4) 0.466 ± 0.285 Education (years)

< 12 203 (29.9) 0.629 ± 0.304 12–16 338 (49.7) 0.572 ± 0.276

> 16 139 (20.4) 0.521 ± 0.239 First language English 585 (86.0) 0.578 ± 0.282 Not English/bilingual 95 (14.0) 0.581 ± 0.266 Computer experience Yes 277 (40.7) 0.542 ± 0.255 No 403 (59.3) 0.604 ± 0.294 Physical activity (MET

- hr/week)

< 12 385 (56.6) 0.574 ± 0.286 12 to < 30 178 (26.2) 0.602 ± 0.293

≥ 30 117 (17.2) 0.558 ± 0.237 Alcohol (drinks/day)

≥ 2 166 (24.4) 0.573 ± 0.242

< 2 514 (75.6) 0.581 ± 0.291 Diabetes Yes 106 (15.6) 0.567 ± 0.254 No 574 (84.4) 0.581 ± 0.285 Consumed dark fish (times/week)

≥ 1 100 (14.7) 0.566 ± 0.283

< 1 580 (85.3) 0.581 ± 0.280 Nonwhite (% of census tract)

< 5% 268 (39.4) 0.521 ± 0.298 5 to < 10% 188 (27.6) 0.541 ± 0.249

≥ 10% 224 (32.9) 0.679 ± 0.255

≥ 25 years of age with at least a college degree (% of census tract)

< 30% 214 (31.5) 0.626 ± 0.301 30 to < 50% 281 (41.3) 0.540 ± 0.277

≥ 50% 185 (27.2) 0.583 ± 0.250 Smoking Never 192 (28.2) 0.557 ± 0.255 Former 453 (66.6) 0.584 ± 0.294 Current 35 (5.1) 0.634 ± 0.208 BMI (kg/m 2 )

< 25 152 (22.4) 0.587 ± 0.262

≥ 25 528 (77.6) 0.576 ± 0.285 Hypertension Yes 454 (66.8) 0.587 ± 0.288 No 226 (33.2) 0.562 ± 0.264 Tibia bone lead Measured 363 (53.4) 0.599 ± 0.286 Imputed 299 (44.0) 0.559 ± 0.271 Missing 18 (2.6) 0.507 ± 0.289 **Figure 1**

**.** Predicted 1-year average BC exposures (μg/m 3 ) for the greater Boston area in 1995

. 0.02–0.07
0.08–0.19
0.20–0.28
0.29–0.35
0.36–0.41
0.42–0.48
0.49–0.55
0.56–0.61
0.62–0.82
0.83–1.55

Limited access highway Town boundaryTraffic-related air pollution and cognition

Environmental Health Perspectives • volume 119 | number 5 | May 2011 

### 685 global cognitive function, which combined the remaining seven cognitive test scores, a doubling in BC was significantly associated with a decrement of 0.054 SD in cogni

tive test score in our multivariable-adjusted model (95% CI

, –0.103 to –0.006; Table 2), an effect similar to a 1. 9- year differ

ence in age in our data. We found no evi

dence of heterogeneity of results across tests [ p -value = 0.25]. See Supplemental Material, Table s 1 and 2 (doi:10.1289/ehp.1002767)] for the full multivariable-adjusted models

. In our sensitivity analyses, we additionally adjusted for smoking and BMI, and our results were materially unchanged. We found no evidence of interactions between BC and diabetes, smoking, BMI or hypertension on MMSE scores ( p -values for all interactions > 0.1). Our exploration of potential interactions between BC and these factors on global cognitive function, in mod

els that combined the remaining seven test scores, suggested that the adverse effects of BC were concentrated in overweight and obese individuals ( p -value for interaction = 0.10) and in ever smokers ( p -value for inter

action = 0.07)

, but we found no evidence for effect modification by hypertension or diabe

tes ( p -values for interactions > 0.1). Among participants with measured tibia bone lead concentrations, the mean ± SD bone lead concentration was 19.2 ± 11.9 μ g lead/g bone mineral ; among those with imputed bone lead concentrations

, it was 16.1 ± 7.0 μ g lead/g bone mineral. In the sensitivity analysis that adjusted for estimates of cumulative leadexposure, we observed that the multivariableadjusted association between BC and low MMSE scores was almost identical (OR

= 1.3 per doubling in BC ; 95% CI

, 1.1–1.7). The association between BC and global cognitive function was somewhat attenuated after we adjusted for lead in our multivariable-adjusted model (–0.038 per doubling in BC ; 95% CI

, –0.089 to 0.012).



### Discussion The results of this study suggest an adverse effect of traffic-related air pollution on global cognitive function in older men. Confounding by lead cannot fully account for these findings. When we explored the potential for effect modification, our results suggest that the effect of traffic-related air pollution on cognition may be greater in smokers or overweight and obese individuals. Because these conditions are

pro inflammatory, this is biologically plausible but requires further confirmation. To our knowledge, this is only the sec

ond study to consider the association between air pollution and cognitive function in older adults. Ranft et al. ( 2009) considered the association between two markers of air pollu

tion, a measure of PM with an aerodynamic diameter ≤ 10 μ m (PM 10 ) and distance to a major road, and cognitive function in 399 women 68–79 years of age who had lived at the same address for 20 years. Residence within 50 m of a major road, but not PM 10 , was significantly associated with a decrement in the total score of the CERAD-Plus test battery, the Stroop test, and a test of olfac

tory function in multivariable-adjusted mod

els. In addition, residence within 50 m of a major road was adversely associated with performance on all sub tests of the CERAD battery, although few individual associations achieved statistical significance. Our findings are consistent with these, because BC, a traffic particle, is strongly associated with distance to major road and weakly associated with PM 10 . A handful of studies have evaluated the association between air pollution and cogni

tive function in younger populations, and, col

lectively, they also suggest an adverse effect. In a study of adults 20–59 years of age, Chen and Schwartz (2009) reported that estimates of exposure to ozone, but not PM 10 , were asso

ciated with inferior performance on two of three neurobehavioral tests in fully adjusted models. Calderón-Garcidueñas et al. ( 2008a) found the performance age on several sub

tests of the Wechsler Intellegence Scale for Children, Revised ( WISC-R) to be signifi

cantly behind chronological age in children residing in cities with high levels of air pollu

tion but not in those residing in cities with low levels. In a study that compared neurobehav

ioral test scores across students from two pri

mary schools in the same city in China, Wang

et al. (2009) found that students who attended the school with high levels of traffic-related air pollution were more likely to exhibit poor performance than were those who attended the school with low levels. Franco Suglia et al. ( 2008) found that higher residence-based estimates of average lifetime exposure to BC were associated with lower cognitive test scores in children 8–11 years of age . Similarly, in 4- to 5-year-old children from the INMA (Environment and Childhood) study, Freire

et al. (2010) observed that higher residencebased estimates of nitric dioxide were associ

ated with lower scores on all subscales of a standardized version of the McCarthy Scales of Children’s Abilities, although only one of these associations achieved statistical significance. Several biological mechanisms have been proposed to explain how traffic-related air pollution may have an adverse effect on CNS function. First, ultrafine particles, such as those found in diesel exhaust, are small enough to pass through the air

– blood barrier of the lung, enter the systemic circulation, and translocate to other body tissues, includ

ing the brain (Oberdörster et al. 2004; Peters

et al. 2006), and may also translocate directlyto the brain via the olfactory nerve (CalderónGarcidueñas et al. 2003; Elder et al. 2006). The presence of such particles in the brain is associated with neuroinflammation and oxida

tive stress (Calderón-Garcidueñas et al. 2003; Elder et al. 2006). Second, traffic-related PM may exert indirect effects on CNS function through effects on cardiovascular health. Exposure to PM is associated with a variety of cardiovascular end points (Brook 2007; Pope and Dockery 2006), including hypertension (Auchincloss et al. 2008; Brook 2007) and atherosclerosis (Künzli et al. 2005, 2010), as well as markers of increased cardiovascular risk, including progression of atherosclerotic plaques (Floyd et al. 2009; Künzli et al. 2010; Sun et al. 2005) and homocysteine (Baccarelli

et al. 2007; Park et al. 2008). Several of these factors are also associated with worse cognitive function (Komulainen et al. 2007; Qiu et al. 2005; Sander et al. 2010; Vidal et al. 2008), which likely reflects the link between cogni

tive impairment and vascular brain pathology. The present study has several strengths. The BC exposure model enabled us to report indi

vidual estimates of long-term exposure to traf

fic-related air pollution. In our study, we were also able to control for socio economic status (SES) using both personal and residence-based characteristics, which should limit residual con

founding by this factor. Furthermore, we were able to address the potential for confounding by past exposure to lead, another environmen

tal pollutant that may affect cognitive function in older adults, using a combination of meas

ured and imputed biomarkers for cumulative past lead exposure. Although correlated with traffic-related air pollution, exposure to lead cannot completely account for the observed associations. Finally, our results are based on a substantial number of observations, given that, on average, each of our 680 participants com

pleted 2.14 cognitive testing sessions.

**Table 2.** Adjusted associations for a doubling in BC concentration on the natural scale and cognitive test score(s). Effect per doubling in BC concentration (95% CI)

Analysis Model 1: age adjusted Model 2: age and education adjusted Model 3: multivariable adjusted a
Low MMSE score OR 1.4 (1.1 to 1.6) 1.3 (1.0 to 1.5) 1.3 (1.1 to 1.6) Global analysis estimate –0.073 (–0.122 to –0.023) –0.052 (–0.100 to –0.004) –0.054 (–0.103 to –0.006)

a Adjusted for age, education, first language, computer experience, physical activity, alcohol consumption, diabetes, dark fish consumption, percentage of residential census tract that is non white, percent age of residential census tract adults with a college degree, indicator for first cognitive assessment, and indicator for part-time resident

.Power et al.



### 686 volume 119 | number 5 | May 2011 • Environmental Health Perspectives Several potential sources of bias must be considered when interpreting our results. The use of exposure estimates based on residential address may misclassify personal exposure lev

els. However, the lack of significant occupa

tional or commuting exposure in this largelyretired cohort should mean that residencebased exposure estimates are an excellent measure of personal exposures over the past few years. Because 87% of our participants have lived at the same address for at least 5 years before their baseline cognitive assess

ment (mean ± SD duration

, 18 ± 12 years) and because people are likely to choose simi

lar neighborhoods when relocating, misclas

sification due to participant relocation is also expected to be minimal. In addition, occa

sional exposures encountered elsewhere are unlikely to be correlated with cognitive func

tion and so would result in non differential misclassification of exposure, which would be expected to attenuate our effect estimates (Gryparis et al. 2009). Similarly, non differ

ential misclassification of cognitive function is expected when assessing cognitive func

tion and would make it harder to detect a true effect, although our use of global analy

ses helps to reduce the impact of noise by using multiple measures to capture under

lying global cognitive function. We observed statistically significant associations between BC and cognitive function, when measured as the risk of a “low” MMSE score and as overall performance on our battery of cogni

tive tests, despite the presence of misclassi

fication, suggesting that the true association may be even stronger than what we observed. Although residual confounding cannot be excluded, we do not believe confounding to be a major source of bias in the present study given the availability of information on potential confounders and the use of sev

eral different, related variables to account for SES. Moreover, we do not believe confound

ing by regional pollutants, which may have an independent effect on cognition, to be a major source of bias. Correlation between BC and regional pollutants may be induced through similar spatial or temporal patterns. However, traffic-related air pollution exhib

its significant spatial variation not shared by more regional pollutants [e.g.

, ozone or par

ticulate matter with an aerodynamic diameter

< 2.5 μ m (PM 2.5 )]

, and temporal correlation is quite weak between our 1- year residencebased BC estimates (which have varying start dates depending on the timing of the baseline cognitive assessment) and the 1- year average of ozone concentrations at four central moni

tors in the Boston area ( r = –0.03) or 1- year average PM 2.5 concentrations at a central site monitor in Boston ( r = 0.16) calculated over the same time periods. Incomplete follow-up may induce bias in the present study but is unlikely to account for the observed associa

tions. In our study, and generally in studies of older adults, participants who are lost to follow-up exhibit lower cognitive test scores than do those who complete follow-up (Euser

et al. 2008). Because air pollution has been related to cardiovascular morbidity and mor

tality (Brook 2007; Pope and Dockery 2006) and because we observed lower BC estimates in participants with three or more follow-up visits, we expect that a greater loss of those with both lower cognitive test scores and higher BC estimates to lead to an underesti

mate of the association. Thus, the true asso

ciation may be stronger than that observed. One additional limitation lies in our inability to attribute our findings to a particu

lar traffic-related exposure. We have estimated exposure to BC particles for each participant. However, traffic-related air pollution is a com

plex mixture of gases and particles, and BC is correlated with other components of the mix

ture. Although existing evidence suggests that PM , specifically ultrafine PM , is a likely agentfor adverse effects to the CNS (CalderónGarcidueñas et al. 2003; Elder et al. 2006; Oberdörster et al. 2004; Peters et al. 2006), other components may be important. In addition, measures of traffic-related air pol

lution are often correlated with other envi

ronmental exposures. Although we were able to address the potential for lead to account for the observed associations, other exposures must be considered, including noise. Elevated noise levels have been linked to metrics of cognitive function in children in a handful of studies (Clark et al. 2006; Stansfeld et al. 2005), and chronic occupational exposure to noise is associated with neurophysiologi

cal measures related to attention in adults (Gomes et al. 1999). Given the high correla

tion between measures of traffic-related air pollution and noise (Allen et al. 2009; Davies

et al. 2009), it is possible that the associa

tions observed for one exposure are attribut

able to the other. Further research to evaluate the rela tive contribution of particular trafficrelated pollutants or other exposures to the observed association is warranted.



### Conclusions Our findings suggest that traffic-related air pollution may have an adverse effect on cog

nition in older men. This is the first study to find an association between traffic-related air pollution and cognition in older men, and only the second to consider the relationship in older adults. Given the ubiquitous nature of the exposure, if traffic-related air pollution is causally related to cognitive impairment in older adults, implementation of interventions to reduce exposure, including establishment of more stringent emissions standards, would be expected to have substantial benefits. **R efe**  **r ences** 

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